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ECOLOGICAL RISK ASSESSMENT OF TRACE METALS IN SEDIMENTS ALONG THE EGYPTIAN MEDITERRANEAN COAST A Thesis Submitted to Institute of Graduate Studies and Research Alexandria University In Partial Fulfillment of the Requirements for the Degree of Doctor of Philosophy In Environmental Studies By Naglaa Farag Elsayed Soliman B.Sc. Chemistry & Oceanography, 1997 Faculty of Science M.Sc. in Environmental Studies, 2008 Alexandria University Department of Environmental Studies Institute of Graduate Studies and Research Alexandria University 2012 ECOLOGICAL RISK ASSESSMENT OF TRACE METALS IN SEDIMENTS ALONG THE EGYPTIAN MEDITERRANEAN COAST Presented by Naglaa Farag Elsayed Soliman Examiners Committee: Approved Prof. Dr. Mamdouh Saad Masoud Professor of Chemistry Department of Chemistry Faculty of Science ………………….. Alexandria University Prof. Dr. Mohamed Mohamed Attia Shreadah Professor of Marine Chemistry President of the National Institute of Oceanography and Fisheries Alexandria ………………….. Prof. Dr. Samir Mahmoud Nasr Professor of Marine Geochemistry Department of Environmental Studies Institute of Graduate Studies and Research Alexandria University Date / / 2012 ………………….. Advisors’ Committee: Prof. Dr. Samir Mahmoud Nasr ………… Professor of Marine Geochemistry, Department of Environmental Studies, Institute of Graduate Studies and Research, Alexandria University Dr. Mohammed Abd El-Hamid Khairy Lecturer, Department of Environmental Science, Faculty of Science, Alexandria University ……...… ACKNOWLEDGEMENT First of all, I thank God for helping me to accomplish this research and for providing me with such very encouraging and supporting supervisors. I wish to express my deepest appreciation and sincere gratitude to Professor Dr. Samir Mahmoud Nasr, Professor of Marine Geochemistry, Department of Environmental Studies, Institute of Graduate Studies and Research, University of Alexandria for the suggestion of the research subject and the ideas, his keen interest, guidance and valuable discussions and his cooperation and continuous encouragement he has given to me to accomplish the work. It is honor working under his supervision. I would like to express my sincere thanks to Dr. Mohammed Abdel Hamid Khairy, Lecturer, Department of Environmental Science, Faculty of Science, University of Alexandria, for his great support, guidance, supervision and advice throughout the study and his encouragement during the preparation of the manuscript. No words can express my sincere gratitude to Prof. Dr. Mohammed Abdel Aziz Okbah, Professor of Marine Chemistry, National Institute of Oceanography and Fisheries, for his detailed and constructive comments, and for his important support throughout this work and for his detailed review, constructive criticism and excellent advice during the preparation of this work. I would like also to express my deepest thanks to Mr. Mohammed Abdel Khaleq for his help, support and encouragement at the beginning of my practical work. I would like to thank him very much for his assistance on the field and in the laboratory during the project period. Last of all, I am greatly indebted to my family. Thanks to my parents, for giving me life in the first place, for educating me for unconditional support and encouragement to pursue my interests. Table of Contents Page ACKNOWLEDGMENT ....................................................................... i TABLE OF CONTENT ........................................................................ ii LIST OF TABLES ................................................................................. iii LIST OF FIGURES ............................................................................... iv LIST OF ABBREVIATIONS ............................................................... v I- INTRODUCTION ............................................................................. 1 II- REVIEW OF LITERATURE ......................................................... 4 2.1. Contaminants in the environment ............................................................ 4 2.2. Trace metals ................................................................................................ 4 2.2.1. Sources, uses and toxicity of trace metals .................................................. 6 2.2.2. Pollution of the aquatic environment with trace metals ........................... 18 2.2.2.1. Trace metals in the water column ........................................................................... 18 2.2.2.2. Metals in seawater .................................................................................................. 20 2.2.2.3. Metals in marine biota ............................................................................................ 21 2.2.2.4. Metals in marine sediments .................................................................................... 22 2.2.3. The importance of studying sediments ....................................................... 23 2.2.4. Effects of trace metals contamination in sediments .................................. 26 2.2.4.1. Metals polluted sediments ...................................................................................... 26 2.2.4.2. Ecology ................................................................................................................... 26 2.2.4.3. Human health.......................................................................................................... 27 2.2.5. Factors affecting trace metal distribution, concentration and fate in sediments ................................................................................................................. 27 2.2.5.1. Trace metals input into sediment ............................................................................ 28 2.2.5.2. The influence of grain size ..................................................................................... 28 2.2.5.3. Sediment composition ............................................................................................ 29 2.2.5.4. The influence of pH values..................................................................................... 30 2.2.5.5. Influence of organic matter .................................................................................... 30 2.2.5.6. The influence of oxidation reduction potential ...................................................... 31 2.2.5.7. Adsorption/desorption reactions ............................................................................. 32 2.2.5.8 Physical transport .................................................................................................... 33 2.2.5.9. Bioturbation ............................................................................................................ 34 2.2.5.10. The influence of other species .............................................................................. 34 2.2.6. Analysis of trace metals in sediments ......................................................... 35 2.2.6.1 Acid volatile sulphide ................................................................................. 36 2.2.6.2. Sequential extraction procedure .............................................................. 37 2.3. Environmental problems and previous studies on the coastal area along the Mediterranean Sea ..................................................................................... 41 2.4. Ecological risk assessment ......................................................................... 53 2.4.1. Ecological risk terms .................................................................................... 53 2.4.2. Phases of Ecological risk assessment .......................................................... 53 2.4.3. Ecological risk assessment in a management context ............................... 54 2.4.4. Contributions of Ecological Risk Assessment to Environmental Decision making .................................................................................................................... 56 2.4.5. Factors Affecting the Value of Ecological Risk Assessment for Environmental decision making ............................................................................ 56 III- SOCIOECONOMIC AND ENVIRONMENTAL ASPECTS ... 57 3.1. Description of the Egyptian Mediterranean environment coastal environment ....................................................................................................... 57 3.1.1. History and culture....................................................................................... 57 3.1.2. Climate........................................................................................................... 57 3.1.3. Topography ................................................................................................... 58 3.1.4. Subsidence and sea level rise ....................................................................... 59 3.1.5. Current .......................................................................................................... 59 3.1.6. Wind............................................................................................................... 59 3.1.7. Waves ............................................................................................................. 61 3.1.8. Tides and storm surges ................................................................................ 61 3.1.9. Hydrology ...................................................................................................... 61 3.1.10. Biological diversity ..................................................................................... 62 3.1.11. Ecosystem features ..................................................................................... 62 3.12. Water quality ................................................................................................ 62 3.13. Sediment characteristics ............................................................................... 63 3.2. Economic activities of the Egyptian Mediterranean coastal area ......... 64 3.2.1 Population ...................................................................................................... 65 3.2.2. Main activities sectors ............................................................................... .. 66 3.2.3. Land use ..................................................................................................... .. 69 3.2.4. The economic importance of the coastal lakes ........................................ ..70 3.2.5. The economic importance of the Egyptian Mediterranean ports ......... ..71 3.3. Environmental aspects ............................................................................. ..73 IV- MATERIALS & METHODS .................................................................................................................. 7 5 4.1. Study area ................................................................................................. ..75 4.2. Sample collection, preservation and storage ......................................... ..75 4.3. Sample pre-treatment .............................................................................. ..75 4.4. Physicochemical characterization of sediment ..................................... ..78 4.4.1. Determination of water content 9%WC) ................................................ ..78 4.4.2. Determination of pH.................................................................................. ..78 4.4.3. Determination of grain size analysis ........................................................ ..78 4.4.4. Determination of total carbonate ............................................................. ..78 4.4.5. Determination of total organic carbon (TOC) ........................................ ..79 4.5. Determination of total metals ................................................................. ..79 4.5.1. Sample preparation ................................................................................... ..79 4.5.2. Measuring system ...................................................................................... ..79 4.5.3 Analysis of certified reference materials .................................................. ..80 4.6. Determination of leachable metals ......................................................... ..80 4.7. Sequential extraction procedure for trace metals ............................... ..81 4.8. SEM/AVS analysis procedure ................................................................. ..83 4.8.1. Reagents...................................................................................................... ..83 4.8.2. Generation of H2S ...................................................................................... ..83 4.8.3. Procedure ................................................................................................... ..83 4.8.4. Analysis of sulfide ...................................................................................... ..84 4.8.5. Calculation of AVS .................................................................................... ..84 4.8.6. Determination of simultaneously extractable metals (SEM)................. ..84 V- RESULTS ....................................................................................... ..86 5.1. Physico-chemical parameters ................................................................ ..86 5.1.1. Seawater temperature ..................................................................................86 5.2.1. pH value .........................................................................................................86 5.3.1. Salinity ...........................................................................................................86 5.1.4. Dissolved oxygen ...........................................................................................86 5.2. Geochemical Analysis ............................................................................. ..88 5.2.1. pH value .........................................................................................................88 5.2.2. Calcium carbonate (CaCO3)........................................................................88 5.2.3. Total organic matter (TOM%) ...................................................................88 5.2.4. Water content (%WC) .................................................................................88 5.2.5. Grain size .......................................................................................................88 5.3. Trace metals distribution ....................................................................... ...91 5.3.1. Total metals ................................................................................................... 91 5.3.1.1. Total Iron (TFe) ...................................................................................................... 91 5.3.1.2. Total Manganese (TMn) ..................................................................................... …91 5.3.1.3. Total Zinc (TZn) ..................................................................................................... 92 5.3.1.4. Total Copper (Cu)................................................................................................... 92 5.3.1.5. Total Nickel (Ni) .................................................................................................... 93 5.3.1.6. Total Chromium (Cr).............................................................................................. 93 5.3.1.7. Total Cobalt (Co) .................................................................................................... 93 5.3.1.8. Total Lead (Pb) ....................................................................................................... 94 5.3.1.9. Total Cadmium (Cd)............................................................................................... 94 5.3.2. Leachable Metals ......................................................................................100 5.3.2.1. Leachable Iron (Fe) ............................................................................................ 100 5.3.2.2 Leachable Mnganese (Mn) .................................................................................. 100 5.2.2.3. Leachable Zinc (Zn) ........................................................................................... 100 5.2.2.4. Leachable Cupper (Cu)....................................................................................... 101 5.2.2.5 Leachable Nickel (Ni) ......................................................................................... 101 5.2.2.6 Leachable Cr (Cr) ................................................................................................ 101 5.2.2.7 Leachable Co (Co) ............................................................................................... 101 5.2.2.8 Leachable Lead (Pb) ............................................................................................ 102 5.2.2.9. Leachable Cadmium (Cd)................................................................................... 102 5.3.3. Partitioning of Metals ..............................................................................107 5.3.3.1. Fractionation of Iron (Fe) ................................................................................... 107 5.3.3.2. Fractionation of Manganese (Mn) ...................................................................... 108 5.3.3.3. Fractionation of Zinc (Zn) .................................................................................. 108 5.3.3.4. Fractionation of Nickel (Ni) ............................................................................... 109 5.3.3.5. Fractionation of Chromium (Cr) ........................................................................ 110 5.3.3.6. Fractionation of Lead (Pb).................................................................................. 110 5.3.4. Acid volatile sulfide (AVS) and simultaneously extracted metals (SEM)........................................................................................................... 126 VI- DISCUSSION ............................................................................... 130 6.1. Geochemical Analysis ............................................................................. 130 6.1.1. Grain size distribution ..............................................................................130 6.1.2. Total carbonate ..........................................................................................131 6.1.3. Organic matter...........................................................................................132 6.2. Trace metal distribution ......................................................................... 133 6.2.1. Total metals ................................................................................................133 6.2.1.1. Assessment of sediment quality ......................................................................... 144 6.2.1.2. Estimation of pollution impact ........................................................................... 156 6.2.1.2.1. Enrichment factor .................................................................................................. 156 6.2.1.2.2. Geoaccumulation Index (Igeo) ................................................................................ 159 6.2.1.2.3. Contamination factor (Cf) and Degree of contamination (Cd) .............................. 162 6.2.1.2.4. Modified degree of contamination (mCd)............................................................. 162 6.2.1.2.5. Pollution Load Index ............................................................................................. 163 6.2.2. Leachable metals .......................................................................................166 6.2.3. Fractionation of trace metals ...................................................................176 6.2.3.1. Risk assessment code (RAC).............................................................................. 188 6.2.4. Toxicity assessment of trace metals in sediments based on AVS, SEM models ...................................................................................................................190 6.3. Ecological risk assessment ...................................................................... 196 6.3.1. Problem formation ....................................................................................196 6.3.2. Analysis setup.............................................................................................197 6.3.2.1. Exposure characterization .................................................................................. 197 6.3.2.2. Effect characterization ........................................................................................ 197 6.3.3. Risk characterization ................................................................................200 6.3.4. Area of special concern based on the conducted SLERA ......................204 6.3.5. The potential Ecological Risk Index method ..........................................206 6.4. Multivariate Statistical analysis ............................................................ 209 6.4.1. Application of principal component analysis (PCA) ..............................209 6.4.2. Cluster analysis ..........................................................................................210 6.4.3. Correlation matrix.....................................................................................216 VII- English Summary ....................................................................... 225 References ........................................................................................... 235 LIST OF TABELS Table 1. 2. 3. 4. 5. 6. 7. 8. 9. 10. 11. 12. 13. 14. 15. 16. 17. Page Description of the study area and sources of marine pollution Concentrations of metals (µgg-1) obtained from the analysis of the Standard Reference Materials (IAEA-405) and their recovery Physical parameters of the surface seawater of the study area. Calcium carbonate (CaCO3%), total organic matter (OM%), Water Content (WC%), pH, grain size and type of sediments along the Egyptian Mediterranean Coastal area. Total trace metals concentration (µgg-1 dry weight) in surfacial sediments along the Egyptian Mediterranean Coastal area. Leachable trace metals concentration (µgg-1 dry weight) of surfacial sediments along the Egyptian Mediterranean coastal area. Fractionation of Fe concentration (µgg-1) and its relative percentage from the total in sediments of the Egyptian Mediterranean coastal area. Fractionation of Mn concentration (µgg-1) and its relative percentage from the total in sediments of the Egyptian Mediterranean coastal area. Fractionation of Zn concentration (µgg-1) and its relative percentage from the total in sediments of the Egyptian Mediterranean coastal area. Fractionation of Ni concentration (µgg-1) and its relative percentage from the total in sediments of the Egyptian Mediterranean coastal area. Fractionation of Cr concentration (µgg-1) and its relative percentage from the total in sediments of the Egyptian Mediterranean coastal area. Fractionation of Pb concentration (µgg-1) and its relative percentage from the total in sediments of the Egyptian Mediterranean coastal area. Concentration of AVS and SEM (µmole/g, dry weight) in surfacial sediments of the Egyptian Mediterranean coastal area from El-Salloum to Rafah Average concentrations (µgg-1) of total trace metals in sediments along the Egyptian Mediterranean coastal area compared with nocontaminated sediments Concentrations of trace metals (µgg-1) determined in sediments of the present study compared to other parts along the Mediterranean coast. Comparison of the surfacial sediments from the Egyptian Mediterranean coast with Sediment quality guidelines Estimated mean ERMq and PELq of surface sediments along the Egyptian Mediterranean coastal area 77 80 87 89 96 103 112 113 114 115 116 117 127 142 143 148 154 Table 18. 19. 20. 21. 22. 23. 24. 25. 26. 27. 28. 29. 30. 31. 32. 33. 34. 35. 36. 37. 38. 39. 40. Page The metal threshold values of some different criteria used to distinguish marine sediment quality (µgg1-) Classification of sediments according to the background and classification system from the Hong Kong environmental Protection Department (EPD, 1992) Enrichment factor (EF) in the surface sediments of the Egyptian Mediterranean coastal area Geoaccumulation Index Igeo Igeo values of trace metals in the surface marine sediments along the Egyptian Mediterranean coastal area The classification and description of the modified degree of contamination (mCd) Modified degree of contamination (mCd) and contamination factors (Cf) for the surfacial sediments along the Egyptian Mediterranean coastal area The relative percentage of leachable Metals from total metals in the sediments of the Egyptian Mediterranean coastal area Classification of Risk assessment code (RAC) Risk assessment code (RAC) (%) and risk rank for trace metals in the sediments of the Egyptian Mediterranean coastal area The concentrations of AVS, SEM (µmole/g), and the ratio of SEM and AVS in surface sediments of the Egyptian Mediterranean coastal area. The concentrations of AVS, SEM (µmole/g), and the SEM-AVS in surface sediments of the Egyptian Mediterranean coastal area. The concentrations of AVS, SEM (µmole/g), and the SEMAVS/fOC in surface sediments of the Egyptian Mediterranean coastal area. Table 31: Assessment and measurement endpoints for the SERA of the Egyptian Mediterranean coast. Summary of the effect concentration levels from different SQGs applied in the SERA of the Egyptian Mediterranean coast Summary of the information obtained from the risk characterization process for pollutants in sediments of the Egyptian Mediterranean Coast. The calculated PEC HQ of the Egyptian Mediterranean coastal sediments Pollution index, integrated pollution index and pollution grade in sediments along the Egyptian Mediterranean coastal area Relation between RI and pollution levels Evaluation on potential risk of trace metal pollution in sediments along the Egyptian Mediterranean costal area Factor loadings on elements in surfacial sediments samples along the Egyptian Mediterranean coastal area (n=20) Factor loadings on leachable metals in surfacial sediments samples along the Egyptian Mediterranean coastal area (n=20) Factor loadings of variable (5 metals) using PCA technique of the data set in the Exchangeable fraction of the surfacial sediments along the Egyptian Mediterranean coastal area. 155 155 158 159 160 163 164 172 188 189 194 195 195 197 201 205 206 207 208 208 212 212 213 Table 41. 42. 43. 44. 45. 46. 47. 48. 49. 50. 51. 52. Page Factor loadings of variable (5 metals) using PCA technique of the data set in the Carbonate fraction of the surfacial sediments along the Egyptian Mediterranean coastal area. Factor loadings of variable (5 metals) using PCA technique of the data set in the Oxides fraction of the surfacial sediments along the Egyptian Mediterranean coastal area. Factor loadings of variable (5 metals) using PCA technique of the data set in the Organic fraction of the surfacial sediments along the Egyptian Mediterranean coastal area. Factor loadings of variable (5 metals) using PCA technique of the data set in the Residual fraction of the surfacial sediments along the Egyptian Mediterranean coastal area. Correlation matrix between heavy metals, CaCO3 and OM in sediments (n=20) along the Egyptian Mediterranean coast from Salloum to Rafah Correlation matrix between leachable trace metals , CaCO3 and OM in sediments from Salloum to Rafah Correlation coefficient matrix between chemical characteristics and different species of Iron. Correlation coefficient matrix between chemical characteristics and different species of Manganese. Correlation coefficient matrix between chemical characteristics and different species of Zinc. Correlation coefficient matrix between chemical characteristics and different species of Nickel. Correlation coefficient matrix between chemical characteristics and different species of Chromium. Correlation coefficient matrix between chemical characteristics and different species of Lead. -12- 213 213 214 214 217 222 223 223 223 224 224 224 LIST OF FIGURES Figure 1. 2. 3. 4. 5. 6. 7. 8. 9. 10. 11. 12. 13. 14. 15. 16. 17. 18. 19. Page Figure (1): Map of Egyptian Mediterranean coast representing the sampling sites of the study area Flow chart of the sequential extration scheme used in this study Distribution of CaCO3 % in surface sediments along the Egyptian Mediterranean Coast. Distribution of TOM% in surface sediments along the Egyptian Mediterranean Coast. Distribution of % Water Content in surface sediments along the Egyptian Mediterranean Coast. Distribution of Fe, Mn and Zn in surface sediments collected from the Egyptian Mediterranean coastal area Distribution of Cu, Ni, and Cr in surface sediments collected from the Egyptian Mediterranean coastal area Distribution of Co, Pb and Cd in surface sediments collected from the Egyptian Mediterranean coastal area Concentration of LFe, LMn and LZn in surfacial sediments along the Egyptian Mediterranean coastal area. Concentration of LCu, LNi, LCr in surfacial sediments along the Egyptian Mediterranean coastal area. Concentration of LCo, LPb, LCd in surfacial sediments along the Egyptian Mediterranean coastal area. Percent contribution of Fe, Mn and Zn fractions from the total concentration in surfacial sediments of the Egyptian Mediterranean coastal area Percent contribution of Ni, Cr, and Pb fractions from the total concentration in surfacial sediments of the Egyptian Mediterranean coastal area The relative percentage of Fe fractions from the total concentration in the three regions, Egyptian Mediterranean coastal area The relative percentage of Mn fractions from the total concentration in the three regions, Egyptian Mediterranean Sea sediments The relative percentage of Zn fractions from the total concentration in the three regions, Egyptian Mediterranean Sea sediments The relative percentage of Ni fractions from the total concentration in the three regions, Egyptian Mediterranean Sea sediments The relative percentage of Cr fractions from the total concentration in the three regions, Egyptian Mediterranean Sea sediments The relative percentage of Pb Fractions from the total concentration in the three regions, Egyptian Mediterranean Sea sediments -13- 76 82 90 90 90 97 98 99 104 105 106 118 119 120 121 122 123 124 125 Figure 20. 21. 22. 23. 24. 25. 26. 27. 28. 29. 30. 31. 32. 33. 34. 35. 36. 37. 38. 39. 40. 41. Page The relative percentage of simultaneously extracted metals in the three regions, Egyptian Mediterranean Sea sediments The average of SEM in the three regions, Egyptian Mediterranean Sea sediments The average of AVS in the three regions, Egyptian Mediterranean Sea sediments The average of total Fe, Mn and Cr levels in µgg-1 dry weight at the studied regions The average of total Ni, Zn and Pb levels in µgg-1 dry weight at the studied regions The average of total Cu, Co and Cd levels in µgg-1 dry weight at the studied regions Concentration of Fe, Mn and Cr, in sediments along the Egyptian Mediterranean coastal area comparable to US SQG. Concentration of Ni, Pb and Cu, in sediments along the Egyptian Mediterranean coastal area comparable to US SQG. Concentration of Cr, Ni and Zn, in sediments along the Egyptian Mediterranean coastal area comparable to US NOAA's. Concentration of Pb and Cu in sediments along the Egyptian Mediterranean coastal area comparable to US NOAA's. Estimated mean ERMq of surface sediments along the Egyptian Mediterranean coast Estimated mean PELq of surface sediments along the Egyptian Mediterranean coast Mean Enrichment factor for surface sediments along the Egyptian Mediterranean coastal area Igeo values distribution of trace metals in the surface marine sediments along the Egyptian Mediterranean coastal area Modified degree of contamination (mCd) for sediments along the Egyptian Mediterranean coast Pollution load index distribution at different stations along the Egyptian Mediterranean coastal sediments. Distribution of total trace metals concentrations (Fe, Mn and Pb) and leachable fractions in sediments along the Egyptian Mediterranean coast Distribution of total trace metals concentrations (Zn, Ni and Cr) and leachable fractions in sediments along the Egyptian Mediterranean coast Distribution of total trace metals concentrations (Co, Cu and Cd) and leachable fractions in sediments along the Egyptian Mediterranean coast The average concentration of Fe speciation µgg-1 in surfacial sediments from the Egyptain Mediterranean coast The relative percentage of Fe species µgg-1 in surfacial sediments from the Egyptain Mediterranean coast The average concentration of Mn speciation µgg-1 in surfacial sediments from the Egyptain Mediterranean coast -14- 128 129 129 139 140 141 149 150 151 152 153 153 158 161 165 165 173 174 175 182 182 183 Figure 42. 43. 44. 45. 46. 47. 48. 49. 50. 51. 52. 53. 54. 55. 56. 57. 58. 59. 60. 61. 62. Page The relative percentage of Mn species µgg-1 in surfacial sediments from the Egyptain Mediterranean coast The average concentration of Zn speciation µgg-1 in surfacial sediments from the Egyptian Mediterranean coast The relative percentage of Zn species in surfacial sediments from the Egyptian Mediterranean coast The average concentration of Ni speciation µgg-1 in surfacial sediments from the Egyptian Mediterranean coast The relative percentage of Ni species in surfacial sediments from the Egyptian Mediterranean coast The average concentration of Cr speciation µgg-1 in surfacial sediments from the Egyptian Mediterranean coast The relative percentage of Cr species in surfacial sediments from the Egyptian Mediterranean coast The average concentration of Pb speciation µgg-1 in surfacial sediments from the Egyptian Mediterranean coast The relative percentage of Pb species in surfacial sediments from the Egyptian Mediterranean coast The relationship between OC and AVS 183 Conceptual site model for the SLERA in the Egyptian Mediterranean Coast SLERA approach applied in the Egyptian Mediterranean coast TEC HQ and PEC HQ for trace metals in the Egyptian Mediterranean coastal sediments Cluster analysis of the selected trace metals in the surfacial sediments along the Egyptian Mediterranean coastal area Dendogram showing station groups formed by group averaging cluster analysis of elemental concentrations Relationship between Fe, Mn, Co, Cr and Ni Relationship between Zn and Cu Relationship between Zn and Pb Relationship between Mn and Cr Relationship between Co and Cr Relationship between Ni and Cr, Mn and Co 199 -15- 184 184 185 185 186 186 187 187 192 202 203 215 215 218 219 219 219 219 220 Chapter I Introduction Marine sediments are not only the final depositories of pollutants, such as trace metals, but have also to be considered as potential pollutant sources (Burges and Scott, 1992)(1). Through early diagenesis and benthic organism activity, but also because of natural phenomena (mechanical re-suspension), trace metals are re-mobilized from sediments and are re-distributed in the marine environment. The importance of sediments as a trace metals source is more pronounced in the coastal zone. This is particularly relevant in a land-locked marginal sea with a highly populated coastal zone, like the Mediterranean Sea. In the Mediterranean Sea, anthropogenic trace elements are introduced into the marine environment through atmospheric deposition, fluvial plumes and direct discharges from coastal urban and industrial development. Settling particles scavenge the greater part of trace metals introduced in the water column and transport them into the coastal as well as deep-sea sediments. After deposition, sediments are not inert depositories of trace metals. On the contrary, through benthic fluxes at the sediment/water interface, they may represent a very important trace element secondary source to the marine Environment (Angelidis, 2005)(2). Trace metals occur naturally as they are components of the lithosphere and are released into the environment through volcanism and weathering of rocks (Fergusson, 1990)(3). Heavy metals and trace elements are by-products of many industrial processes, contributing varying amounts of different metals and trace metals and as such are discharged as waste into the marine environment (Robson and Neal, 1997)(4). They enter the marine environment through atmospheric and land based effluent sources (Gonzalez- Macias et al., 2006)(5). The metals considered toxic and which are of concern have been restricted largely, but not exclusively, to the ten which appear to be most poisonous to marine life. These include, in order of decreasing toxicity: mercury, cadmium, silver, nickel, selenium, lead, copper, chromium, arsenic and zinc (Davies, 1978)(6). Sediments can be valuable indicators for monitoring contaminants in aquatic environments (Atgin et al., 2000)(7). The sediments have been found polluted with various types of hazardous and toxic substances, including trace metals which accumulate via disposal of liquid effluents, terrestrial runoff, and leachates carrying chemicals originating from numerous urban, industrial, and agricultural activities, as well as atmospheric deposition (Mucha et al., 2003)(8). The amount of heavy metals in sediments also affects their characteristics, particularly, the type and quantities of organic matter, grain size, cation exchange capacity and mineral constituents (Tam and Wong, 1995)(9). Most trace metals are bound in the finegrained fraction (<63μm) mostly because of its high surface area to grain size ratio and humus substance content (Moore et al., 1989)(10) where they have a potentially greater biological availability than those in the larger (2 mm–63μm) sediment fraction (Everaat and Fischer, 1992)(11). Al-Abdali et al. (1996)(12) found that positive correlations exists between increasing metal concentration and decreasing grain size, suggesting that adsorption onto mud is the primary mechanism of metal accumulation in marine sediments. -16- Over the last decade, much concern has been focused on the measurement of total concentration in sediment. However, it cannot provide sufficient and proper information on mobility, bioavailability and toxicity of trace metals (Wei et al., 2007)(13). Pollution by metals is a serious problem because of their toxicity and ability to accumulate in biota with a negative impact on the environment and human health. It is now widely accepted that the role of aquatic sediments as a sink or as a source of pollutants cannot fully be assessed by measuring total metal concentrations. In addition, the determination of total elements does not give an accurate estimate of the likely environmental impact. Instead, it is desirable to have information on the potential availability of metals (whether toxic or essential) to biota under various environmental conditions. Since the mobility of trace metals and their bioavailability and related ecotoxicity to plants depend critically on the chemical form in which a metal is present in the sediment, considerable interest exists in element speciation (Davidson et al. 2004)(14). Sequential extraction schemes provide information on evaluation of metal bioavailability and identification of binding sites of metals for assessing metal accumulation, pollution and transport mechanisms. The most widely used sequential extraction procedures was proposed by Tessier et al. (1979)(15) and the Community Bureau of Reference (BCR)(Ure et al., 1993; Rauret et al., 1999)(16, 17). To overcome the problem of re-adsorption and redistribution among the trace elements during the extraction procedure, some modified BCR schemes have also been proposed to eliminate this problem, which have been applied to soil, sewage sludge and sediment (Rauret et al.,1999; Rauret, 1998; Quevauviller, 1998, Filgueiras et al., 2002)(17-20). In these application metal partitioning in sediments was divided into acid soluble (metal precipitated or co-precipitated with carbonate), reducible (hydrous oxides of Mn and Fe), oxidizable (complexation with organic or bound to sulfide) and silicate residuals (Davidson et al., 2004)(21). Sulfide, which was among the oxdiziable phase during sequential extraction, was chosen for controlling factor on partitioning of toxic metals between aqueous and solid phases (Di Toro et al., 1990 ; Ankley et al., 1996)(22, 23). However, sulfide was not distinguished from organic in sequential extraction, which obscures the true speciation of metals in reduced sediments (Wei et al., 2007)(13). SEM (simultaneously extracted metals) /AVS (acid volatile sulfide) was endorsed as the best technology for assessing the bioavailability of five metals (Pb, Zn, Cu, Cd, and Ni). Different from BCR, it laid emphasis on toxicity and bioavailability of metals through the comparison of sulfide and SEM. However, it has been recognized that this measurement was applicable only to reduced sediments with measurable AVS and other tests of metal toxicity were needed for oxidized sediments. Although SEM were mainly controlled by sulfide in anoxic sediments, other minerals such as Fe-Mn oxide, carbonate and silicate also affect speciation of the metals as well (O’ Day et al., 2000)(24). The effectiveness of sequential extraction with AVS analysis was evaluated and it was found that sequential extraction significantly underestimated the amount of Zn associated with sulfide phases (Peltier et al., 2005)(25). Obviously, BCR or SEM/AVS measurement alone cannot comprehensively assess the toxicity and bioavailability of trace metals in sediments (Fang et al., 2005)(26). BCR results cannot specify the effect of sulfide on metal toxicity and bioavailability although it provides enough information on metal speciation. However SEM/AVS method neglects other metal speciations and only targets reduced sediment. Comparison of sequential extraction and SEM/AVS make up for the drawbacks that SEM/AVS only applied in anoxic sediments and overestimate metal bioavailability if nonsulfide was also extracted other than sulfide phases. Therefore, it will contribute to -17- quantifying the possible chemical partitioning patterns in sediments, thus have a deep insight in interpreting the speciation of trace metals (Wei et al., 2007)(13). The Problem During the last decades, there has been an extensive increase in the level of urbanization and industrialization along the Egyptian coastal area. At the same time, little data are available for the concentrations of trace metals along the Egyptian Mediterranean Coast. Studies on the environmental state of the Egyptian Mediterranean Coast have concentrated in the past mostly on simple chemical and bulk analysis of sediments. Most of the studies investigated metals in the total form and no comprehensive study was performed to investigate the most important metal bearing fractions in sediments and their mobility, bioavailability and thereby their toxicity. In addition, no data are available for the AVS/SEM as an important tool for evaluating metal toxicity in sediments. Aim of the study Industrial and human activities have increased dramatically in the last 20 years. Consequently, updated information is needed as basis for decision makers to establish effective management plans. Thus, the purpose of this study was set to: 1. Evaluate the levels and the spatial distribution of trace metals in the surfacial sediments of the Egyptian Mediterranean Coast. 2. Investigate the possibility of assessing the sediment toxicity based on analysis of simultaneously extracted metals (SEM) and acid volatile sulfides (AVS). 3. Evaluate metals mobility, bioavailability and toxicity by applying the sequential extraction procedure on the sediment samples. 4. Comparison between the above mentioned techniques to determine the best available methodology for assessing the sediment toxicity of the Egyptian Mediterranean Coast and to try to develop site specific sediment quality guidelines. 5. Formulate a detailed level ecological risk assessment on sediments to evaluate the possibility of occurrence of adverse ecological effects to benthic species based on the site specific characteristics. -18- Chapter II Literature Review 2.1. Contaminants in the environment Human activities have introduced synthetic substances into the environment, and have increased the concentrations of many naturally occurring substances. When the concentrations of these substances rise above the background levels, they are regarded as contaminates. The term anthropogenic is used to describe contaminants derived from man activities. Contaminants are termed pollutants when concentrations are high enough to cause toxic effects in exposed organisms. Organisms are not necessarily impacted negatively by the presence of contaminants but as concentrations increase, the likelihood of organism experiencing negative effects from exposure increase (Campbell et al., 2006)(27). Growing social concern about environmental quality can be observed in recent years, both on a global and local scale. Emission of harmful substances has negative effects on the natural environment, human health and agricultural production efficiency. When the consequences of environmental pollution become visible, it is often too late to prevent them and chronic toxic effects, impossible to notice at the initial stage of the process, may manifest after many years. Toxic chemical substances introduced into the environment may be transported by the air, water and living organisms and may become a part of the natural biogeochemical cycle and accumulate in the food chain (Adu, 2010)(28). Due to constant technological progress the natural environment undergoes numerous changes, deteriorating its quality, which often results in negative interactions between particular ecosystem components (Duffus, 2002)(29). Various contaminants released into the sea may significantly affect marine ecology, and in extreme cases, may lead to the destruction of whole ecosystems. The contaminants of major concern are sewage, nutrients, metallic compounds, substances disrupting endocrine functions, persistent organic pollutants and petroleum hydrocarbons (GESAMP, 2001)(30). Many contaminants such as trace metals (also referred as heavy metals), though occur at extremely low concentrations in seawater, are accumulated by marine organisms and concentrations in their body tissue can be hundreds of times greater than the levels in seawater (Riley and Chester, 1971)(31). The study of metals in the marine environment has received considerable attention because of their biological significance as well as the possibility of their transfer to man through the food chains in quantities that can be harmful. The available information indicates that though the open oceans suffer from some contamination and ecological damage, they are still in a relatively healthy state as compared to some coastal areas. It is the waters nearest to the shore, particularly in estuaries and in semi-enclosed seas and bays bordering highly industrialized and urbanized zones that have suffered ecological degradation over the past few decades (GESAMP, 2001)(30). Environmental pollution with toxic metals is becoming a global phenomenon. As a result of the increasing concern with the potential effects of the metallic contaminants on human health and the environment, the research on fundamental, applied and health aspects of trace metals in the environment is increasing (Vernet, 1991)(32). 2.2. Trace metals Metals are discovery of the old world. Humans began using metals in about 6000 B.C. Metals are everywhere, from air to water and to the deepest places in Earth. Metals are useful but they can be hazardous and toxic (Dahrazma, 2005)(33). The term “heavy metal” is -19- used to describe metals having density greater than 5-6 g cm-³ (Sedgwick, 2005)(34). Heavy metals are often referred to as trace metals, occurring naturally in low concentrations in organisms, although the term trace metal might imply the presence of an essential requirement by organisms for that particular metal (Furness and Rainbow, 2000)(35). Heavy metals can be divided into two groups namely; i) metals essential to at least some organisms (micronutrients) such as As, Cr, Cu, Ni, and Zn and ii) nonessential heavy metals with no known biological function which include Hg, Pb and Cd (Furness and Rainbow, 2000)(35). Even though micronutrients are essential to some forms of life, they become toxic at high concentrations (Sedgwick, 2005)(34). The contamination of sediments by trace metals is of particular importance because of their widespread use and their non degradable nature (Calmano et al., 1988)(36). The trace metals of greatest environmental concern are those that are both industrial and toxicological importance, such as Cd, Cr, Cu, Ni, Pb, Sn and Zn (Salbu and Steinnes, 1995)(37). Chromium (Cr VI) is classified as priority pollutant by the United States Environmental Protection Agency (USEPA) with a carcinogenicity classification A (human carcinogen), while Cd and Pb are classified in the same list with a carcinogenicity classification B (probable human carcinogen) (USEPA, 1999)(38). Trace metals are ubiquitous in the environment, and can enter aquatic systems through natural processes as well as anthropogenic loadings (Drever, 1997)(39). Metals participate in various biogeochemical mechanisms, have significant mobility, can affect the ecosystems through bioaccumulation processes and are potentially toxic for the environment and for human life (Manahan, 2000)(40). Metals are natural constituents of rocks, soils, sediments, and water. However, over the 200 years following the beginning of industrialization huge changes in the global budget of critical chemicals at the earth's surface have occurred, challenging those regulatory systems which took millions of years to evolve (Wood and Wang, 1983)(41). Advances in information of the distributions and concentrations of trace metals in the marine environment have occurred since the mid 1970s (Burton and Statham, 2000)(42). This is mainly due to developments in procedures for contamination free sampling, the adoption of clean methodologies for handling and analysis of samples, and increased application of improved analytical methods such as inductively coupled plasma-mass spectrometry (ICPMS) (Plant et al., 2003)(43). The trace metal content of sediments comes from natural sources (rock weathering, soil erosion, dissolution of water-soluble salts) as well as anthropogenic sources such as municipal wastewater treatment plants, manufacturing industries, and agricultural activities (Guven and Akinci, 2008)(44). Trace metals, which include Cr, Mn, Fe, Co, Ni, Cu, Zn, As, Pb, Cd, Hg, Ti and V enter the oceans as a result of natural processes and human activities via rivers, land runoff, dumping, atmosphere and the seabed. Major natural sources of these elements are rock weathering, degassing, emissions from terrestrial and submarine volcanoes and dissolution from marine sediments. Hence, in areas characterized by metal-bearing formations these metals occur at elevated concentrations in water and bottom sediments of the marine zones receiving the runoff (Munsgaard and Parry, 2002)(45). The dominant inputs of most trace metals to coastal areas are through rivers and land runoff but for a few elements such as Hg, As, and Pb the atmospheric route is also important, particularly in the open ocean, although even for these elements local discharges and rivers often dominate the coastal input. The important anthropogenic sources of metals like Cr, Mn, Co, Ni, Cu, Zn, Pb, Cd, Hg and As to coastal and inshore waters are industrial processing of ores and metals; ferrous and nonferrous metal industries including metal plating; industries producing both organic and inorganic chemicals; use of metal and metal components; leaching of metals from solid waste; -20- and offshore dumping of domestic sewage, sludge and industrial wastes (Owens et al., 1997)(46). Coastal environments continue to attract heavy investment in various economic activities such as tourism, aquaculture, industrialization, agricultural, mining and urbanization. Therefore coastal zone pollution problems are becoming increasingly prevalent, with potentially adverse environmental and socio-economic effects. Consequently in global context, anthropogenic fluxes of contaminants such as trace metals now exceed the natural flux in many areas (Onyari et al., 2003)(47). Other potential sources include ports, harbors, marinas and mooring sites, also subjected to trace metal inputs associated with recreational, commercial, and occasionally, military, boating, and shipping activities (Denton et al., 1997)(48). Trace metals have certain unique properties and characteristics, distinct from organic substances, which create difficulty in determining ecological risk. Because they are naturally occurring and ubiquitous in the environment, metals can concentrate at a particular site (e.g. related to a specific point source discharge) or on a regional scale (e.g. related to a particular watershed) due to natural processes. Metals can occur in the environment in various chemical forms. These different forms influence availability, hence extent of toxic effect, to organisms. The bioavailability and persistence of metals are generally controlled by external environmental conditions. These characteristics create challenges when assessing risk of metals in ecosystem (Kabata-Pendia and Pendia, 2000)(49). In aquatic systems trace metals play a dual role as toxicant and essential nutrient (Morel and Hering, 1993)(50). Metal risk assessment in aquatic system is considerably more complicated than that associated with organic chemicals. Unlike many organic chemicals, metals cannot be degraded biologically; they are, in a sense, infinitely persistent. Using a more scientifically defensible approach, one defines persistence in terms of bioavailable metal transport, fate, and bioavailability. These include chemical speciation (including redox chemistry), adsorption/desorption, and precipitation/dissolution (Adams et al., 2000)(51). The distribution of metals within the aquatic environments is governed by complex processes of material exchange affected by various anthropogenic activities or natural processes including riverine or atmospheric inputs, coastal and seafloor erosion, biological activities, water drainage, discharge or urban and industrial wastewaters (Ip Carman et al., 2007)(52). The pollutants from industrial activity and urban sewage commonly reach their final destination in the coastal waters through river mouths or by direct discharge into the sea. Metals are important among these pollutants because many of them are highly toxic and that they are not biodegradable in the environment (Morillo et al., 2002)(53). 2.2.1. Sources, uses and toxicity of trace metals Metals have many sources from which they can flow into the water body, these sources are: Natural sources: Metals are found throughout the earth, in rocks, soil and are introduced into the water body through natural processes, weathering and erosion (Rashed, 2004)(54). Trace metals occur naturally as they are components of the lithosphere and are released into the environment through volcanism and weathering of rocks (Fergusson, 1990)(3). Rivers: Trace metals can enter coastal and estuarine waters via riverine input, non point source runoff from land and direct point source discharges. Most rivers make a major contribution to trace metal loadings in estuarine and coastal waterways. A large quantity of trace metals in river water originates from weathering of rocks and leaching of soils. For this reason, the trace metal loading depends largely on the natural occurrence of metals and ore -21- bearing deposits in the catchment area. Where the river passes through industrial, agricultural or urbanized areas, stormwater runoff contributes to the dissolved or suspended metal burden within the river (Burton, 2005)(55). Atmospheric pollution : Acid rains containing trace metals as well as suspended particulate matter input to the water body will cause the pollution of water with metals (Rashed, 2004)(54). Mining and processing ores: Digging a mine, removing ore from it, and extraction and processing of the minerals may destroy habitats, farmland, and homes; produce soil erosion; and pollute waterways via toxic drainage. Ore processing, smelting, and refining operations can cause deposition of large quantities of trace metals, such as lead, zinc, copper, arsenic, and silver into drainage basins or direct discharge into aquatic environments (Csuros et al., 2002)(56). Fossil fuel combustion: Fossil combustion is a major source of airborne metal contamination of natural waters (Csuros et al., 2002)(56). Agricultural sources: Agricultural discharge contains residual of pesticides and fertilizers which contains metals (Rashed, 2004)(54). The metal content of agriculture runoff originate in sediments and soils saturated by animal and plant residues, fertilizers, specific herbicides and fungicides, and use of sewage and sludge as plant nutrients (Csuros et al., 2002)(56). Metal containing pesticides (such as Zn salts, Cu and Pb arsenates, and organometallic compounds) are used to control pests in horticultural and vegetable crops, and in turf cultivation. Major nutrient fertilizers often contain appreciable quantities of trace metals as impurities derived from the raw materials. Agricultural reuse of urban and farm wastes, such as pig and poultry waste slurries and sewage sludge, can also cause appreciable enrichment of agricultural soil with a range of metals. Under certain situations these metals may entre waterways via leaching and surface runoff (Burton, 2005)(55). Domestic wastewater effluents: Large amounts of heavy metals copper, lead, zinc, and cadmium, can be found in metabolic waste products, corrosion of water pipes from the domestic wastewater effluents while iron, manganese, chromium, nickel, cobalt, zinc, and arsenic are often present in household products, such as detergents. Although wastewater treatment can removes metals from the influent, more than 50% of metal content in the influent still remain in the effluent. Moreover, the sludge resulting from wastewater treatment is also one of the major artificial sources of cadmium, chromium, copper, iron, lead, and mercury pollution (Csuros et al., 2002)(56). Storm water runoff: Many activities such as city planning, traffic, road construction land use, can contribute to the metal pollution in the receiving waters via storm water runoff from the urbanized areas (Csuros et al., 2002)(56). In Heavily urbanized areas, stormwater runoff (generally regarded as a diffuse source) can make a significant contribution for a wide range of metals. Trace metals of greatest concern in urban stormwater runoff are Pb, Cu, Zn, Cd, As and Be. The principal diffuse urban sources are emissions from motor vehicles and metal release from weathering of surface material (Makepeace et al., 1995)(57). Industrial effluents and emissions: Trace metals are employed during the manufacturing of a wide variety of products. The most important activities are metal processing and finishing industries, such as coating, smelting and refining of non-ferrous metals, and iron/steel manufacturing. However, a number of other industries also use metals in their processes. These include paint/ink production, leather tanning/finishing, timber preservation, battery manufacturing and petroleum refining. Regulatory efforts to restrict the discharge of metalbearing effluents have lead to declines in industrial loadings of trace metals in natural waterways. However, there are many examples of areas where sediments remain contaminated as a result of past industrial discharges (Burton, 2005)(55). Trace metal -22- contributions from past mining activities have results in sever sediment contamination, with levels of contamination similar to those found in the mine tailings themselves (Teasdale et al., 2003)(58). Coastal waste disposal: other forms of disposal of solid and liquid waste in or near the marine environment contribute to the direct pollution of the sea in various ways, depending on the type and amount of the material disposed off. Maritime (offshore) sources: the pollutant discharged in greatest amounts is ballast oil from tankers. In many cases, beaches suffer a variable amount of damage. Ships also dispose of waste materials overbroad. In very general terms, the majority of the social economic consequences of marine pollution can be expressed as immediate of long-term effects on human health. In this context, the two main types of human exposure to pollutants in the marine environment are through direct contact with polluted seawater and/or beach sand, and consumption of contaminated seafood. In some cases where the seawater, after being treated in desalinization plants, is used for drinking purposes, pollution may constitute a potential health risk (WHO/UNEP, 1995)(59). Summary of past and present uses of some of the examined trace metals Metal Cadmium Chromium Copper Lead Nickel Zinc Uses of Metals and Compounds Electroplating (anticorrosion coatings); thermoplastic stabilizers, e.g. in PVC; Ni-Cd batteries; alloys; solders; catalysts; engraving; semiconductors; TV tube phosphorus; pigments in paints and plastics; glass ceramics; biocides (Denton et al., 1997) (48) Metallurgy-ferrochromium alloys, refractory bricks; electroplating; industrial dyes; ink; tanning; paint; wood preservative; glass making; cement production (Denton et al., 1997) (48) Electrical industry; alloys, e.g. brass; chemical catalyst; anti-fouling paint; algaecide; wood preservative (Denton et al., 1997) (48) Storage batteries; leaded gasoline; pigments; read lead paint; ammunition; solder; cable covering; anti-fouling paint; glazing; PVC stabilizers (Denton et al., 1997) (48) Hydrogenation oil processes, rechargeable batteries (nickelcadmium), ambient air at very low levels as a result of releases from oil and coal combustion, nickel metal refining, sewage sludge incineration, manufacturing facilities (Dean et al., 1972)(60) Cleaners, cosmetics, fillers, pesticides, inks, oils, medicines, paints, polish, preservatives, water treatment, fertilizers, oil refining, inorganic chemicals (Dean et al., 1972)(60). Cadmium (Cd) Cadmium is widely spread by human activity, volcanic activities and erosion. Large quantities of Cd are mainly used in the production of nickel-cadmium batteries or in welding (El Nemr, 2007a)(61). Cadmium is a heavy metal that is widely distributed in the environment. Its concentration in the earth's crust is generally estimated to be 0.15 to 0.20µgg-1, whereas that in uncontaminated soils is 0.40 µgg-1 (Fleischer et al.,1974)(62). The concentration in normal animal foods seldom exceeds 0.5 µgg-1 (Doyle et al., 1974)(63). Industrially, Cd is used extensively in the mining and electroplating industries and is found in fertilizers and fungicides. All chemical forms are toxic (Fleischer et al., 1974)(62). Cadmium is usually present as complex oxides, sulfides, and carbonates in zinc, lead and copper ores (Finkelman, 2005)(64). Cadmium in several aspects is similar to zinc and therefore, it is always associated with zinc in mineral deposits (Callender, 2003)(65). Cadmium is extremely toxic to -23- most plants and animal species particularly in the form of free cadmium ions (Denton et al., 1997)(48). The major sources of cadmium include metallurgical industries, municipal effluents, sewage sludge and mine wastes, fossil fuels and some phosphorus containing fertilizers (Denton et al., 2001)(66). Nonferrous metal mines represent a major source of cadmium to the aquatic environment. Contamination can arise from mine drainage water, waste water from the processing of ores, overflow from the tailings pond, and rainwater runoff from the general mine area. The release of these effluents to local watercourses can lead to excessive contamination downstream of the mining operation (Morley et al., 1997)(67). In sediments, cadmium does not appear to be absorbed to colloidal material, but organic matter, such as humic substances and organic debris, appear to be the main sorption material for the metal. Cadmium levels tend to increase with decrease in size and increase in density in terms of partition of sediment samples by size and density. The sorption of cadmium to sediments, and to the clay content, increases with pH. The release of cadmium from the sediment is influenced by a number of factors including acidity, redox conditions and complexing agents in the water. Under alkaline conditions, cadmium is less mobile (Fergusson, 1990)(3). Also under saline conditions, Cl¯ ion affects the mobility of cadmium (Morrison et al., 1996)(68). The average cadmium level of sea water has been given as about 0.1 µg L-1 or less (Owen and Sandhu, 2000)(69). WHO (1995)(70) reported that current measurements of dissolved cadmium in surface waters of the open oceans gave values of <5 ng L -1. The vertical distribution of dissolved cadmium in ocean waters is characterized by a surface depletion and deep water enrichment, which corresponds to the pattern of nutrient concentrations in these areas (Shen et al., 1987)(71). This distribution is considered to result from the absorption of cadmium by phytoplankton in surface waters and its transport to the depths, incorporation to biological debris, and subsequent release. In contrast, cadmium is enriched in the surface waters of areas of upwelling and this also leads to elevated levels in plankton unconnected with human activity. Oceanic sediments underlying these areas of high productivity can contain markedly elevated cadmium levels as a result of inputs associated with biological debris (Simpson, 1981)(72). Cadmium can potentially harm human health depending upon the form of cadmium present, the amount taken in, and whether the cadmium is eaten or breathed. If the levels are high enough, the cadmium in the kidney will cause kidney damage and also may cause bones to become fragile and easily broken (Finkelman, 2005)(64). Moreover, when ingested by humans, cadmium accumulates in the intestine, liver and kidney (WHO, 2004)(73). The kidney cortex is regarded as the most sensitive organ. The health effects of chronic exposure of Cd include proximal tubular disease and osteomalacia (Jambe and Nandini, 2009)(74). It accumulates in the body, especially in the kidney and the liver, over many years because the body has no homeostatic mechanism to keep Cd at a constant safe level, such as those that function for zinc. Hence, Cd is a cumulative poison (Miller, 1971)(75). The major effects of cadmium poisoning are experienced in the lungs, kidneys and bones. Acute effects of inhalation are bronchitis and toxemia in the liver. Chronic inhalation of cadmium compounds as fumes or dust produce pulmonary emphysema, where the small air sacs of the lungs become distended and eventually destroyed reducing lung capacity (Ansari et al., 2004)(76). Cadmium is a serious environmental contaminant that is also transported atmospherically. In fish, it can cause anaemia and vertebral fractures, osmoregulatory problems, decreased digestive efficiency, haematological and biochemical effects, erratic swimming, and mortality (Burger, 2002)(77). -24- Chromium (Cr) Chromium like zinc, is one of the most abundant heavy metals in the lithosphere with an average concentration of about 69 and mercury level in carbonate sediments is reported to be 0.03 µgg-1 (Callender, 2003)(65). Chromium is moderately toxic to aquatic organisms. Major coastal marine contributors of chromium are dominated by input from rivers, urban runoff, domestic and industrial wastewaters and sewage sludge (Denton et al., 1997)(48). Also other major sources in the aquatic environment include the waste stream from electroplating and metal finishing industry (Finkelman, 2005)(64). Chromium is found chiefly in Chrome-Iron Ore (FeO-Cr2O3). Chromium is considered non-essential for plants, but an essential element for animals. The average abundance of Cr in the earth's crust is 122µgg-1; in soils Cr ranges from 11-22 µgg-1. It is used in alloys, in electroplating and in pigments. Chromium and its salts are used in the leather tanning industry, the manufacture of catalyst, pigments and paints, fungicides, the ceramic and glass industry and in photography and for chrome alloy and chromium metal production, chrome plating and corrosion control (Abbasi et al., 1998)(78). Hexavalent compounds are carcinogenic by inhalation and are corrosive to tissues. There is an environmental cycle for chromium, from rocks and soils to water, biota, air, and back to the soil. However, a substantial amount (estimated at 6.7 x 106 kg per year) is diverted from this cycle by discharge into streams, and by run-off and dumping into the sea (Schulz and Zabel, 2000)(79). Cr has been considered a metal with low biogeochemical mobility which should reduce its toxicity potential (Muniz et al., 2004).(80) Chromium is carcinogenic to humans and long term exposure has been associated with lung cancer in workers exposed to levels in air that in the order of 100 to 1,000 times higher than usually found in the environment (Finkelman, 2005)(64). Trivalent chromium (Cr3+) may be essential in human nutrition, but hexa-valent chromium (Cr+6) is highly toxic. Intake of hexa-valent chromium can cause hemorrhaging in the liver, kidneys, and respiratory organs. When people are exposed to hexa-valent chromium, dermatitis and ulceration and perforation of the nasal septum have been developed. Also, gastric cancers, presumably from excessive inhalation of dust containing chromium, have been reported (Fergusson, 1990)(3). Copper (Cu) The average abundance of Copper is 68 µgg-1; in soils it is between 9 and 33 µgg-1. Copper is widely used in electrical wiring, roofing, various alloy, pigments, cooking utensils, piping and in the chemical industry. Copper is present in munitions, alloys (brass, bronze) and coatings. Copper compounds are used as or in fungicides algicides, instecticides, and wood preservatives and in electroplating, azo dye manufacture, engraving, lithography, petroleum refining and pyrotechnics. Copper compounds can be added to fertilizers and animal feeds as a nutrient to support plant and animal growth. Copper compounds are also used as food additives (Abbasi et al., 1998)(78). In addition, copper salts are used in water supply systems to control biological growths in reservoirs and distribution pipes and it forms a number of complexes in natural waters with inorganic and organic lignads (WHO, 2004)(73). The aqueous species of copper include Cu 2+, Cu(OH)2 and CuHCO3+(Jumbe and Nandini, 2009)(74). Inputs of copper into the natural waters come from various sources including mining, smelting, domestic and industrial wastewaters, steam electrical production, incinerator emissions, and the dumping of sewage sludge. Algaecides and antifouling paints are identified as major contributors of copper to harbor areas whereas coastal waters are generally receiving inputs from rivers and atmospheric sources (Denton et al., 1997)(48). Copper has a high -25- affinity for clay mineral fractions, especially those rich in coatings containing organic carbon and manganese oxides (Callender, 2003)(65) and as a result, residues are often elevated in sediments near localized sources of inputs (Denton et al., 1997)(48). Callender (2003)(65) reported that the adsorption behavior of copper in natural systems is strongly dependent on the type and concentration of inorganic and organic ligands. Copper exists in construction materials, pesticides, fertilizers, sprays, and agricultural and municipal wastes as well as industrial wastes. As these materials are exposed to the environment the levels of copper increase. The average level of copper in plants is in the range of 5 to 30 µgg-1 while in soil it varies between 2 to 100 µgg-1 (Cameron, 1992)(81). Because Cu is an essential trace nutrient, most marine organisms have evolved mechanisms to regulate concentrations of this metal in their tissues in the presence of variable concentrations in the ambient water, sediment and food (Mohammed, 1991)(82). Although essential for life due to its major role in enzyme functions, copper in large amounts is quite toxic. For example, copper salts are used to kill bacteria, fungi, and algae, and paints containing copper are used on ship hulls to prevent fouling by marine organisms. Acute exposure overdose causes an immediate metallic taste, followed by epigastric burning, nausea, vomiting, and diarrhea (Fergusson, 1990)(3). Regulation of copper in the human body is not sufficient with very low amounts of dietary copper (0.38 mg/day) and it appears to be delayed when copper intake is high (Turnlund, 1998)(83). Pro-oxidant activity of copper ions can make it extremely toxic at elevated levels. Copper related inherited disorders such as Menkes disease (due to copper deficiency) and Wilson disease (due to copper toxicosis) demonstrate the necessity and potential toxicity of copper. There is a good chance of involving copper induced oxidative damage in other pathogenic or neurodegenerative conditions such as Alzheimer's disease and prion diseases (LIanos and Mercer, 2002)(84). Copper is essential for good health. However, exposure to higher doses can be fatal. Long term exposure to copper results in nose irritation, mouth, and eyes, and cause headaches, dizziness, nausea, and diarrhea (Finkelman, 2005)(64). It is an essential element in the normal metabolism of plants, animals and human life, however in high levels, causes many diseases (Gratten et al., 2003)(85). In high levels, it accumulates in blood, liver, and kidneys and causes anemia, renal and intestinal irritations, coma death, and Wilson's disease (Gratten et al., 2003)(85). Cobalt (Co) Cobalt is a silvery grey solid at room temperature. It is the 33rd most abundant element and has been found in a variety of media, including air, surface water, leachate from hazardous waste sites, groundwater, soil, and sediment. Sources of exposure to cobalt and inorganic cobalt compounds are both natural and anthropogenic (Barceloux, 1999)(86). Natural sources include wind-blown dust, seawater spray, volcanoes, forest fires, and continental and marine biogenic emissions. Anthropogenic sources include the burning of fossil fuels, sewage sludge, phosphate fertilizers, mining and smelting of cobalt ores, processing of cobalt alloys, and industries that use or process cobalt compounds. Cobalt released into the atmosphere is deposited on soil, and cobalt released to water may sorb to particles and settle into sediment or sorb directly to sediment (Erdogan, 2009)(87). The average cobalt abundance in earth's crust is 29 µgg-1; in soils it is 1.0-14 µgg-1. Cobalt is widely used as alloy for various steel, in electroplating, in fertilizers, porcelain and glass making. Cobalt is considered essential for algae and bacteria but not essential to higher plants. In animals it is only requires in trace basis (WHO, 2004)(73). The distribution coefficient of cobalt varies due to pH, redox conditions, ionic strength, and dissolved organic matter concentrations. Factors affecting the speciation and -26- fate of cobalt in water, sediments, and soil include organic ligands such as humic acids, anions, pH, and redox potential. The soil mobility of cobalt is inversely related to the strength of adsorption by soil constituents. Although plants may take up cobalt from the soil, the translocation of cobalt from the roots to other parts of the plant is not significant. Mean cobalt concentrations in seawater have been reported to be less than 1 µgL-1. Cobalt concentrations in drinking water are generally <1–2 µgL-1. In rainwater, mean concentrations are 0.3–1.7 µgL-1. The earth’s crust contains an average cobalt concentration of 20–25 µgg-1. Near some anthropogenic sources, the concentration of cobalt in soil may be several hundred milligrams per kilogram. The major anthropogenic sources of environmental cobalt include mining and processing of cobalt-bearing ores, the use of cobalt-containing sludge or phosphate fertilizers on soil, the disposal of cobalt containing waste, and atmospheric deposition from activities such as the burning of fossil fuels and smelting and refining of metals (Smith and Carson, 1981)(88). Cobalt is beneficial for humans because it is a part of vitamin B12, which is essential for human health. Cobalt is used to treat anemia with pregnant women, because it stimulate the production of red blood cells. However, too high concentrations of cobalt may damage human health. When we breath in too high concentrations of cobalt through air we experience lung effects, such as asthma and pneumonia. This mainly occurs with people that work with cobalt. Soils near mining and melting facilities may contain very high amounts of cobalt, so that the uptake by humans through eating plants can cause health effects. Health effects that are a result of uptake of high concentrations of cobalt are: vomiting and nausea, vision problems, heart problem, and thyroid damage. Health effects may also be caused by radiation of radioactive cobalt isotopes. This can cause sterility, hair loss, vomiting, bleeding, diarrhea, coma and even death. This radiation is sometimes used with cancer patients to destroy tumors. Cobalt dust may cause asthma like disease with symptoms ranging from cough, shortness of breath and dyspnea to decreased pulmonary function, nodular fibrosis, permanent disability and death. Exposure to cobalt may cause weight loss, dermatitis, and respiratory hypersensitivity (Greenwood and Earnshaw, 1984)(89). Lead (Pb) Lead is one of the oldest known metals. Its emission into the atmosphere has much increased during the last century. Its anthropogenic inputs greatly exceed those from natural sources. The atmospheric fallout of lead constitutes its most important source in the aquatic environment (Moore and Ramamoorthy, 1984)(90). It is present in all tissues of organisms causing hazardous effects, as it is a cumulative poison (Saad, 2004)(91). In fish, lead can cause deficits or decreases in survival, growth rates, development, and metabolism, in addition to increased mucus formation (Burger et al., 2002)(77). Lead is one of the most abundant toxic metals in earth's crust. It has been used since prehistoric times and has become widely distributed and mobilized in the environment. Exposure to lead in the environmental and occupational settings continues to be a serious public health problem (WHO, 1995)(92). The average abundance in Earth's crust is 13µgg-1; in natural soils background level ranges from 2.6-25 µgg-1; the common aqueous species are hydroxides and carbonates of Pb2+. Lead in water comes from industrial, mines and smelter discharges before being deposited in the sediment sinks. Lead is non essential for plants and animals and is toxic by ingestion-being a cumulative poison. Lead is also used in the production of lead acid batteries, solder, alloys cable sheathing, pigments, rust inhibitors, ammunition, glazes and plastic stabilizers. Tetraethyl and tetramethyl lead are important because of their extensive use as antiknock compounds in petrol (Sharma and Pervez, 2003)(93). Lead is reported to be in the 15-50 µgg-1 range for coastal and estuarine sediments around the world with < 25 µgg-1 in clean coastal sediments (Denton et al., 1997)(48). -27- The main sources of Pb in natural waters include manufacturing processes (especially metals), atmospheric deposition (e.g. from pyrometallurgical nonferrous metal production; the combustion of leaded fuels; the burning of wood and coal; and the incineration of municipal refuse). Other sources include domestic wastewaters, sewage and sewage sludge (Denton et al., 1997)(48). Metallic lead does occur in nature, but it is rare. Lead is usually found in ore with zinc, silver and copper, and is extracted together with these metals. The main lead mineral is galena (PbS), which contains 86.6% lead. Inorganic lead is moderately toxic to aquatic flora and ranks behind mercury, cadmium, copper and zinc in the order of toxicity to invertebrates. On the other hand, organolead compounds, particularly the alkyl-lead compounds are considered toxic to any forms of life (Denton et al., 1997)(48). Inorganic lead is moderately toxic to aquatic flora and ranks behind mercury, cadmium, copper and zinc in the order of toxicity to invertebrates. Organolead compounds, on the other hand, particularly the alkyl-lead compounds used as antiknock agents in gasoline, are considered toxic to any forms of life (Denton et al., 1997)(48). Lead is a non essential element, being a toxic metal that can affect humans when ingested or inhaled in high doses, causing encephalopathy, colic, renal diseases, and anemia. In particular, children are susceptible to lead toxicity, with numerous epidemiological studies reporting neurocongitive functions to be inversely correlated with blood or tooth lead levels (USCDC, 1991)(94). Lead enters the body through breathing or swallowing and the main target for lead toxicity is the nervous system. Lead exposure may also cause weakness in fingers, wrists, or ankles and miscarriage for pregnant women (Finkelman, 2005)(64). Lead is toxic to the nervous system of human beings, especially children. It is readily absorbed from the intestinal tract and deposited in the central nervous system. High lead levels in blood (more than 10µg/dl) may contribute to learning disabilities, nervous system damage, and stunted growth (Fergusson, 1990)(3). The chronic effect of lead on man includes neurological disorders, especially in the foetus and children. This can lead to behavioral changes and impaired performance in IQ tests (Needleman, 1987)(95). Lead toxicity leads to anaemia both by impairment of haemobiosynthesis and acceleration of red blood cell destruction. Both are dose related. Lead also depresses sperm count (Anglin-Brown et al., 1995)(96). In addition, Pb can also produce a damaging effect on the kidney, liver, male and nervous system, blood vessels and other tissues (Sharma and Pervez, 2003)(93). Nickel (Ni) Nickel is a ubiquitous trace metal and occurs in soil, water, air, and in the biosphere. Levels in natural waters have been found to range from 2 to 10 µg L-1 (fresh water) and from 0.2 to 0.7 µg L-1 (marine). The prevalence ionic form is nickel (II) (WHO, 1991)(97). The common aqueous species found in water is predominantly Ni 2+. It is suspected to be essential trace elements for plants and animals. Nickel may be present in some ground waters as a consequence of dissolution from nickel ore-bearing rocks. Nickel is used principally in its metallic form combined with other metals and nonmetals as alloys. Nickel alloys are characterized by their hardness, strength and resistance to corrosion and heat. Nickel is also used mainly in the production of stainless steels, non-ferrrous alloys and super alloys. Other uses of nickel-cadmium batteries, in coins, in welding products. It is estimated that 8% of nickel is used for household appliance. Nickel is also incorporated in some food supplements, which can contains several microorganisms of nickel per tablet (WHO, 2004)(73). Nickel is moderately toxic to most species of aquatic plants, though it is one of the least toxic inorganic agents to invertebrates and fish. The major source of discharge to natural waters is municipal wastewater followed by smelting and the refining of nonferrous metals (Denton et al., 2001)(66). Also mine drainage effluents are known to be major contributors due to high concentrations of nickel found in the discharges (Finkelman, 2005)(64). Typically, -28- nickel residues in sediments can be up to 100 µgg-1 or higher but may fall below 1 µgg-1 in some clean coastal waters (Denton et al., 1997)(48) with the average concentration of nickel in the lithosphere of 55 (Callender, 2003)(65). Major uses of nickel include its metallurgical use as an alloy, plating and electroplating, a major component of Ni-Cd batteries, and as a catalyst for hydrogenating vegetable oils (Callender, 2003)(65). Most nickel is used for the production of stainless steel and other nickel alloys with high corrosion and temperature resistance. Nickel alloys and nickel plating are used in vehicles, processing, machinery, armaments, tools, electrical equipment, household appliances, and coinage. Nickel compounds are also used as catalyst, pigments, and in batteries. The primary sources of nickel emissions into the ambient air are the combustion of coal and oil for heat or power generation, the incineration of waste and sewage sludge, nickel mining and primary production, steel manufacture, electroplating, and miscellaneous sources such as cement manufacturing. Nickel from various industrial processes and other sources finally, reaches waste water. Residues from waste-water treatment are disposed of by deep well injection, ocean dumping, land treatment, and incineration (WHO, 1991)(97). Entry into the aquatic environment is by removal from the atmosphere, by surface runoff, by discharge of industrial and municipal waste, and also following natural erosion of soils and rocks. In rivers, nickel is mainly transported in the form of a precipitated coating on particles and in association with organic mater (Schuz and Zabel, 2000)(79). In the bottom sediments of estuaries in which anaerobic conditions often occur, sulfide tends to control the mobility of nickel. However, under aerobic conditions, the solubility of nickel is mainly controlled by either the co-precipitate NiFe2O4 or Ni(OH)2(s) (Callender, 2003)(65). Although the role of nickel in the human body is not known, it is an essential nutrient for other mammalian species and has been suggested to be essential for human nutrition as well. Following data from animals, it is estimated by extrapolation that a 70kg person would have a daily requirement of 50 µg per kg nickel. Since nickel is an element of the crust of the earth, it exists in food, air, and water. Food is believed to be the major source of nickel exposure. In the US, an average intake for adults of approximately 100 to 300 micrograms per day (µg/d) is estimated. Nickel production, processing, and use, contact with everyday items such as nickel-containing jewelry and stainless steel cooking and eating utensils, and smoking tobacco are major sources of exposure of nickel to humans (USEPA, 2001)(98). Nickel and its compounds have little toxicity. Nickel itch or contact dermatitis is the most commonly seen reaction to nickel compounds especially in women due to use of nickel in costume jewelry, especially earrings. Chronic exposure to nickel causes cancer in the respiratory tract and the lungs (Fergusson, 1990)(3). Among Nickel's properties, its mutagenic, immunotoxic, carcinogenic and teratogenic properties are the most important. Due to efficient phagocytosis into the cells, solid nickel compounds are the most toxic, at least in regard to carcinogenicity and mutagenicity. In addition, water soluble salts, like NiCl2, are also mutagenic. Nickel salts have been found to be harmful for reproduction of laboratory rodents. Embryonal and fetal mortality have been found to increase when females have been exposed to nickel (Kakela et al., 1999; Snodgrass, 1980)(99, 100). Some of the most serious health effects due to exposure to nickel include reduced lung function some nickel compounds are reported to be carcinogenic to humans and metallic nickel may also be carcinogenic (Finkelman, 2005)(64). Zinc (Zn) The average abundance of Zn in Earth's crust is 76µgg-1; in soils it is 25-68 µgg-1. Zinc is used in a number of alloys including brass and bronze, batteries, fungicides and -29- pigments. Zinc is an essential growth element for plants and animals but at elevated levels it is toxic to some species of aquatic life (Eaton and Franson, 2005)(101). In addition, Zn is involved in a variety of enzyme systems which contribute to energy metabolism, transcription and translation. Zinc is also potentially hazardous and excessive concentrations in soil lead to phytotoxicity as it is a weed killer (Abbasi et al., 1998)(78). Zinc is used in galvanizing steel and iron products. Zinc oxide, used in rubber as a white pigment, for example, is the most widely used zinc compound. Peroral zince is occasionally used to treat zinc deficiency in humans. Zinc carbamates are used as pesticides (Anglin-Brown, 1995)(96). Zinc is one of the most ubiquitous and mobile of the trace metals and it transported in natural waters in both dissolved forms and associated with suspended particles (Mance, 1987)(102). In river waters, zinc is predominantly present in the dissolved form. In estuaries, where concentrations of suspended particles are greater, a greater proportion of the zinc is adsorbed to suspended particles (CCREM, 1987)(103). In low salinity areas of estuaries, zinc can be mobilized from particles by microbial degradation of organic matter and displacement by calcium and magnesium. In the turbidity maximum, zinc associated with suspended sediment will be deposited with flocculated particles where it can accumulate particularly in anaerobic sediments (Schulz and Zabel, 2000)(79). In seawater, much of the zinc is found in dissolved form as inorganic and organic complexes. However, zinc (and nickel) are less toxic metals. Zinc is the most abundant trace metals in human body. It functions as a cofactor where many enzymes depends upon it as well as body cells (Al-Ouran, 2005)(104). Zinc is widely used in modern society, most commonly to coat or galvanise iron to prevent corrosion. It is also mixed with other metals to form alloys such as brass. Particles released from vehicle tyres and brake linings are a major source of zinc in the environment (WHO, 2001)(105). Zinc is a very common environmental contaminant and it is commonly found in association with lead and cadmium (Finkelman, 2005)(64). It is used in coating to protect iron and steel, in alloys for die casting, in brass, in strips of dry batteries, in roofing and in some print processes (Al-Ouran, 2005)(104). Although it is not regarded as particularly toxic, it is sometimes released into the sea in substantial quantities (Denton et al., 2001)(66). It may enter the aquatic environment through natural or anthropogenic sources, including sewage and industrial discharge (Al-Ouran, 2005)(104). Major sources of Zinc to the aquatic environment include the discharge of domestic wastewaters; coal-burning power plants; manufacturing processes involving metals; and atmospheric fallout (Denton et al., 2001)(66). Approximately one third of all atmospheric zinc emissions are from natural sources, the rest come from nonferrous metals, burning of fossil fuels and municipal wastes, and from fertilizer and cement production (Callender, 2003)(65). Zinc is an essential micronutrient in all marine organisms, being a cofactor in nearly 300 enzymes. Therefore, marine animals are able to regulate tissue Zn at the concentrations in sea water and sediment from normal ambient levels to incipient lethal levels (Franca et al., 2005)(106). Several crustacean are able to regulate the uptake of zinc but, at higher concentrations, this process appears to breakdown leading to an influx of zinc (Schulz and Zabel, 2000)(79). Zinc is the second most abundant trace element in the body (after iron), and the brain has its share, with about 10 mg of zinc in a gram of wet tissue (Choi and Koh, 1998)(107). The required daily intake for the human body ranges from 10 to 20 mg (Smith et al., 1976)(108). Zinc is an essential structural element of many proteins. Neural activity releases zinc as a signaling messenger at many central excitatory synapses. New evidence suggests that zinc may also be a parameter in neuronal death associated with transit global ischemia, sustained seizures, and perhaps other neurological disease states (Choi and Koh, 1998)(107). Excessive -30- zinc intake may inhibit copper absorption and lead to copper deficiency. Acidic beverages packaged in galvanized containers may produce toxic zinc concentration levels, causing nausea, vomiting, stomach cramps, and diarrhea (Fergusson, 1990)(3). Taking excess zinc into the body through food, water and dietary supplements can have adverse effects on health. Ingesting high levels of zinc for several months may cause anemia, damage to pancreas, and decrease levels of high-density lipoprotein (HDL) cholesterol (Finkelman, 2005)(64). Zinc is an essential nutrient for the human body and has an importance for health (Hotz et al., 2003)(109). Zinc acts as a catalytic or structural component in many enzymes that are involved in energy metabolism and in transcription and translation of RNA (Moolenaar, 1998)(110). Zinc also has a prominent role in determining the outcome of pregnancies and supporting neurobehavioral development (Hotz et al., 2003)(109). However, like other metals, it can be toxic in high concentrations (ANZECC/ARMCANZ, 2000)(111). Although uncommon, gastrointestinal distress and diarrhoea have been reported following ingestion of beverages standing in galvanized cans or from use of galvanised utensils (WHO, 2001)(105). Other symptoms of Zn toxicity are slow reflexes, shakes, paralyzation of extremities, anaemia, metabolic disorder, terratogenic effects and increased mortality (Klaassen, 1996)(112). Taking excess zinc into the body through food, water and dietary supplements can have adverse effects on health. Ingesting high levels of zinc for several months may cause anemia, damage to pancreas, and decrease levels of high-density lipoprotein (HDL) cholesterol (Finkelman, 2005)(64). Manganese (Mn) Mn in Earth's crust is 1600 µgg-1; in soils it is 61-1060 µgg-1. The common aqueous species found in water is predominantly M2+ and M4+. Manganese is essential for plants and animal. Manganese dioxide and other manganese compounds are used in products such as batteries, glass and fireworks. Potassium permanganate is used as an antioxidant for cleaning, bleaching and disinfection purposes. Manganese greensands are used in some locations for potable water treatment. An organic manganese compound, Methylcyclopentadienyl Manganese tricarbonyl (MMT), is used as an octane-enhancing agent in unleaded petrol. Other manganese compounds are used in fertilizers, varnish and fungicides and as livestock feeding supplements. Manganese can be adsorbed onto soil, the extent of adsorption depending on the organic content and cation exchange capacity of the soil. It can bioaccumulate in lower organisms (e.g. phytoplankton, algae, mollusks, and some fish) but not in higher organisms; bio-magnification in food chains is not expected to be very significant (WHO, 2004)(73). Manganese is the 11th element in terms of abundance in the earth crust (Anschutz et al., 2005)(113). Oxidized forms of Mn are very reactive and have a strong capacity for adsorption of trace metals and play and important role as both an electron donor and acceptor in redox processes of aquatic environments (Chester et al., 1988)(114). Manganese is a naturally occurring element in the environment. It comprises about 0.1% of the earth’s crust (NAS, 1973)(115), and found in rock, soil, water, and food. Thus, all humans are exposed to manganese, and it is a normal component of the human body. Food is usually the most important route of exposure for humans. Manganese is released to air mainly as particulate matter, and the fate and transport of the particles depend on their size and density and on wind speed and direction. Some manganese compounds are readily soluble in water, so significant exposures can also occur by ingestion of contaminated drinking water. Manganese in surface water can oxidize or adsorb to sediment particles and settle to the bottom. Manganese in soil can migrate as particulate matter to air or water, or soluble manganese compounds can be leached from the soil (Erdogan, 2009)(87). -31- Manganese does not occur naturally as a base metal but is a component of more than 100 minerals, including various sulfides, oxides, carbonates, silicates, phosphates, and borates. The most commonly occurring manganese-bearing minerals include pyrolusite (manganese dioxide), rhodocrosite (manganese carbonate), and rhodonite (manganese silicate) (NAS, 1973)(115). Natural levels of manganese in soil range from 40 to 900 µgg-1, with an estimated mean of 330 µgg-1 (Rope et al., 1988)(116). Accumulation of manganese in soil usually occurs in the subsoil and not on the soil surface (WHO, 1981)(117). Manganese is an essential trace element for both animals and man necessary for the formation of connective tissue and bone, and for growth, carbohydrate and lipid metabolism, the embryonic development of the inner ear, and reproductive functions. Some specific biochemical functions of manganese have been discovered such as the catalysing of the glucosamine-serine linkages in the synthesis of the mucopolysaccharides of cartilage. Terrestrial mammals however, may concentrate available manganese up to a factor of 10, whereas fish and marine plants concentrate it by factors of 100 and 100 000, respectively (Preston et al., 1972)(118). The accumulation of manganese in living organism has the potential of reaching toxic levels. Symptoms of the Manganese toxicity in man include dullness, weak muscles, headaches and insomnia. In chronic inhalation exposure to manganese, the main organ systems affected are the lungs, nervous system, and reproductive system, although effects on other organ systems have also been observed (Erdogan, 2009)(87). Iron (Fe) Iron is the most abundant metal, and is believed to be the tenth most abundant element in the universe. Iron is a metal extracted from iron ore, and is hardly ever found in the free (elemental) state. Iron is the most used of all the metals, comprising 95 percent of all the metal tonnage produced worldwide. Its combination of low cost and high strength make it indispensable, especially in applications like automobiles, the hulls of large ships, and structural components for buildings. Steel is the best known alloy of iron (Greaney, 2005)(119). Iron is the fourth most abundant element in the Earth's crust. While it is naturally released into the environment from weathering, it may also be released into the aquatic environment through human activities, such as burning of coke and coal, acid mine drainage, mineral processing, sewage, iron related industries and the corrosion of iron and steel (CCREM, 1987)(103). Iron is essential to all organisms, except for a few bacteria. It is mostly stably incorporated in the inside of metalloproteins, because in exposed or in free form it causes production of free radicals that are generally toxic to cells. Iron binds avidly to virtually all biomolecules so it will adhere nonspecifically to cell membranes, nucleic acids, proteins etc. Iron distribution is heavily regulated in mammals. The iron absorbed from the duodenum binds to transferrin, and carried by blood it reaches different cells. It is strongly advised not to let the chemical enter into the environment because it persists in the environment. Excess iron in the body causes liver and kidney damage (haemochromatosis). Some iron compounds are suspected carcinogens (Greaney, 2005)(119). Iron toxicity is due to its rapid absorption by the body. Drinking water, iron pipes, cookware, and preparations are the main sources of iron and its target organs are the liver, cardiovascular system, and kidneys (Almoray and Belhadj, 2007)(120). Iron, one of the most abundant metals on Earth, is essential to most life forms and to normal human physiology. Iron is an integral part of many proteins and enzymes that maintain good health (Institute of Medicine, 2001)(121). In humans, iron is an essential component of proteins involved in oxygen transport (Dallman, 1986)(122). It is also essential for the regulation of cell growth and differentiation (Andrews, 1999)(123). A deficiency if iron -32- limits oxygen delivery to cells, resulting in fatigue, poor work performance, and decreased immunity (Institute of Medicine, 2001)(121). On the other hand, excess amount of iron in man can result in toxicity and even death (Corbett, 1995)(124). There is considerable potential for iron toxicity because very little iron is excreted from the body. Thus, iron can accumulate in body tissues and organs when normal storage sites are full. For example, people with hemachromatosis are at risk of developing iron toxicity because of their high iron stores. Symptoms of Alzheimer's and Parkinson's disease may also be iron-related (Corbett, 1995)(124). High iron concentrations affect vital organs in humans including the liver, cardiovascular system and kidneys (Alabaster and Lloyd, 1980)(125). 2.2.2. Pollution of the Aquatic Environment with Trace Metals The aquatic environment with its water quality is considered the main factor controlling the state of health and disease in both man and animal (Rashed, 2004)(54). Nowadays, the increasing use of the waste chemical and agricultural drainage systems represents the most dangerous form of chemical pollution particularly heavy metal pollution. The most important heavy metals from the point of view of water pollution are Zinc (Zn), Copper (Cu), Lead (Pb), Cadmium (Cd), Mercury (Hg), Nickel (Ni) and Chromium (Cr) (Rashed, 2004)(54). When trace metals enter the aquatic environment, the metal ions can react with constituents of the water or settle to the bottom and react with the sediments. Trace metals have a greater chance of remaining in solution when complexed to chelating ligands such as specific anions whose concentrations are described by the pH of the surrounding environment. Metals precipitate as oxides/hydroxides at different pH regions and the amphoteric elements return to solution at higher pH. The hydroxide concentration (or pH) is therefore of great importance for the mobility of metals. Other factors also affect the fate of the metal ions like redox conditions and the presence of adsorbent sediments (Alloway and Ayres, 1998)(126). There are basically three reservoirs of metals in the aquatic environment: water, sediment and biota. Metal levels in each of these three reservoirs are dominated by a complex dynamic equilibrium governed by various physical, chemical and biological factors (Murray and Murray, 1973)(127). Among these three reservoirs, sediment is the major repository for metals, in some cases, holding over 99% of the total amount of metal present in the system (Renfro, 1973)(128). The analysis of sediment is a useful method of studying aquatic pollution with trace metals (Batley, 1989)(129). Contaminated sediments, in both freshwater and marine systems, are a significant issue worldwide. Contaminants can persist for many years in sediments, where they have the potential to adversely affect human health and the environment. Some chemicals continue to be released to surface waters from industrial and municipal sources and polluted run-off streams from urban agricultural areas and build up harmful levels of contamination in sediments (Mackeviciene et al., 2002)(130). The enrichment of metals in sediments is influenced by allocthonous influence which is made up of natural and anthropogenic effects and autochthonous influences comprising of precipitation, sorption, enrichment of organism and organometallic completion during sedimentation as well as the post depositional effects of digeneses (Forstner and Witlmann, 1979)(131). 2.2.2.1. Trace metals in the water column Sources of trace metals in the water column Trace metals in the water column are contributed by natural and anthropogenic sources. They enter the water body naturally from the atmosphere and via run-off and, in the -33- case of larger water bodies such as lakes and oceans, from smaller streams and rivers. Some of the anthropogenic sources of trace metals include industrial wastes and by-products generated by mining and smelting, production and use of materials containing the heavy metals, burning of fossil fuels, leaching of waste dumps, urban run-off, sewage effluent, shipping, waste dumping and agriculture run-off. Trace metal partitioning – dissolved and particulate phases In the marine environment, trace metals are partitioned amongst dissolved phases, suspended and bottom sediments and biota in the water column. According to Elder (1988)(132) the fractionation of trace metals depends on many factors including organic matter composition, pH, salinity and binding affinities of heavy metals. The dissolved fraction that represents the principal source of bio-available metals is favored under conditions of low pH, low particulate loads and high concentrations of dissolved organic matter. Low pH is particularly important because: (i) The solubility of metal hydroxides increases as pH decreases; (ii) The adsorption capacity of solid surfaces decreases; and (iii) H+ ions compete with metals for coordination sites on organic molecules. More trace metals may also enter solution as water hardness increases since cations (especially Ca2+ and Mg2+) also compete with metals for binding sites. However, increasing salinity usually results in reduced dissolved metal concentrations due to clay-organic particles forming flocs with a high settling velocity. High pH and Eh as well as elevated particulate organic matter concentrations favor metal partitioning to bottom sediments, or to suspended particulate phases if hydraulic energy is high enough (Elder, 1988)(132). -34- Metal partitioning in water column among 3 major phases (inside triangle) and some environmental conditions that favor each phase (outside triangle)(Elder, 1988) Distribution and behavior of trace metals in the water column A number of studies have been carried out in order to investigate the distribution and fate of trace metals in the water column. Zeri and Voutsinou-Taliadouri (2003)(133) indicated that the distribution and behavior of trace metals in the seawater column and sediments were controlled by many complicated physiochemical processes such as hydrodynamic mixing, adsorption onto both inorganic and organic phases, complexation, precipitation, biological uptake and diffusion from bottom sediments. Leivuori (1998)(134) described in a study of trace metals in water column, that 11 m above the bottom, 77% of suspended particulate matter was originated from re-suspension of sediments. It is well known that decomposition of sinking organic matter, oxygen depletion in surface sediments and oxic/anoxic conditions play an important role in heavy metal burying in sediments and re-mobilisation processes from sediments into the water column (Sullivan and Drever, 2001)(135). Sokolowski et al. (2001)(136) showed that particulate organic matter, chlorophyll a and iron and manganese oxyhydroxides govern the behavior of trace metals in the water column. Suspended particulate matter in the water column is one of the main sources of trace metals in the marine ecosystem, and plays an important role in the transport and storage of potentially hazardous metals. The processes controlling trace metal concentrations of suspended particulate matter are generally well known, but the relative importance of the different processes is poorly quantified. In marine ecosystems, particulate organic and inorganic toxic pollutants including trace metals enter the water column via atmospheric input, river runoff, local point sources and bottom sediment re-suspension (Nguyen et al., -35- 2005)(137). Trace metals are mainly bound to fine-grained particles of mineral or organic origin as well as to iron and manganese sulphides and oxyhydroxides. Adsorbed on particulate matter, trace metals will ultimately reach the sediments where they become permanently buried or released to the water column, either as re-suspended material or in a dissolved form after geochemical transformation in the sediments (Leivuori et al., 2000)(138). The interaction of dissolved trace metals with suspended particulate matter in seawater has been suggested as the major controlling factor affecting the concentration and distribution of trace metals throughout the water column (Sherrell and Boyle, 1992)(139). In general, it is clear that vertical and horizontal variation in dissolved trace metal concentrations result from particle formation, decomposition, and transport superimposed upon physical mixing and advection processes. Due to the abundance of the suspended particulate matter and their large available surface area, it has been suggested that they control exchange with dissolved metals. Several studies have described the distribution of trace metals that are relatively abundant in suspended particulate matter (Bishop and Fleisher, 1987)(140). 2.2.2.2. Trace metals in seawater Metals occur naturally in waters due to geologic leaching and diffusion from minerals (Aguilera and Amils, 2005)(141). However, anthropogenic contamination has resulted in increased concentrations of metals, including Ag, Al, Cd, Cr, Cu, Fe, Hg, Mn, Ni, Pb, Sn, and Zn, and metalloids, including As and Se, which will hereafter be referred to as metal contaminants. Anthropogenic metal contaminants are released into all three compartments of the environment (air, water, and soil/sediment), and may cause metal concentrations to rise greatly above natural background levels. Sources of anthropogenic metal contamination in waters include industrial effluent discharges, urban runoff (e.g. roads, building roofs), sewage outfalls, leaching from municipal waste, leaching of ship antifouling coatings, mining discharges, sediment dredging activities, atmospheric desorption of emission (e.g. industrial, transport, mining, power station), and from the use of fertilizers and pesticides (Warnken et al., 2004)(142). The concentrations of metals in aquatic systems may vary greatly between locations depending on the proximity to natural and anthropogenic sources and may decrease rapidly with time and distance from a source, due to dilution and dispersion (Aguilera and Amils, 2005)(141). Spatial and temporal fluctuations in metal concentrations may also be caused by changing environmental processes/parameters, such as water flow rate, pH, salinity, turbidity, temperature, and organic matter (Baeyenes et al., 2005)(143). Metal contaminations are distinctive as they are persistent in the environment and are not removed by degradation. Instead they undergo conversions between different chemical forms. These conversions may be mediated by both biotic (micro-and macro-organsims) and abiotic (environmental) mechanisms (Hirose, 2006)(144). The distribution of metals between different chemical forms or species is referred to as metal speciation (Apte et al., 2005)(145). Chemical species may vary due to differences in isotopic composition, electronic or oxidation state, and/or molecular structure (Smith et al., 2002)(146). Metals can exist in seawater at least in 4 different forms namely in true solution, as colloidal particles, adsorbed on other colloidal particles, and as a part of living organisms. Their dispersion in seawater is affected by properties such as their volatility, tendency to form insoluble complexes with inorganic and organic compounds, and their ability to forms either soluble complexes with ions common in seawater or oxides or sulphides of low solubility (Tessier et al., 1979)(15). Trace metals dissolved in seawater are present at very low concentrations and contamination during sampling, storage and analysis often gives erroneous results (Forstner, 1979a)(147). -36- 2.2.2.3. Trace metals in marine biota Essential metals such as Cu, Zn, Fe, Co, have important biochemical functions in the organism and form either an electron donor system or function as ligands in complex enzymatic compounds (Fostner, 1979b)(148). In natural marine environment their enrichment in organisms does not exceed the level to interfere with the enzyme system functioning through their concentrations in organisms are generally higher than in seawater. However, if the ambient water or food contains high concentration of these metals, the homeostatic mechanism ceases to function and the essential trace metals act in an either actually or chronically toxic manner (Nelson and Donkinn, 1985)(149). Simkiss and Taylor (1989)(150) have discussed the pathways of metal accumulation by aquatic organisms and suggested six possible types of uptake. The most common is by a passive process of transfer from seawater down a concentration gradient into the tissues. In some cases uptake may also occur through ion pumps because of energy dependency. For many metals including Cd, Cu and Zn, the free metal ion is the most bioavailable form of the element (Goldberg et al., 1976)(151). In case of metals such as Hg and As which can be alkylated in marine environment, the biological uptake is likely to occur in the alkylated form (Turner and Southworth, 1999)(152). Autotrophic organisms probably accumulate trace metals directly from seawater. Hence, environmental parameters such as temperature, salinity, light and pH; and chemical factors such as speciation and complexation of the metal are of considerable significance. The presence of several potentially toxic trace metals can also affect their preferential uptake (FAO, 1976)(153). Variations in concentration of trace metals between species particularly in heterotrophs can be due to trophic level relationships. Though magnification of trace metals through the food web is important, there are several other causes affecting the transfer of trace metals in marine organisms. There is also evidence of seasonal variations in the trace metal content with species. The biological uptake, retention and translocation of trace metals in marine biota are related to chemical changes in storage tissues with the organism (FAO, 1976)(153). Thus, methyl-Hg assimilated through water or from metabolic conversion of Hg, accumulates in the muscle tissues of carnivore fish while the ionic Hg is preferentially transferred in their liver or spleen. Unlike Hg, Cd does not appear to concentrate in fish flesh, but accumulates in the gills, liver and gastro intestinal tract. Much of the As in marine organisms is in the form of organic As compounds (Culler and Reimer, 1989)(154). 2.2.2.4. Trace metals in marine sediments Marine sediments constitute part of the contaminants in aquatic environments. The bottom sediment serves as a reservoir for trace metals, and therefore, deserves special consideration in the planning and design of aquatic pollution research studies. Trace metals such as cadmium, mercury, lead, copper, and zinc, are regarded as serious marine pollutants because of their toxicity, tendency to be incorporated into food chains, and ability to remain in an environment for a long time (Puyate et al., 2007)(155). Sediments are known to act as the main sink for trace metals in coastal ecosystems that are impacted by anthropogenic activities. The concentration of trace metals in sediments can be influenced by variation in their texture, composition, reduction/oxidation reactions, adsorption/desorption, and physical transport or sorting in addition to anthropogenic input (Basaham and El-Sayed, 1997)(156). Potentially, toxic compounds, especially trace metals, are adsorbed on mineral or organic particles either in their organic or inorganic forms (Forstner and Wittman, 1983)(157). Studies on the distribution of trace metals in sediments and other media are of great importance in the context of environmental pollution (Howari, 2005)(158). -37- Metals in marine sediments can originate from several sources. In inshore and coastal areas the major source of metals is lithogenous associated with weathering products from the source rock. Hydrogenous formations that include precipitation products and metals adsorbed on particles formed due to physico-chemical changes in water also contribute to the metal burden in marine sediments (Riley and Chester, 1971)(31). Anthropogenically introduced metals are ultimately transferred to the bed sediments (Marchand et al., 2006)(159). Hence the environmental geochemistry requires knowledge of the naturally occurring metals in order to assess man's environmental impact. Although sediment analyses do not represent the extent of toxicity, they are useful to assess the burden of anthropogenic component over and above the lithogenic background and also in some instance, trace the sources of pollution long after input has taken place (Buccolieri et al., 2006)(160). Sediments of rivers, lakes and estuaries in a large number of locations have been contaminated by inorganic and organic materials. Among the inorganic materials, metals are frequent and important contaminants in aquatic sediments. They are involved in a number of reactions in the system including sorption and precipitation, and they are greatly influenced by redox conditions in the sediments (Allen, 1995)(161). Heavy metals are transported as either dissolved species in water or an integral part of suspended solids. They may be volatilized to the atmosphere or stored in riverbed sediments. They can remain in solution or suspension and precipitate on the bottom or can be taken up by organisms (Topcuoglu et al., 2002)(162). The heavy metal content of sediments comes from natural sources (rock weathering, soil erosion, dissolution of water-soluble salts) as well as anthropogenic sources such as municipal wastewater-treatment plants, manufacturing industries, and agricultural activities (Güven and Akıncı 2008)(44). Sediments accumulate hazardous trace elements to levels many times higher than water column concentrations, causing a serious problem due to their toxicity and their ability to accumulate in biota (Morillo et al., 2007)(163). The concentrations of trace metals present in bottom sediments typically exceed the concentrations in the overlying water by between three and five orders or magnitude. In such situations, the contaminated sediments can represent a significant, long term source of trace metals to the overlying water column and the aquatic ecosystem. The sediment particles themselves can also represent a bioavailable source of trace metals, thereby causing direct toxicity to benthic biota or providing a pathway for trace metal entry into aquatic food chains (Burton, 2005)(55). Sediments are heterogeneous assemblages of minerals and organic components and therefore exhibit a wide degree of variability in terms of composition and physico-chemical properties (Berner, 1981)(164). Trace metals may be distributed within a range of geochemical solid phases, as well as being dissolved in the associated sediment pore waters (Hong et al., 1995)(165). Consideration of the partitioning of trace metals between pore water and the various solid phases in natural sediments provides a far more realistic and accurate description of environmental risk compared to total metal concentrations (Berry et al., 1996)(166). Trace metal distribution amongst the various sediment phases is controlled by a range of sorption-desorption reactions, which include precipitation-dissolution of mineral species and adsorption-desorption on mineral and organic surfaces (Tessier et al., 1994)(167). When environmental conditions change (pH, sediment redox potential, organic matter, etc.); some of the sediment bound metals can remobilize and be released back into the water, where they can have adverse effects on living organisms (Song et al., 2009)(168). Metals are associated with different phases (crystalline minerals, carbonates, hydrous metal oxides, organic substances, etc.) that determine their behavior in the environment, mobility, bioavailability, and toxicity (Usero et al., 1998)(169). The most crucial property of metal ions is that they are bioavailable and not biodegradable in the environment and that their uptake by -38- benthic organisms depends largely on their mobility, total concentration and chemical forms (Morillo et al., 2007)(163). Thus, to assess the environmental impact of polluted sediments, the measurement of total trace metals is not enough (Kersten and Forstner, 1987)(170). 2.2.3. The importance of studying sediments Sediment is the loose sand, clay, silt and other soil particles that settle at the bottom of body of water (Davies and Abowei, 2009)(171). The erosion of bedrock and soils leads to accumulation of sediments of past or on-going natural and anthropogenic processes and components. Data from sediments can provide information on the impact of distant human activity on the wider ecosystem. The composition of sediment sequences provides the best natural archives of recent environmental changes (Olubunmi, 2010)(172). Sediment is a habitat and major nutrient source for aquatic organisms. Sediment analysis is important in evaluating qualities of total ecosystem of a body of water in addition to water sample analysis practiced for many years because it reflects the long term quality situation independent of the current inputs (Adeyemo et al., 2008)(173) and it is the ultimate sink of contaminants in the aquatic system (Davies and Abowei, 2009)(171). Monitoring of the contamination of soil and sediment with trace metals is of interest due to their influence on ground water and surface water and also on plants, animals and humans (Suciu et al., 2008)(174). Accumulation of trace metals occur in upper sediment in aquatic environment by biological and geochemical mechanisms and become toxic to sediment-dwelling organisms and fish, resulting in death, reduced growth, or in impaired reproduction and lower species diversity (Praveena et al., 2007)(175). Trace metals also occur naturally in rock forming minerals and ore minerals; hence they can reach the environment from natural processes (Akinmosin et al., 2009)(176). The occurrence of metals in aquatic ecosystems in excess of natural background loads has become a problem of increasing concern. Trace metals in environment may accumulate to toxic levels without visible signs. This may occur naturally from normal geological phenomenon such as ore formation, weathering of rocks and leaching or due to increased population, urbanization, industrial activities, agricultural practices, exploration and exploitation of natural resources (Ajayi and Osibanjo, 1981)(177). After the Industrial Revolution, point sources from mining, municipalities, industries and non-point sources from both agriculture and urban storm water runoff have accumulated in water resources, settling to the bottom areas of water bodies. Contaminated sediments pose a risk to the environment in two basic mechanisms: (1) ecological risk to aquatic and piscivorous animals and (2) toxic risks on terrestrial habitat when contaminated area is dredged and placed on land (Khan et al., 2000)(178). The study of marine sediments provides useful information in marine, environmental and geochemical research about pollution of the marine environment (Calace et al., 2005)(179). Urban developments and industrial activities contribute to the introduction of significant amounts of contaminants (among them trace metals) into the marine environment and affect directly the coastal systems where they are often deposited (Dassenakis et al., 2003)(180). The growing apprehension about the potential effects of sediment toxicity poses to marine fauna and flora and the risk posed to the environment by the contaminants accumulated by the sediments have aroused an increase in research interests in marine sediments (Calace et al., 2005)(179). Study of marine sediments represents a useful tool for determining the actual state of environmental pollution and for understanding the origin and mechanism of the phenomena. Sediments could be regarded as a historical reflection to changes occurring in the overlying -39- water system and can be used as good indicators for metals in any study area. Meanwhile, sediments are major repository of trace metals in the coastal marine environment (Salomonos and Forstner, 1984)(181) and sometimes become a major potential source of trace metals, which can be eventually returned to the biosphere (Saad and Badr, 2003)(182). Sediment is a matrix of materials, made up of detritus, inorganic and organic particles, and is relatively heterogeneous in terms of its physical, chemical and biological characteristics (Sarkar et al., 2004)(183) and consist of a wide range of particle sizes, including gravels, sand, silt and clay (Fergusson, 1990)(3). Sediments are well known to act as a major sink for many of the more persistent organic and inorganic chemicals introduced into the aquatic environment by atmospheric deposition, erosion of the geological matrix, or from anthropogenic sources (such as industrial effluents, mining wastes, etc.) (Calace et al., 2005)(179). Sediments also act as potential sources of pollution for the surrounding water and benthic flora and fauna by releasing sorbed contaminants back to the overlying water column should remobilization occur through any disturbance (Adamo et al., 2005)(184). Contaminants of major concern found in the marine coastal environment include trace metals, persistent organic pollutants (POPs), oils (hydrocarbons), nutrients and radioactive substances (UNEP, 1999)(185). Contamination of the environment, and in particular the marine environment by trace metals has received considerable attention as evidenced by an increase of publications appearing in the literature (Chandra, 2002)(186). Environmental contamination from trace metals is of major concern because they show behavior similar to those of persistent toxic chemicals. Metals are partitioned amongst soluble phases, suspended and bottom sediments and biota in aquatic systems (Gangaiya, 1994)(187). Sediments play a useful role in the assessment of trace metal contamination (Gangaiya et al., 2001)(187). The partitioning behavior of trace metals is such that they tend to accumulate in sediments to levels that are several orders of magnitude higher than in the surrounding water (Denton et al., 1997)(48). Further, their deposition rates are generally related to their rates of input in the surrounding water (Forstner, 1990)(188). The analysis of trace metals in the sediments permits detection of contaminants that may be either absent or in low concentrations in the water column, and their distribution in coastal sediments provides a record of the spatial and temporal history of pollution in a particular area or ecosystem (Binning and Baird, 2001)(189). Therefore, the chemical analysis of sediments, is very important from the environmental pollution point of view because sediment concentrates metals from aquatic systems, and represents an appropriate medium in monitoring of environmental pollution (Sarkar et al., 2004)(183). Sediments are essential and integral parts of water systems. They provide the substrate for organisms and through interaction with the overlying waters play an essential role in the aquatic ecosystem (Burden et al., 2002)(190). They are increasingly recognized as both a carrier and a possible source of contaminants in aquatic systems, and these materials may also affect groundwater quality and agricultural products when disposed on land. Contaminants are not necessarily fixed permanently by the sediment, but may be recycled via biological and chemical agents both within the sedimentary compartment and the water column. Bioaccumulation and food chain transfer may be strongly affected by sedimentassociated proportions of pollutants. Benthic organisms, in particular, have direct contact with sediment, and the contaminant level in the sediment may have greater impact on their survival than do aqueous concentrations (Malins et al., 1984)(191). -40- They are also an important repository for metal pollutants that enter the sea. Sediments provide habitats for many aquatic organisms and also a major repository for many of the more persistent chemicals that are introduced into surface waters. In the aquatic environment, most anthropogenic chemicals and waste materials including toxic organic and inorganic chemicals eventually accumulate in sediments. In aquatic environments, many trace metals are transported predominantly in association with particulate matter, and consequently, a high concentration of trace metals is often detected in sediments in many industrialized harbors and coastal regions around the world (Wang et al., 2007)(192). Contaminated sediments are crucial indicators of pollution in aquatic environments and can be defined as soils, sand, organic matter, or minerals accumulated at the bottom of a water body (USEPA, 1998)(193). Contaminants contained in sediments can be released to overlying waters and sediments can be important sources of contaminants in waters (Güven and Akinci, 2008)(44). Many of the sediments in seas, rivers, lakes, and oceans have been contaminated by pollutants. These pollutants are directly discharged by industrial plants and municipal sewage treatment plants, others come from polluted runoff in urban and agricultural areas, and some are the result of historical contamination (Begum, et al., 2009)(194). Contaminated sediments can threaten creatures in the marine environment. Some kinds of toxic sediments kill benthic organisms, reducing the food available to larger animals such as fish. Some contaminants in the sediment are taken up by benthic organisms in a process called bioaccumulation. When larger animals feed on these contaminated organisms, the toxins are taken into their bodies, moving up the food chain in increasing concentrations in a process known as bio-magnification. As a result, fish and shellfish, waterfowl, and freshwater and marine mammals may accumulate hazardous concentrations of toxic chemicals (Begum et al., 2009)(194). Contaminated sediments do not always remain at the bottom of a water body. Anything that stirs up the water, such as dredging, can re-suspend sediments. Re-suspension may mean that all of the animals in the water, and not just the bottom-dwelling organisms, will be directly exposed to toxic contaminants. Different aquatic organisms often respond to external contamination in different ways, where the quantity and form of the element in water, sediment, or food will determine the degree of Accumulation (Begum et al., 2008)(195). Many dangerous chemical elements, if released into the environment, accumulate in the soil and sediments of water bodies. Under certain conditions, chemical elements accumulated in the silt and bottom sediments of water bodies can migrate back into the water. Silt can become a secondary source of trace metal pollution (Begum et al., 2009)(194). 2.2.4 Effects of Trace Metals Contamination in Sediments 2.2.4.1. Metal polluted Sediments Trace metals are preferentially transferred from the dissolved to the particulate phase (Gangaiya et al., 2001)(196) and this results in the elevation of metal concentrations in estuaries and marine sediments. Therefore, concentrations often exceed those in overlying water by several orders of magnitude (Langston, 2000)(197). Because sediments can accumulate trace metals, concentrations can be high and ultimately become potentially toxic (Williamson et al., 2003)(198). Exposure and uptake of even a small fraction of sediment-bound metal by organisms could have significant toxicological significance, in particular where conditions favor bioavailability. In addition, increased metal concentrations in pore water may contribute significantly to sediment toxicity (Langston, 2000)(197). Evidence of fatal effects of metal-polluted sediments can be determined by the absence of sensitive species or by the development of resistance mechanisms and adaptation -41- in tolerant forms such like efficient excretory features in organisms (Langston, 2000)(197). Binning and Baird (2001)(189) reported that the density and diversity of nematode communities in the Swaetkops River estuary, South Africa, are influenced by the degree of trace metal contamination in the sediments. Many of the metals have no known biological function in the marine environment, but can act synergistically with other chemical species to increase toxicity (Binning and Baird, 2001)(189). The potential impacts of accumulating levels of trace metals can be estimated by comparing the concentrations of contaminants of interest present in sediments with sediment quality guidelines (SQGs) (Williamson et al., 2003)(198). The Sediment Quality Guidelines (SQGs) have been derived from large databases, which correlate the incidence of adverse biological effects with the concentrations of contaminants in sediments (Long et al., 1995)(199) and are used in the evaluation of sediment contamination and potential ecotoxicological effects (Casado-Martinez et al., 2005)(200). One of the most widely used SQGs for estuarine and marine environments, which will be applied in this study as well, is a set of effects-range guidelines developed by the National Oceanic and Atmospheric Administration (NOAA) (McCready et al., 2006)(201) in the U.S. (Long et al., 1995)(199). There are two levels of risks considered under this SQG – effects low range (ERL) and effects range-moderate (ERM) (Guerra-Garcia and Garcia-Gomez, 2005)(202). Concentrations below the ERL value are rarely associated with biological effects while concentrations above the ERL but below the ERM indicate a possible range in which effects would occur occasionally. Concentrations above ERM are associated with frequent adverse ecological effects on the benthic communities (Guerra-Garcia and Garcia-Gomez, 2005)(202). 2.2.4.2. Ecology Given that metal concentrations in sediment are normally higher than those in the overlying water, macrophytes, at the primary production level, rooted in these enriched sediments tend to have higher concentrations than the sediment (Mance, 1987)(102). This is due to the uptake of metals not just only from the sediment via the roots but also from the surrounding water (Redfern, 2006)(203). The effect of trace metal contaminants in the sediment on benthic organisms can be either acute or chronic (cumulative) (Binning and Baird, 2001)(189). No matter whether metals are essential or not, all trace metals form an important group of enzyme inhibitors when natural concentrations are exceeded. Therefore, organisms living in or adjacent to metal contaminated sediments may suffer toxic effects that can be fatal in highly contaminated situations to relative abnormal metabolic adjustments at the sub-lethal level (Denton et al., 2001)(66). In addition, metal enrichment in estuaries and coastal environments is a major concern as heavy metals have the ability to bio-accumulate in the tissues of various biota, and can ultimately affect the distribution and density of benthic organisms, as well as the composition and diversity of infaunal communities (Binning and Baird, 2001)(189). A wide range of criteria to assess the impact of metals on marine organisms have been developed during the last few years and consequently, effects are now recognized at a much lower levels than in earlier LC50 studies (Langston, 2000)(197). Growth, reproduction, and recruitment are usually the processes most susceptible to metal stress (Redfern, 2006)(203). The toxicity of a trace element to an organism depends on the metal chemical species, its concentration and the organism being affected (Sedgwick, 2005)(34). As for the organism, toxic effects occur when excretory, metabolic, storage, and detoxicification mechanisms are no longer have the capacity to match uptake rates. This capacity may vary between phyla, species, populations, even individuals and can also depend on the stage in the life history of the organism (Langston, 2000)(197). -42- 2.2.4.3. Human health The consumption of marine food is the principal path to human exposure to trace metals. Effects on humans can be observed after either a one-off exposure to a large nonlethal dose (acute) or after repeated exposure to lower doses (chronic) (Sedgwick, 2005)(34). Trace metal contamination has become a subject of public interest because humans have been harmed by metal contamination (Chandra, 2002)(186). One of the well-documented incidents of metal contamination that attracted greater public interest was an industrial mercury contamination on Minimata Bay in Japan caused by severe health effects in consumers of fish and shellfish from the area and led to the identification of methyl mercury as an extremely toxic compound (Chandra, 2002)(186). Methyl mercury can bio-accumulate in the food chain and its accumulation in some fish represents a risk to those people who consume a large proportion of fish in their diet (Williamson et al., 2003)(198). 2.2.5. Factors affecting trace metal distribution, concentration and fate in sediments Enrichment of trace metals from anthropogenic sources in the estuarine and marine environments has become a serious human health and environmental concern. Once trace metals are deposited in sediments, they undergo a series of physical, biological and chemical processes. Trace metals occur in a number of different forms, mainly in the dissolved and in the solid state (adsorbed onto surfaces of clays, element oxides, organic material, coprecipitated with sediment phases and incorporated into organic matter). The highest proportion is usually in the solid phase. How an element is bound in sediment determines the biologically active fraction and its fate and cycling (Erdogan, 2009)(87). Understanding the processes affecting trace metals concentration and their fate in sediments is important in gauging appropriate designs for sampling and monitoring programs and planning for appropriate remediation options (Williamson and Wilcock, 1994)(204). It has been validated that each environmental factor presents unique influence on metals distribution in sediment. The influences of some factors, such as pH, (Oxidation reduction potential) ORP and (Organic matter) OM are more crucial than the others. Only a slight variation of them, the distributions of metals would be producing some significant variations. Correspondingly, some other factors (e.g. salinity, temperature) can only alter metals distribution to a less extent (Peng et al., 2009)(205). The relatively important factors are introduced in the following: 2.2.5.1. Trace metals input into sediment Increased inputs of metals in such forms available for association with sediments ultimately result in increases in metal concentrations in sediments (Luoma, 2000)(206). Metal enrichment in the sediments is usually located close to past and present sources of pollution (Williamson and Wilcock, 1994)(204) and in particular the sheltered environments where discharge is restricted (Williamson et al., 1992)(207). This is supported by numerous studies which have demonstrated that metal inputs from human activities are reflected by metal concentrations in sediments (Luoma, 2000)(206). -43- Simply, concentrations drop with distance away from the source of input as determined by the physical processes that dilute and redistribute the particles with which metals associate such like the dilution with less contaminated sediments (Luoma, 2000)(206). However, the rate of decline in concentration with distance from sources of pollution is extremely variable (Williamson and Wilcock, 1994)(204). 2.2.5.2. The influence of grain size Metal concentrations in marine and estuarine sediments are determined not only by metal inputs but also by sediment characteristics. Grain size distribution has been recognized to affect trace metal concentrations in estuarine and marine sediments (Luoma, 2000)(206). Generally, trace metals are mainly concentrated in the silt/clay sediment fraction, consisting of particles with a grain size <0.063 mm (Krumgalz et al., 1992)(208). The enrichment of the silt/clay fraction by anthropogenic trace metals is due to the large specific area of this fraction and to the strong adsorptive properties of clay minerals (Krumgalz et al., 1992)(208). Fine grained sediment of this particular fraction has a high absorption potential because the sediment has a large surface area to ratio, and contain large amounts of interstitial water (Loomb, 2001)(209). The feature of clay that is of significance regarding the trace metals is their ability to absorb metal ions by their outer sheath of hydroxyl groups (Fergusson, 1990)(3). The surface of clays may be also negatively charged which is crucial in providing potential absorption sites for metal ions (Williamson et al., 1992)(207). Clay minerals also have a higher surface area to volume ratio and can absorb material into their lattice framework (Loomb, 2001)(209). Luoma (2000)(206), however, found that the relationship of metal concentration and grain size distribution is sometimes complicated. For example, silt/clay sizes particles in estuarine and marine sediments are usually aggregates and particle aggregates can complicate the relationship of metal concentration and surface area. Another potential factor that can affect this relationship is the physical and chemical processes that may affect the degree of accumulation of metal-reactive sediment components on the sediment surface (e.g., movement of water across a redox boundary may facilitate accumulation of iron and manganese oxides) (Luoma, 2000)(206). The accumulation of trace metals in sediment is controlled by the granular compositions of sediment. Grain size affects the surface area, settling velocity and deposition rate of suspended solids in the water column, as well as the degree of chemical partitioning onto the sediment. Metals are generally found to be associated largely with the fine grain fraction of sediment that has been traditionally used to study the pollution of trace metals in sediments. However, trace metals sometimes accumulate in the coarse grain fraction of sediment (Qian et al., 1996)(210). Fine-grained bottom sediments tend to accumulate contaminants due to their sorptive nature, and thus act as an important reservoir by reducing the toxicity potential to aquatic organisms (Fan et al., 2002)(211). Changes in sediment chemistry, due to seabed disturbance, can result in contaminant remobilization. Subsequently, exposure to a different chemical environment could result in desorption and transformation of contaminants into more bioavailable or toxic chemical forms (Sturm et al., 2002)(212). Sediments are able to store and accumulate metals to some extent, due to their adsorption capacity. Sediments exist as complex and dynamic mixtures of mineral particles, particular organic material (detritus) and microbes. The flocculated chemicals and contaminants in sediments may be associated with any of these sediment fractions. The grain size of sediments affects the accumulation of metals through both their chemical and physical properties. The fine-grained sediments tend to show higher concentration of metals, due to -44- their higher surface area. Fine sediments are also often associated with the anoxic nature, higher concentration of sulfide, as well as elevated metals and organic contaminants (Tabata et al., 2009)(213). 2.2.5.3. Sediment composition One of the most important sediment characteristics is the concentration of sediment components. The concentrations of the important metal-reactive components of sediments (Fe and Mn hydrous oxides, sulphides and organic materials) can vary among estuarine and marine environments (Luoma, 2000)(206) and are found to increase as sediment textures become finer (Williamson and Wilcock, 1994)(204). The sediment components (particulate matter) contain many phases that strongly adsorb metals such as amorphous iron oxides, manganese oxides, and polar organic matter (humic acid, carbohydrates, proteinous material) (Williamson et al., 2003)(198). The nature of Fe oxides, organic materials, or Mn oxides will determine site densities for sediment components; and the relative concentrations of Fe, Mn and organic materials will determine aggregate differences in binding site density or binding intensity (Luoma, 2000)(206). Amorphous iron hydrous oxide (FeOOH) has a large surface area per unit weight. It is abundant and it may be an important medium for trace metal adsorption. Concentrations do not change greatly with depth or redox conditions, though are strongly dependent on sediment texture (Williamson and Wilcock, 1994)(204). Amorphous manganese oxide (MnOOH) concentration is lower than iron oxides, though its rapid cycling between reduced and oxidized forms, and between sediments and water mean that it is important in trace metal mobilization from sediments (Williamson and Wilcock, 1994)(204). Generally organic matter content of sediments increase as the sediment texture becomes finer (Denton et al., 2001)(66). The presence of organic matter can potentially increase metal concentrations in sediment by adsorption of metals from surrounding environment onto organic material (Loomb, 2001)(209). Also dead organisms in sediments may carry the trace metals with them, either taken in by the organism while alive or sorbed on to the animal before or after death (Fergusson, 1990)(3) and this contribute directly to the metal levels in the sediments. Organic compounds containing metal ions may also be sorbed onto Fe-Mn oxides. Organic materials can affect metal species solubilization by complexing the metal ions, but they can also take metal ions out from the solution and contribute to the sediments. Decomposition of organic material produces organic ligands that may extract metals from the sediments which can effectively mobilize metals by increasing their concentration in the water (Taulis, 2005)(214). Interestingly, the IrvingWilliams series of increasing stability of metal complexes, is the same order as increasing mobilization (Fergusson, 1990)(3); Mn < Fe < Co < Ni < Cu > Zn. Therefore, the subsequent fate of metal-reactive components of sediment (Fe and Mn hydrous oxides, and organic materials) will determine the fate of the associated heavy metals (Williamson et al., 2003)(198). 2.2.5.4. The influence of pH values The pH is a key parameter controlling trace metal transfer behavior in sediment. Normally, with pH decreasing in sediment, the competition between H and the dissolved metals for ligands (e.g. OH-,CO32-,SO42-,Cl-,S2- and phosphates) becomes more and more significant. It subsequently decreases the adsorption abilities and bioavailability of the metals, and then increases the mobility of trace metal. Sometimes, only with a few lower of pH units, the fixation percentage of trace metals on sediment particles may range from almost a 100% to none (Gundersen and Steinnes, 2003)(215). In sediment, due to the OM degradation and the acid volatile sulfide oxidation, the pH of sediment usually decreases from the neutral in the initial to acid, sometimes even decreasing to pH 1.2, which often results in some metals being released into water again even under stable water conditions (Uta and Jens, 2006)(216). In -45- sediment, there exists a limit pH controlling heavy metal mobility. And the trace metal would be released only as they reaching such pH value. For different metals, this limit pH is different correspondingly, which can be found as the following: The limit pH values of different metals in sediment Metal species Zn Cd Ni As Cu Pb Al Fe pH limit 6.0-6.5 6.0 5.0-6.0 5.5-6.0 4.5 4.0 2.5 2.5 Therefore, under similar pH value, the potential mobility of heavy metals in sediment is different significantly. For example, when pH was controlled at 4.0, the potential mobility of metal decrease as follows: Zn>Cd>Ni>As>Cu>Pb (Valerie et al., 2004)(217). 2.2.5.5. Influence of organic matter Organic compound in sediment, frequently existing in considerable amounts in particle form, play an important role in trace metal transformation. For example, in the sediment of some rivers or lakes, the trace metal bound to organic matter (OM) generally takes up the largest fraction. Additionally, in sediment, the solubility of organic matters usually directly determines the mobility of trace metals. Normally, the complexation of metal ions with insoluble organic compounds can strongly lower their mobility, whereas the formation of soluble metal complexes with dissolved organic compounds would enhance their mobility (Sekaly et al., 1999)(218). In natural rivers or lakes, OM is mainly composed of humic and fulvic substances. The complexation reaction between trace metals and organic complexants is usually recognized as the most important reaction pathway, due to this reaction determining, to a large extent, the speciation and bioavailability of metal, and then influencing the mobility of trace metal in natural water environment. However, in severely polluted river, due to the complexity of organic matter, the reaction types between organic complexes and metals are difficult to predict. In most conditions, precipitation, coprecipitation or flocculation usually plays the most important role in heavy metal fixation (Peng et al., 2009)(205). Total organic carbon added to the sediments, primarily through the decomposition of plant and animal matters, can directly binds and/or absorbs trace metals and also contains trace metals accumulated by plants that have been exposed to contaminated sediment during their life time. Nonetheless, high percentages of organic matter and /or small grains in sediments, reduce the metals availability, and undoubtedly play a major role in controlling metals' concentration in the pore water (Tabata et al., 2009)(213). 2.2.5.6. The influence of Oxidation reduction potential It is generally accepted that sediment oxidation reduction potential (ORP) is also a most important factors controlling heavy metal mobility (Salomons and Stigliani, 1995)(219). In anaerobic sediment, Acid volatile sulfide (AVS), a key component controlling the activities of some divalent cationic metals, usually present naturally (Di-Toro et al., 1990)(22). Initially, the majority of AVS contained in the anaerobic sediment is bound to iron as solid iron -46- monosulfide (FeS), crystalline mackinawite (FeS), pyrrhotite (FeS), greigite (Fe3S4),or exits As free sulfides. However, if divalent metals, such as cadmium, copper, chromium, lead or zinc are present, the iron in iron-sulfide are displaced and one of these heavy metals rapidly bind to AVS with stronger affinity (Hansen et al., 1996)(220). Finally, in those sediment contaminated, the metal bound with sulfide usually takes up a rather high proportion (Peng et al., 2009)(205). When ORP in sediment increases, the oxidization rate of metal sulfides and the degradation rate of organic compounds will increase correspondingly. Both can accelerate the release of the adsorbed/complexing heavy metal (Calmano et al., 1993)(221). The reaction can be expressed as: MS2 + (15/4)O2 +(7/2)H2O = M(OH)3 +2SO42 - +4H+. The release of H+ ions into porewater would decrease the pH of sediment and then cause a secondary release of heavy metals. Part of this released material will be re-adsorbed, especially onto the more labile binding fractions. For example, with ORP in sediment increase, the Cd bound to organic sulfide, a stable metal forms, would decrease from 65% to 30% and form a more mobile form (Tneofanis et al., 2001)(222). Accordingly, with the annual variations of ORP in sediment, the trace metal presents seasonal release and fixation. These phenomena are very significant in some seasonally flooding rivers. For example, in Mulde reservoir, approximately 18t of Zn can be released from sediment into water only due to the sediment being disturbed and oxidized in flooding, which led to a significant increase of Zn concentration in water (Tneofanis et al., 2001)(222). Therefore, in the dredging process of river or lake, for decreasing the release of metal from sediment, oxidation of sediment should be avoided (Peng et al., 2009)(205). Biological oxidation of metabolisable forms of organic carbon has been recognized as the most important factor in early diagenesis (Williamson and Wilcock, 1994)(204). In the surface sediments, organic matter is decomposed by organisms in the presence of oxygen. In finer sediments such as clay, with the exception of coarse sediments and other high-energy areas where there is rapid advection of oxygenated water, this decomposition uses up oxygen in the sediment quickly. The decomposition occurs faster than the rate of diffusion of oxygen into the sediments and, as a result, most sediments are anaerobic just below the surface (Williamson et al., 2003)(198). The decomposition of organic matter proceeds under anoxic conditions using alternative electron acceptors to oxygen, such as nitrate, manganese and iron oxides, and sulphate to oxidize (metabolise) organic carbon (Williamson et al., 2003)(198). This oxidation, together with the resulting anoxic conditions, produces large changes to the form of iron, manganese and sulphur, which are important in ‘binding’ trace metals in sediment and releasing them to the overlaying water (Williamson and Wilcock, 1994)(204). For instance, when sulphate is used, sulphide is produced and heavy metals react with the sulphides and produce soluble precipitates (Williamson et al., 2003)(198). Sulphide also reacts with Fe to form black ferrous sulphide and pyrites (FeS2) to give the subsurface sediments their characteristic black and grey color. Mercury is different. While it undergoes similar reactions to other metals, microbiota changes a proportion to organo-mercury (methylmercury) a toxic compound that has the ability to bio-accumulate in the food chain (Williamson et al., 2003)(198). In sediments with high inputs of organic matter, reactions are concentrated close to the sediment-water interface. In addition, iron, manganese and sulphur in many oxidized and reduced forms can react with each other abiotically. All these reactions contribute to the complex sediment chemistry (Williamson and Wilcock, 1994)(204). -47- 2.2.5.7. Adsorption / desorption reactions The release of metals from oxic sediments can happen as the salinities increase or reduction/oxidation condition changes due to the high ionic strength of seawater and potential competition for binding sites with Ca and Mg (Luoma, 2000)(206). The flux of oxygen from the water to the sediments controlled the reaction at the interface; hence the depletion of oxygen consequently limits the release of the metals into the water. The extent of losing the metals from oxic sediments can be reduced by readsorption to precipitating Fe and Mn oxides (Luoma, 2000)(206). Metal removal from estuarine sediments can occur due to desorption of metals from particulates to solution when freshwater and seawater mix and this has been demonstrated in the laboratory experiments. However, readsorption also takes place at the freshwater/seawater interface in estuaries due to the formation of new particles, increased turbidity, increased pH and the occurrence of complex recirculation patterns (Luoma, 2000)(206). The above processes are not only fueled by the changing redox environment and pH but also by the metabolism of carbon organic matter, changing environmental conditions brought about by bioturbation (muds and sands) or waves (sand) and irrigating the sediment (Williamson and Wilcock, 1994)(204). The following diagram illustrates how the pollutants move within the hydrosphere. -48- Movement of pollutants in the hydrosphere (Fergussion, 1990)(3) 2.2.5.8. Physical transport Sediment type and dynamics are known to affect contaminant concentration and fate (Williamson and Wilcock, 1994)(204). In coastal environments with low hydrodynamic energy, fine particulates tend to be trapped, while in areas where hydrodynamic energy is high, fine particulates are ‘moved on’ (Williamson et al., 2003)(198). There are 3 main zones that can be distinguished based on three types of processes (Williamson et al., 2003)(198). i) Areas of accumulation (deposition). This is where fine materials are continuously being deposited. Wave and current energies are very low in this area; ii) Areas of transportation. This is where fine materials are deposited discontinuously, i.e. periods of accumulation are interrupted by periods of periods of remobilization (generally of short duration and associated with storms); and iii) Areas of erosion. This is where there is little deposition of fine materials. Wave and/or current energies are high in this area. Bare rock, gravels and sand characterize areas of erosion while sediments in areas of transport are diverse; ranging from muds to sands. The deposits within areas of accumulation are typically muddy, with a high water and organic matter content (Williamson and Wilcock, 1994)(204). For most metals, the intermediate fate is the deposition area where the finest sediments generally accumulate (Williamson et al., 2003)(198). These areas tend to be sheltered estuaries and embayments, and deeper water offshore. The ultimate fate of trace metals is burial given that metals do not break down. When buried, trace metals become immobilized as insoluble sulphide precipitates due to the decomposition of organic material (dead animals, plant material) (Williamson et al., 2003)(198). 2.2.5.9. Bioturbation Movement of pollutants in the hydrosphere -49- Numerous studies have suggested that bioturbation strongly affects the physical, chemical and biological properties of sediments (Williamson and Wilcock, 1994)(204). Biological mixing is more important in muddy sediments than sandy sediments, where strong physical processes occur. There are two groups of animals based on the magnitude of sediment disturbance; i) large individual predators, such as rays and crabs, may shift large amount of sediment when searching for food, and ii) smaller animals such as worms and gastropods. The latter burrow and ingest sediment, shift only small amounts of sediments, but their high population densities make them important in sediment turnover (Williamson and Wilcock, 1994)(204). Bioturbation has a major impact on the chemistry of muddy sediments. Oxygen penetration in unbioturbated sediments is highly restricted, and the redox boundary occurs a few millimeter below the surface (Williamson and Wilcock, 1994)(204). Marine organisms, such as polychaetes and crabs, create extensive ‘honeycombs’ in mud flats up to 60 cm in depths allowing oxygen to be transported deep within the sediments via burrows (Williamson and Wilcock, 1994)(204). These ‘honeycombs’, in turn, provide low tide irrigation of burrow water, which maintains oxic conditions when tidal flats are submerged (thus facilitating the exchange of solutes between sediments and water) (Redfern, 2006)(203). Burrowing organisms also can alter the levels and the speciation of trace metals in sediments by affecting the sediment stratigraphy to become blurred, particle size altered, pore spaces and pH changed (Fergusson, 1990)(3). Consequently, metal concentrations do not appear to change rapidly with depth (Williamson and Wilcock, 1994)(204). The organisms may also bio-accumulate trace metals and remove them from the sediment profile (Fergusson, 1990)(3) hence decreasing the metal concentrations in the sediments (Redfern, 2006)(203). 2.2.5.10. The influence of other species Except pH, OM and ORP, some other factors, such as temperature, salinity, metal species and retention time, can also affect the distributions of trace metal in sediment. For example, due to the differences of cation exchange capacity among different metal, their mobility capacity varies correspondingly, and usually ranges as follows: Cs>Zn>Cd>Fe>Ag>Co>Mn (Emile and Jonathan, 1998)(223); with temperature increasing, the adsorption content of trace metal on sediment often decreases gradually; with salinity in pore water increasing, the total adsorption content of heavy metal would decrease ascribed to the competition among heavy metal and some other cations (Garnier et al., 2006)(224). Additionally, long time kinetic adsorption–desorption experiments also show that the metal freshly associated with particles presents less stable and higher potential bioavailability than those associated for a long time (Peng et al., 2009)(205). 2.2.6. Analysis of trace metals in sediments Metals in sediments are generally considered to be present in the following forms: water soluble, exchangeable, carbonate bound, bound to hydrous metal oxides (as Fe, Mn), bound to organic matter and sulfides, and finally in the crystal lattice of the different minerals composing marine sediments. Many terms have been used to describe metals bound to sediments. Metals that are loosely bound to sediments and can be released back to the water column are known as labile metals. Another name used to describe this fraction is non-detrital metals as they are bound to non-detrital particles (Loring et al., 1985)(225). One more term used to describe this portion is non-residual metals. The other portion that is found inside the lattice of sedimentary minerals is known as residual metals, detrital or non-labile metals, as they can’t move back to the overlying water column (Khairy, 2008)(226). -50- Concentrations of total metals in sediments can be obtained by the digestion of the sediment sample in a mixture of acids to release all metals bound to the different fractions of the sediments. But the determination of total metals will not be useful in environmental pollution assessment studies in a given area as it implies that all forms of a given metal have an equal impact on the environment. Such assumption is clearly untenable (Tessier et al., 1979)(15). Also, the use of the total concentration of a trace metal in sediment as a measure of its toxicity and its ability to bioaccumulate is problematic because different sediments exhibit different degrees of bioavailability for the same total quality of metal. These differences have been reconciled by relating organism toxic response (mortality) to the contaminant concentration in the sediment interstitial water (Di-Toro et al., 1990)(22). AVS is one of the major chemical components that control the activities and availability of metals in the interstitial waters of sediments (Prica et al., 2008)(227). A large reservoir of sulfide exists as iron sulfide in anoxic sediment. Sulfide reacts with several divalent transition metal cations (cadmium, copper, mercury, nickel, lead and zinc) and predominantly monovalent silver to form highly insoluble compounds that are not bioavailable. It follows in theory, and with verification (Di-Toro et al., 1990)(22), that divalent transition metals do not begin to cause toxicity in anoxic sediment until the reservoir of sulfide is used up (i.e. the molar concentration of metals exceeds the molar concentration of sulfide), typically at relatively high dry weight metal concentrations. This observation has led to a laboratory measurement technique for calculating the difference between simultaneously extracted metal (SEM) concentration and acid volatile sulfide (AVS) concentration from field samples to determine potential toxicity (Ankley et al., 1991)(228). The presence of AVS in sediments provides a mechanism for partitioning metals from the pore water to solid phase, reducing the potential solubility and bioavailability (Ankely et al., 1996)(23). Methods for measuring metals in each fraction of the sediment are known as sequential extraction techniques. The results obtained by the sequential extraction technique can provide a wider and deeper insight into the metal pollution in the environment. However, the analytical procedure of the sequential extraction techniques is tedious and time consuming. It is not an effective method, which can be easily applied in environmental investigations (Chen et al., 1989)(229). Numerous extraction schemes for soils and sediments have been discussed in literature (Tessier et al. 1979; Sposito et al. 1982; Wette et al. 1983; Clevenger, 1990; Howard and Vandenbrink, 1999)(15, 230-233). The procedure of Tessier et al. (1979)(15) is one of the thoroughly researched and widely used procedures to evaluate the possible chemical associations of metals in sediments and soils. Another two important schemes of sequential extraction are those of Kersten and Forstner, (1986)(234) and the Bureau Communautaire de Reference (BCR) sequential extraction method (Ure et al. 1993)(16). The sequential extraction procedure is also often used to assess the possible chemical partitioning of trace metals, particularly on the mobility and bioavailability of metals in sediments (Li et al., 2001)(235). A comparison of sequential extraction procedure and SEM results may provide new insights for interpreting the SEM/AVS measurement (Fang et al., 2005)(26). 2.2.6.1. Acid Volatile Sulphide (AVS) Trace metals in the overlying water can be adsorbed by sediments through the main metal binding phases of total organic carbon (TOC), and acid volatile sulphide (AVS) (Song and Muller, 1999)(236). The organic matter accumulated in sediments is decomposed to -51- sulfide in reduced environment. Therefore, the presence of sulfide may be an indication of high TOC concentration (Griethuysen et al., 2002)(237). AVS is a reactive pool of solid-phase sulfide that is available to bind metals and render that portion unavailable and nontoxic to biota (Simpson et al., 2000)(238). In anoxic sediments, the availability of divalent metals to organisms living nearby oxidative surface sediments has been related to AVS (Hansen et al., 1998)(239). The metals that associated with AVS may be released via oxidation within the sediments (Daskalakis and O'Connor, 1989)(240). The oxidative release of trace metals during the mixing or re-suspension of anoxic sediments in well oxygenated overlaying waters is an obvious concern (Yu et al., 2001)(241). According to the geochemistry theory, divalent metals first bind to AVS among those competitive metal-binding phases since the Ksp values of metal sulfides are very low. The sulfides of most trace metals are highly insoluble, and are considered to be less mobile and less bio-available to benthic organisms (Argeses et al., 1997)(242). It has been verified that divalent transition metals don not begin to cause toxicity in sediment until the reservoir of sulfide is used up (i.e. until the molar concentration of metals exceeds the molar concentration of sulfide), typically at relatively high dry weight metal concentrations (Di Toro et al., 1990)(22). It has been pointed out by many authors that, metals which are easily extracted in dilute acid form sediments, are said to be bio-available (Forstner, 1989)(243). AVS is operationally defined as the amount of sulfides released during cold acid extraction, while SEM is defined as the amount of metals (normally including Cu, Pb, Zn, Cd, and Ni) liberated during the extraction of AVS (Di Toro et al., 1990)(22). Acid volatile sulphide (AVS) has been used to predict the toxicity in sediments of divalent metals, including copper (Cu), cadmium (Cd), nickel (Ni), lead (Pb), and zinc (Zn) (Di-Toro et al., 1992)(244). The rational is that the AVS present in sediment reacts with the simultaneously extracted metal-SEM, the reactive metal fraction that is measured in the cold acid extract used to measure AVS. This reaction forms an insoluble metal sulphide that is relatively nonavailable for uptake by benthic organisms. The amount of AVS present in sediments will therefore serve a critical role in setting the limits of metal bioavailability and toxicity in sediments (McGrath et al., 2002)(245). The use of different relationships between AVS and SEM to establish mechanical models such as the ratio of SEM and AVS (SEM/AVS), the difference between SEM and AVS (SEM-AVS) or the organic carbon normalized difference between SEM and AVS (SEM-AVS)/ foc to assess metal toxicity has been widely applied (Di Toro et al., 1990; Burton et al., 2005;Yin et al., 2008)(22, 246, 247). SEM/AVS approach is one of the current methods to take bioavailability of trace metals in sediments into account (e.g., Di Toro et al., 1992)(244), which assumes precipitation of trace metals (measured as SEM) with sulfides (measured as AVS) in reduced (anoxic) environments. If SEM exceeds AVS, trace metals will potentially be present in the pore water, depending on the presence of other sorption sites in the sediment. In contrast, if SEM is smaller than AVS, virtually all metals will be precipitated. This concept has been tested in laboratory and field settings as an evaluation tool of toxicity risks. SEM-AVS has been found to give good predictions about pore water concentrations and absence of toxicity in test organisms (e.g., Ankley et al., 1991; Di Toro et al., 1992)(228, 244). 2.2.6.2. Sequential extraction procedure Trace metals are widely dispersed in the aquatic environment, and ultimately deposited in the sediment, which is therefore of particular interest concerning its metal content (Gomes et al., 2010)(248). Sediments have a high storage capacity for pollutants; in no part of the hydrological system more than 1% of these substances are actually dissolved in the -52- water, while more than 99% are stored in the sediments (Salomons and Stigliani, 1995)(219). Metals can exist in different forms in the environment, where they may be transformed from one forms into another or exists in different forms simultaneously (Martinez-Sanchez et al., 2008)(249). Aquatic sediments consist of several different geochemical phases that act as reservoirs of trace metals. These phases include carbonates, sulfides, organic matter, iron and manganese oxides, and clays, all of which may occur in a variety of structural forms (Gao et al., 2010) (250). The form or "chemical speciation" of metals varies widely depending on environmental conditions. Such differences in chemical speciation affect the environmental fate, bioavailability and environmental risk of the metals. Knowledge of metal's speciation can help to assess the metal retention in soil or sediments and how easily it may be released into the soil solution (Martinez-Sanchez et al., 2008)(249). The terms “species” and “speciation”, in a chemical sense, have become widely used in the literature, and it is now well established that the occurrence of an element in different compounds and forms is often crucial to understanding the environmental and occupational toxicity of that element (Cornelis et al., 2005)(251). A number of definitions of speciation can be found in the literature. In the past, the term “speciation” has been used to refer to “reaction specificity” (rarely); in geochemistry and environmental chemistry, to changes taking place during natural cycles of an element (species transformation); to the analytical activity of measuring the distribution of an element among species in a sample (speciation analysis); and to the distribution itself of an element among different species in a sample (species distribution) (WHO, 2006)(252). Chemical extraction is employed to assess operationally defined metal fractions, which can be related to chemical species, as well as to potentially mobile, bioavailable, or ecotoxic phases of a sample. According to Verloo et al. (1980) (253), the mobile fraction is defined as the sum of the amount dissolved in the liquid phase and an amount, which can be transferred into the liquid phase. It has been generally accepted that the ecological effects of metals (e.g., their bioavailability, ecotoxicology, and risk of groundwater contamination) are related to such mobile fractions rather than the total concentration (Adriano, 1986)(254). Shortterm effects have been related to metal concentrations, frequently referred to as the intensity factor (Lindsay, 1979)(255), while medium- to long-term effects are mainly governed by the kinetics of desorption and dissolution of metals from solid-phase species, representing a capacity factor of metal solubility. The use of selective extraction methods to distinguish analytes, which are immobilized in different phases of soils and sediments, is also of particular interest in exploration geochemistry for location of deeply buried mineral deposits. Fractionation is usually performed by a sequence of selective chemical extraction techniques, including the successive removal, or dissolution of these phases and their associated metals (Hlavay et al., 2004)(256). The concept of chemical leaching is based on the idea that a particular chemical solvent is either selective for a particular phase or selective in its action. Although a differentiated analysis is advantageous over investigations of bulk chemistry of soil and sediments, verification studies indicate that there are many problems associated with operational fractionation by partial dissolution techniques. Selectivity for a specific phase or binding form cannot be expected for most of these procedures. There is no general agreement on the solutions preferred for the various components in sediment or soils to be extracted, due mostly to the matrix effect involved in the heterogeneous chemical processes (Martin et al., 1987)(257). All factors have to be critically considered when an extractant for a specific investigation is chosen. Important factors are the aim of the study, the type of solid materials, -53- and the elements of interest. Partial dissolution techniques should include reagents that are sensitive to only one of the various components significant in trace metal binding. Whatever extraction procedure is selected, the validity of selective extraction results primarily depends on the sample collection and preservation prior to analysis (Hlavay et al., 2004)(256). In sediments, metals can be present in a number of chemical forms, and generally exhibit different physical and chemical behavior in terms of chemical interaction, mobility, biological availability and potential toxicity (Wang et al., 2010)(258). Therefore, it is necessary to identify and quantify the forms in which a metal is present in sediment to gain a more precise understanding of the potential and actual impacts of elevated levels of metals in sediments and to evaluate processes of downstream transport, deposition and release under changing environmental conditions (Horowitz, 1991)(259). Determination of the total concentration of a metal in sediment is not a particularly useful indicator of sediment toxicity, as it does not distinguish between the natural and anthropogenic components of the metal. Quantifying the available or labile metals in the sediment provides a better indicator of sediment toxicity (Larner et al., 2008)(260). Leaching techniques are widely used for the assessment of heavy metal mobilization (Gleyzes et al., 2002)(261). Extraction procedures are undertaken to evaluate the metal availability and bioavailability (Kersten and Forstner, 1995)(262). In sequential extraction several selective reagents are used consequently to extract "operationally defined phases" from the sediment in a set sequence (Passos et al., 2011)(263). Methods for the determination of different forms of metals in sediments include sequential extraction, whereby a series of reagents is used to extract operationally defined discrete phases from sediments in an outlined sequence. The overall behavior of metals in an aquatic environment is strongly influenced by the associations of metals with various geochemical phases in sediments (Horowitz, 1991)(259). Sequential extraction techniques have been applied to study the geochemical partitioning of metals in contaminated soils and sediments (Zakir and Shikazono, 2011)(264). Geochemical distribution results have also been used as an aid in predicting potential contaminant mobility and bioavailability (Zakir et al., 2008)(265). This could help us to understand the geochemical processes governing metal mobilization and potential risks induced (Zakir and Shikazono, 2011)(264). There are five major mechanisms of accumulation of metals in sediments, namely exchangeable, bound to carbonate, bound to reducible phases (amorphous Fe oxyhroxide and crystalline Fe-oxide), bound to organic matter (oxidizable fraction) (Singh et al., 2005)(266). These categories have different behaviors with respect to remobilization under changing environmental conditions. The fractions introduced by anthropogenic activity include the adsorptive, exchangeable and bound to carbonate fractions. These are considered to be weakly bounded metals, which may equilibrate with the aqueous phase and thus become more rapidly bioavailable (Pardo et al., 1990)(267). Exchangeable fraction The fraction of exchangeable metals includes the portion, which is held by the electrostatic adsorption as well as those specially adsorbed. The amount of metals in this phase indicated the environmental conditions of the overlying water bodies. Metals in this fraction are the most mobile and readily available for biological uptake in the environment (Zakir et al., 2008)(265). Exchangeable fraction, usually extracted with magnesium chloride solution or sodium acetate solution (1M) at pH 8.2 for 1h, refers to the metals directly adsorbing on sediments (Krishna et al., 2001)(268). Through some typical sorption–adsorptions processes, these metals can be exchangeable and are inequilibrium with the ionic content in water. Generally, this fraction is usually used to represent the environmentally available components (Peng et al., 2009)(205). -54- This fraction comprises metals adsorbed on the surface of the sediment. It is the most accessible, and metal migration from the solid phase to water can occur, e.g. after a change of ionic composition of water or as a result of a shift of adsorption equilibrium in the system (Zerbe et al., 1999)(269). It has been widely accepted that the exchangeable metal in sediments is labile, highly toxic and the most bioavailable fraction (Wang et al., 2010)(258). Carbonates Fraction Metals associated with this fraction are not strongly bound to the sediment solids and can be released to the sediment pore water in acidic conditions (pH< 5). Among the chemical reagents, acetic acid best represented the fraction that was likely to be bioavailable to sediment ingesting and benthic organisms. Finally association of metals with this fraction is probably the best example of human-induced influence in the sediment of the study area (Zakir and Shikazono, 2011)(264). Continuously extracted with NaOAc or HOAc solution (1M) at pH 5.0 for 5h, mainly refers to the metals that are precipitated or co-precipitated with carbonate. This fraction is sensitive to pH variations (Peng et al., 2009)(205). The adsorption of trace metals is related to changes in water ionic composition which probably affect sorption-desorption processes. It is known that the carbonates of sediment contain significant trace metal concentrations and the concentrations are sensitive to changes of pH (Tokalioglu et al., 2003)(270). They can be released as a result of pH decrease (Zerbe et al., 1999)(269). Reducible or bound to Fe and Mn oxides fraction Fe–Mn oxides fraction includes the soluble metal oxides/hydroxides under slightly acidic pH as well as the metal associated with reducible amorphous Fe–Mn oxyhydroxides, which was extracted with 25% (v/v) acetic acid containing some NH2OH·HCl at 960C for 6h. This fraction can be dissolved with oxidation–reduction potential (ORP) varying (Peng et al., 2009)(205). This fraction is sensitive to the redox potential changes and in anaerobic conditions it is thermodynamically unstable (Zerbe et al., 1999)(269). It is well known that Feand Mn-oxides are present as cement, concentrations or nodules between particles or only as coating on particles. These oxides bind the trace metals and have strong scavenging efficiency for trace metals, but they are thermodynamically unstable under the anoxic circumstances (Tokalioglu et al., 2000)(270). Due to the large surface area, amorphous hydrous Fe-Mn oxides are one of the most important geochemical phases impacting the mobility and behavior of trace meals (Turner, 2000)(271). Large numbers of studies have been conducted to remove organic or inorganic pollutants by utilizing the storng adsorption capacity of hydrous Fe or Mn oxides (Root et al., 2007)(272). Oxidizable or bound to organic fraction Organic fraction may be associated with various forms of organic material such as living organisms, detritus or coatings on mineral particles through complexation or bioaccumulation process. It is extracted mainly with 0.02 M nitric acid and 30% hydrogen peroxide at pH 2.0 and 850C. This kind of metals can exist in sediment for longer periods, and can also be released with OM decomposition (Peng et al., 2009)(205). Organic matter and sulfides are important factors controlling the mobility and bioavailability of heavy metals (Wang et al., 2010)(258). The trace metals may be associated with various forms of organic material such as living organisms, detritus, or coatings on mineral particles. The complexation and peptization characteristics of the natural organic substances are well known. The organic substances may be broken up freeing the soluble trace metals in the natural waters under oxidizing conditions (Tokalioglu et al., 2000)(270). -55- Degradation of organic matter under oxidizing conditions can lead to the release of soluble metals bound to this fraction (Purushothaman and Chakrapani, 2007)(273). The affinity of trace metals for organic substances and their decomposition products are of great importance for the release of the metals into water. Trace metal bound to this fraction is assumed to reflect strong association with sediment organic material (Sharmin et al., 2010)(274). Residual fraction Residual fraction, namely the metals still remained in sediment after the above extraction procedures, usually presents as consolidated oxides, co-precipitates, and strongly held complexes, which keeps relatively stable and does not show significant transformation in various conditions (Peng et al., 2009)(205). This residual solid contains mainly primary and secondary minerals which include the trace metals within their crystal structures (Tokalioglu et al., 2000)(270). In natural conditions they are practically inaccessible for living organisms and can be treated as permanently immobile (Zerbe et al., 1999)(269). The residual or lithogenic fraction is a major carrier of transition metals in most aquatic system. The concentration of trace metals in the crystalline fraction is largely controlled by the mineralogy and extent of weathering trace metals in the form which are not soluble under experimental conditions and hence may be considered to be held within the mineral matrix (Sharmin et al., 2010)(274). Residual phases of metal are generally much less toxic for organisms in aquatic environment (Wang et al., 2010)(258). Fractionation is not only very useful for determining the degree of association of the metals in the sediments, and to what extent they may be remobilized into the environment (Jain, 2004)(275), but also for distinguishing those metals with a lithogenic origin from those with an anthropogenic origin (Passos et al., 2011)(263). According to Rubio et al. (1991)(276) metals with an anthropogenic origin are mainly present in the first three extraction fractions (soluble in acid, associated with Fe and Mn oxides and associated with organic matter and sulfides), while in the last stage of the process the residual fraction is obtained corresponding to metals with lithogenic origin. Normally, the summation of the mobile and the exchangeable fractions can be used to assess the environmentally available components. The fractions bound to Mn oxides and organic materials are supposed to represent the potentially mobile component under changing conditions, which are reviewed as the most important components in sediments for metals binding. While the residual fraction represents the more stable metal forms associated with anthropogenic or geogenic components, the influence of which to ecological system is much less than the others in major conditions (Peng et al., 2009)(205). 2.3. Environmental problems and previous studies on the coastal area along the Egyptian Mediterranean Sea Coastal areas provide important benefits to humans in terms of food resources and ecosystem services. At the same time, human activities here may have significant negative impacts on the health of ecosystems and the vitality of resources. Therefore, coastal and marine pollution control is required to predict and monitor the consequences of human activities on marine and estuarine ecosystems (Erdogan, 2009)(87). From an environmental point of view, the coastal zone can be considered as the geographic space of interaction between terrestrial and marine ecosystems that is of great importance for the survival of a large variety of plants, animals and marine species (Castro et al., 1999)(277). Most of the coastal areas of the world have been reported to be damaged from pollution, significantly affecting commercial coastal and marine fisheries. therefore, control of -56- aquatic pollution has been identified as an immediate need for sustained management and conservation of the existing fisheries and aquatic resources (González-Macias et al., 2006)(5). Coastal regions are some of the most sensitive environments and yet they are subject to growing human pressures (David, 2003)(278). Since the industrial revolution, tremendous amounts of toxic pollutants have been discarded into coastal environment and the sediments of bays and estuaries have represented huge sinks of trace metals (Fan et al., 2002)(279). Urban and industrial activities contribute to the input of significant amounts of pollutants (among them trace metals) into the marine environment and directly affect the coastal systems in which they are often deposited (Dassenakis et al., 2003)(180). Increasing residential populations and tourism threaten coastal landscapes, ecosystems, resources and the rich biodiversity inhabiting these environments (UNEP, 1996)(280). Therefore, pollution levels are often elevated in the coast because of nearby land based pollution sources (Wang et al., 2007)(192). Mediterranean Sea appears to suffer from high anthropogenic pressure due to inputs from; industrial, sewage effluents, storm water drains, shipping activities, spillage, rivers, atmospheric fallout, coastal activities and natural oil seeps (El Nemr et al., 2007b)(281). Mediterranean coastal water environments are impacted more and more by anthropogenic activities resulting in pollution of marine sediments by persistent pollutants especially the trace metals (MESAEP, 2003)(282). Intense human development in the Mediterranean region may have negative consequences on the marine environment. Inland activities such as industrial production, agriculture and tourism, combined with population growth and heavy urbanization, originate increasing pressures onto the coastal areas (EEA, 1999)(283), involving the degradation of coastal habitats and a heightened risk for inhabitating organisms and human population. Moreover, the particular oceanographic characteristics of the Mediterranean basin (relatively shallow, semi-enclosed and with limited natural water exchanges) favour the accumulation rather than the dispersion of contaminant inputs, rendering it a particularly vulnerable and potentially threatened ecosystem (Fowler, 1986)(284). The Mediterranean coast of Egypt of the Pleistocene age, extends about 900 km inlength from Sallum to Rafah and is cut by the two branches of the Nile river (El-Wakeel et al., 2006)(285). It hosts a number of activities beside a long stretch of undeveloped areas. The Mediterranean coast of Egypt with different inland and offshore activities, the estuaries of the Nile, at Rosetta and Damietta, and the coastal lakes Maryut, Idku, Burullus, Manzalah and Bardawil pour ca. 8,000 x 106 m3/y of water some of which carries heavy load of pollutants. Major cities on the coast used to get ride of their waste through sea outfalls like Alexandria, and into lakes that pour its water into the sea like Port Said. The lakes of Maryut and Manzalah are heavily polluted, and parts of them are actually dead. The maritime transport in the eastern Mediterranean, including oil tankers, commercial ships and passenger ships, affect the coast to a large extent. The entire beaches are permanently polluted by oil lumps, litter and plastic debris even in the very far remote areas of the coast where there are no known activities there. The marine environment (as a part the coastal zone) is of great economic and environmental significance. This zone in Egypt is currently under sever and ever increasing pressure. A number of factors contribute to this situation: a) rapid urbanization of the coast; b) pollution from residential commercial and industrial activities, c) tourism development, d) resource users; e) continuous development in hazards prone areas. Pollution originated from -57- the discharge of huge amounts of wastewater (sewage, industrial and agricultural discharge) into the coastal water of the Mediterranean Sea of Egypt (UNEP, 2002)(286). Degradation of water quality due to land based pollution is a serious problem in the Mediterranean coastal areas. The countries of the Mediterranean Sea basin face a variety of shared environmental problems that are trans-boundary in nature (EEAA, 2009a)(287). Coastal and marine resources contribution to sustainable development is often overlooked. Population growth, agricultural and urban development is taking place at rapid rates at many coastal areas resulting in excessive pollution loads that are allowed to enter coastal waters (Nessim et al., 2010)(288). Measurement of trace metal concentrations in sediments is the first step in evaluating their potential health or ecological hazard. Several studies were performed on the total concentration of trace metals in sediments in different areas along the Egyptian Mediterranean Coast to evaluate their ecological risk. Concentrations of eight heavy metals (Cd, Cr, Cu, Fe, Mn, Ni, Pb, and Zn) in surface sediment from El-Sallum to Sidi-Kreer along western part of Egyptian Mediterranean Coast were determined to evaluate their levels and spatial distribution by Ahdy and Khaled (2009)(289). The ranges of the measured concentrations in the sediments are as follows: 0.5240.924 μgg-1 for Cd, 16.248-34.164 μgg-1 for Cr, 26.529-33.332 μgg-1 for Cu, 846.4261433.933 μgg-1 for Fe, 32.371-108.915 μgg-1 for Mn, 31.703-43.592 μgg-1 for Ni, 20.67235.624 μgg-1 for Pb, and 26.267-112.73 μgg-1 dry weights for Zn. There were no significant correlations among most of these metals, indicating they have different anthropogenic and natural sources. To assess metal concentrations in sediment, Numerical Sediment Quality Guidelines (SQGs) were applied. The concentrations of Cd, Cr, Pb, and Zn in all sediment samples are lower than the proposed TECs indicated that there are no harmful effects from these metals. On the other hand, concentration of Ni exceeded TEC in all samples while Cu was exceeded the TEC at El-Sallum and Sidi-Barrani indicated that these stations were in potential risk. The metal contamination in the sediments was evaluated by applying Index of geo-accumulation and contamination factor. El Nemr et al. (2007a)(61) assessed the marine pollution due to metals for surfacial sediments sampled from 20 sites along Mediterranean coast of Egypt. The samples were analyzed for leachable and total heavy metal concentrations (Cd, Co, Cr, Cu, Fe, Mn, Ni, Pb, and Zn). Evaluation of the heavy metals pollution status was carried out using enrichment factors, the effect range-low (ERL) and the effect range median (ERM). The study showed high concentrations of Cd, Co, Pb, Ni and moderate concentrations of Cr, Cu and Mn were contaminated in the sediments of studied sites. They found that the main source of contamination is the offshore oil field and industrial wastes, which arise due to the ineffective and inefficient operation equipments, illegal discharge and lack of supervision and prosecution of offenders. The coastal strip along Alexandria city from Agami in the west to Maamoura in the east was studied by El-Sammak and Aboul-Kassim (1999)(290). They used the pollution load index to find out the mutual pollution effect at the different stations by the different metals (Co, Zn, Ba, Mn, Sr, Ni, and Fe). They found that there was an increase of PLI toward the western side. They concluded that these two zones was considered to be the most polluted areas at Alexandria beach. El-Mex bay: -58- El-Mex bay, lies in the western part of Alexandria coast between longitude 29 45 and 54 E and latitude 31 07 and 31 15 N, and extends for about 7 km between El-Agami (west) and the Alexandria commercial Western Harbor (east) with maximum depth 20 m. The bay is one of Alexandria coasts but it differs in having several industrial plants that directly discharge their effluents into it. These are petrochemical, cement, chemicals, tanneries, industrial dyes, ink, petroleum refining, meat processing, and fish production beside the Alexandria iron and steel factory (Rifaat, 1982)(291). In addition, the bay is an estuarine zone of huge agricultural drain called Omoum Drain its discharge rate 2,547.7 x 106 m3/year. The downstream part of the last drain receives considerable amounts of Alexandria domestic and industrial wastes prior discharging to the bay at a site lies just west of the Western Harbor (Abdallah, 2007a)(292). Under prevailing hydrographic conditions and a sheltered geographical position, El-Mex Bay estuary is two layered estuary, the fresh water from the drain spreads in the estuary after mixing with seawater as surface brackish layer that overlies the other layer of almost proper Mediterranean seawater (El-Gindy et al., 1986)(293). El-Mex Bay is considered one of the most important hot spot areas in Alexandria. It is subjected to large quantities of untreated industrial and domestic sewages (Masoud et al., 2007)(294). 29 The distribution of several heavy metals (Cr, Cu, Cd, Pb, Zn, and Hg) was investigated by Massoud et al. (2007)(294) in muscle, gill, and liver in two different fish species seasonally collected in El-Mex Bay (autumn 2004–summer 2005). In order to evaluate the pollution status of the Bay, the concentrations of the selected metals in the labile and total fractions were analyzed in sediment samples collected from eight sites in El-Mex Bay during autumn 2004. Also, the Index of Geoaccumulation (Igeo) for the sediment was estimated. The total and labile fractions of the selected metals in sediment samples were 15.2 and 62.8 μgg-1 dw for Cu, 1.8 and 5.0 μgg-1 dw for Cd, 79.1 and 130.3 μgg-1 dw for Zn, 0.2 and 1.2 μgg-1 dw for Hg, 35.8 and 93.0 μgg-1 dw for Pb, and 13.9 and 31.0 μgg-1 dw for Cr. Abdallah (2008)(295) studied the distribution of heavy metals in El-Mex bay located in Northern Egypt. Eight metals (Cd, Cr, Co, Cu, Zn, Pb, Mn and Fe) were determined in water, suspended particulate matter and sediments. The bay presents higher metal concentrations in aqueous Cd, Co and Pb are above the chronic freshwater quality criteria for aquatic life. Most of the dissolved trace metals displayed a negative association with salinity, indicating Omoum Drain as a source of inputs for them. In the bay water, Fe, Mn and Zn are the most abundant elements in suspended particulate matter whereas Co the less abundant. El-Mex bay exhibited relatively lower concentrations of all the examined metals in sediments, comparing with other regions in the world. The western harbour The western harbor of Alexandria is situated between longitude 29 50 and 29 53 E and latitude 31 9 and 31 12 N. Its length is 7 km, maximum width is 2 km and water depth varies from 5.5-14 m (Saad et al., 2004)(91). It is the largest and oldest harbour on the Egyptian Mediterranean coast, serving about three quarters of Egypt’s international trade. The harbour receives imported and exported materials such as coal, manufactured iron, cement, fertilizers, grains, food, textiles, chemicals, timber, as well as crude and refined oil. There is also an old dry dock and workshop for ship building and repairs. Located on the southern and eastern sides of the harbour, the quays for the various maritime activities divide these sides into several small semi-enclosed or open basins. Wastewaters of varying quantity and quality are discharged into the harbour, mainly through the Umoum Drain (76.4 m3 s-1 ) and the Noubaria Canal (1 m3 s-1 ) (Dorgham et al., 2004)(296). -59- The western harbour of Alexandria, situated to the west of the city of Alexandria along the Mediterranean coast of Egypt, is a complex harbor with an area of about 31 km2. The harbor is connected to the open sea by a narrow strait, which protects the bay from the prevailing NW winds and renders the harbor a safe anchorage. The water body inside the harbor has an average depth of 7m. The harbor was naturally formed during the PreHolocene subsidence of the coast and the subsequent transgression of the sea (Butzer, 1960)(297). Calcareous marine deposits cover the continental shelf surrounding the harbor (Mostafa and Barakat, 2004)(298). The western harbour is connected to the sea by El-Boughaz. It is protected by two water breaks and is divided into two main basins; the inner and outer ports having areas of 200 and 600 acres, respectively. The Mahmoudia canal used to discharge into the inner port has recently ceased to flow in El-Noubaria Navigation canal, crossing the heavily polluted lake Mariut, opens into the outer port. The western harbour is under stress from various pollutants from different external and internal sources. The external pollution results from domestic, industrial and agricultural wastes. Thousands of cubic meters of contaminated waters are discharged daily into the western harbour via El-Nobaria Canal and from El-Mex Pumping Station to the west of the western harbour and are partially introduced into it by the prevailing wind. Besides, considerable amounts of untreated sewage and industrial wastes are dumped directly into the western harbour from several outfalls. The internal pollution originates from different shipping wastes beside the discharges resulting from loading and unloading processes of the imported and exported industrial raw materials (Saad et al., 2004)(91). The western Harbour of Alexandria is the major trade port of the Northern Territory of Egypt. Industrial activities have increased dramatically in this area over the past 20 years. The harbor handles approximately 75% of all ship-borne cargo of the country. As a result aggressive urbanization and industrialization of Alexandria region, the coastal waters in general and the Western Harbour in particular have received considerable amounts of treated and untreated industrial, agricultural and domestic wastes (Salem and Sharkawi, 1981)(299). These wastes are derived principally from effluent discharge from the El-Mex pumping station to the west of the harbor. The effluent consists of overflow from lake Maryut (a coastal lagoon heavily polluted mostly by domestic and industrial wastes), and the drainage water from the El-Umum drain and El-Noubariya Canal. Industries that benefit from their quay-side location include a chlor-alkali plant (Misr Chemical Industries). Portland cement factories discharge unknown quantity of wastes into the harbor. Minor amounts of industrial wastes are directly discharged into the harbor through tanneries (Mostafa and Barakat, 2004)(298). According to Saad and Hemeda (1992)(300), the discharged pollutants cause hazardous effects on the compartments of the western harbour. The harbor’s sediments are mostly covered with sludge containing high levels of organic matter, nutrients and heavy metals (Riffat, 1982)(291). The problem of pollution in the western harbour increases with progress of time, due to the successive increase in population and in the number of visiting ships (Saad and Hemeda, 1992)(300). Because the harbor is a semi-closed basin with restricted water circulation, it may serve as an entrapment of the wastes introduced from land-based sources as well as from the harbor itself due to shipping activities. Future development and continued operation of Alexandria Harbour is of great economic importance to this region, but these activities may also impact its ecological functioning (Mostafa and Barakat, 2004)(298). -60- Mostafa and Barakat (2004)(298) determined the concentrations of heavy metals in surfacial bottom sediments of the Western Harbor to assess their potential biological effects and to identify their possible sources. Sediment samples from 21 stations throughout the harbor were analyzed for grain size, total organic carbon content, and metals (Al, As, Ba, Be, Cd, Cr, Cu, Fe, Mg, Mn, Ni, Pb, Se, Sn, V, and Zn) to assess the extent of contamination in the area. The results indicated that concentrations of metals in the sediments varied widely depending on the location. High levels of metals were observed in the Arsenal Basin and the outfall area of El Mahmoudiya Canal in the inner harbor. El-Mamoney and Mohamed (2006)(301) collected some short cores from the Western Harbor, Eastern Harbor and Abu Qir bay to investigate the penetration of heavy metals into the bottom sediments. Every core interval was analyzed for granulometric characteristics, water content, organic carbon, carbonate, Cd, Co, Cu, Cr, Ni, Zn, Mn and Fe concentrations. They found that the upper most layers of the cores show the highest heavy metal accumulations with the maximum levels in the Western Harbor. Eastern Harbour The Eastern Harbour of Alexandria is located in the southern Mediterranean Sea between latitudes 31 12 and 31 13 N and longitudes 29 53 and 29 54 E ; it is a semienclosed basin (mean depth 6m), and has been strongly affected by urbanization (Abdallah and Abdallah, 2008)(302). The harbour has a surface area of about 2.53 km2; accordingly its volume is about 15.2 x 106 m3. It is sheltered from the sea by artificial break water leaving two openings (left and right). The left opening is the main navigation entrance to the harbour (300 m width). Through these openings the exchange of water between the harbour and Mediterranean water takes place (Abdallah, 2007b)(303). Sources of pollution include untreated domestic discharges through several submerged minor sewage outfalls distributed along the harbour coast. There are various small industries such as; photo development shops, car cleaning and repairing, some foodstuff plants, gas stations, small dairy plants and some foundries. Also the harbour water receives additional waste effluents from fishing ships and the ship yard situated on its western side. Other wastewater discharges occur through two marine outfalls lying at the outer sides of the harbor the Qait Bey and Silsila marine outfalls (El-Rayis et al., 2003)(304). The importance of this harbour relates to the discovery of ancient buildings on the peninsula of Timonium and Antirhodos Island (located in the eastern part of the harbour) and artificial dykes constructed by the Ptolemies and by Marcus Antonius. In addition, about 1000 different artifacts including columns, basins, sphinx statues, and parts of obelisks with hieroglyphs and ceramics were discovered during the excavations. This basin is also considered as one of the main fishing grounds for the city of Alexandria and its adjacent areas (Abdallah, 2007b)(303). The Eastern harbour has been subjected to high levels of pollution due to municipal waste disposal in addition to the waste dumping from ships and shipping activities. Similarly, El-Mex bay having several industrial plants situated close to the coast and directly discharges its effluents into it. In addition this bay is an estuarine zone of huge agricultural drain (Omoum drain), its discharge rate about 2,547x 106 m3/year (El-Rayis and Abdallah, 2006)(305). The distribution, enrichment and accumulation of heavy metals in the surfacial sediments of the Alexandria City Eastern Harbour (Mediterranean coast of Egypt) were investigated by Abdallah (2007b)(303). Surface sediments (in the <63µm fraction) were collected from 12 sites representing the entire area of the harbour, were analyzed by AAS for -61- Cd, Cu, Zn, Cr, Pb and Al. Metal levels were compared with literature data to assess the pollution status of sediments. Enrichment factors (EFs) and the geoaccumulation Index (Igeo) were calculated as a criterion of possible contamination. It was found that Zn represents the highest median concentration, followed by Pb. According to calculations of enrichment factors, Pb and Cd are of moderately severe enrichment, while Zn has the highest level of enrichment. Regarding other elements, Cr is at background levels and Cu is of minor enrichment. Abdallah and Abdallah (2008)(302) determined the concentrations of Cd, Cu, Co, Zn, Mn and Fe in biota and sediment samples collected form the Eastern Harbour and El-Mex Bay in the Mediterranean Sea, Egypt. Results showed that the two species of bivalves, Donax trunculus and Paphia textile had different amounts of metals in their tissue. The abundance of heavy metals concentrations in the mussel samples was found in the order Fe> Zn >Mn > Cu> Co> Cd> and Fe> Zn> Mn > Cu> Cd> Co, respectively for the two species. The metals concentrations were generally higher compared with the previous studies in the same area. The levels of metals accumulated in the investigated fish samples, were higher than those of Marmara Sea (Turkey), for Co and Cd and lower for Cu, Zn, Mn and Fe. El-Mex bay having the highest metals concentration in sediments as their order of abundance were Fe> Zn> Mn> Cu> Cd> Co. The concentrations of heavy metals were determined in sediments of the Eastern Harbour by Nasr et al. (2011)(306). The range and average concentrations (μgg-1) were 2026.79- 2799.11 (2457.59) for Fe; 95.18-285.53 (192.69) for Mn; 55- 164 (111.85) for Zn; 33.33- 180.95 (87.08) for Pb; 24.22-173.70 (67.53) for Cu; 36.47- 127.66 (65.43) for Cr and 122.36- 168.78 (141.56) for Ni. The study concluded that the Eastern Harbor of Alexandria is subjected to serious contamination sources of heavy metals, and reflect the anthropogenic input as a source of heavy metals and normalize them with grain size, total organic matter and total carbonate content of the sediment of the Eastern Harbor. Rossetta and Damietta The Rosetta estuary receives annually controlled outflow of the Nile at certain times through Edfina barrage. The most northern part of this estuary runs through a narrow sandy cape previously formed by the previously gradual sedimentation of mud and silt transported by the Nile flood. This cape was subjected to gradual erosion by seawater currents after construction of the Aswan High Dam, as most of the suspended matter transported by the Nile flood is deposited in the High Dam Lake. The highest discharge from Edfina Barrage occurs in January and the lowest during the period from April to November (Saad and Hassan, 2002)(307). The new Damietta Harbor was constructed in 1982, and is located about 9.7 km west of the Damietta Nile Branch. The harbor basin was constructed inland and its entrance was protected by two breakwaters. The western breakwater extends about 1500 m parallel to the navigation channel, attaining the 7m depth contour. The eastern one is about 500m long, perpendicular to the shoreline and tends to about 3m water depth contour. The navigation channel extends offshore to the middle shelf or about 15m. Since January 1984, the channel of the harbor has experienced sedimentation and subsequently threatening the navigation activities (Shereet, 2009)(308). New Damietta Harbour is considered as semi closed water body influenced by loading/unloading activities, municipal and agricultural waters resulting from Damietta Governorate (Shereet, 2009)(308). Mostly Damietta is an industrial center known for its -62- furniture, leathers, textile and sweets industries in addition to dairy products and rice mills and for its agricultural heritage. It is also a fishing industry town, with one of the largest fleets on the Mediterranean which accounts for fully half of the fishing boats of Egypt. Finally, it is well known for the port. Damietta Harbor is considered as semi closed water body affected mainly from loading/unloading operations, municipal and agricultural wastes resulting from Damietta governorate. It is generally agreed that, the pollution in near-shore waters of the Mediterranean sea has reached a critical level. This is chiefly due to the total absence of control on toxic components. River runoff (Damietta branch) has the direct effect of reducing the salinity of the surface layer of the Mediterranean sea, while tidal currents have a considerable influence on the vertical mixing of shallow water near the coast (Said and Hamed, 2001)(309). Untreated domestic wastewater with agricultural and industrial wastes is still released through a number of drainages and outfalls along the coastal area of study (Said and Hamed, 2006)(310). Faragallah et al. (2009)(311) investigate the hydrographic characteristics, nutrient salts and some heavy metals (Fe, Cu, Zn, Pb and Ni) as well as chemical oxygen demand (COD), biological oxygen demand (BOD) and chlorophyll-a (Chl-a) in six vertical profiles in the open Mediterranean sea water far about 60 Km from Damietta harbor (Egypt). Water samples were collected during April 2007. The results revealed that most of nutrients and heavy metals are concentrated in the surface layer and decreased with increasing the depth. N/P ratio and abundance of the N-ions revealed that the area is mostly N-limiting. Enrichment factor (EF) of the metals gives low values, less than 1 indicating to the enrichment and advection of heavy metals counted each other. The results indicated that the impact of anthropogenic inputs was limited in the distribution of nutrient and heavy metals, the values of metals were similar or lower than that reported for water quality criteria except that the Zn level was slightly higher. The relationships between the different heavy metal concentrations and the other parameters (salinity, chlorophyll-a and suspended particulate matter) were discussed. The values of BOD/ COD ratio indicated that the water of the study area has a biodegradable nature. Relatively high levels of Chl-a concentrations was observed in the surface layer during the period of study and negative correlation was found between Chl-a and both NO3-N, PO4-P and SiO4 (r= -0.58, -0.38 and -0.58, respectively). El-Dekheila Harbour The newly constructed El-Dekheila harbor lies to the west of Alexandria city, between El-Mex and El-Agami at Latitude 29 47 and Longitude 31 10, with surface area of about 12.5 km2 and a depth ranging from 6 to 19 m with an average of 12.4 m. El-Dekheila harbor was constructed to serve basically Alexandria Iron and Steel factory. The harbor as a part of El-Mex bay is subjected to several sources of wastewater (Shata and Deghedy, 2004)(312). This is a commercial harbour. El-Dekheila Harbour is a semi-enclosed basin constructed recently, after 1986, on the western side of El-Mex bay (Fahmy et al., 1997)(313). According to Abdalla et al. (1995)(314) and Fahmy et al. (1997)(313), the harbour’s water is subjected to several sources of wastewater. A huge volume of brackish water is discharged into El-Mex bay through the El-Umoum drain. On its western side, near the harbour, this bay also receives industrial wastes from several sources. The degree of water contamination of the harbour water from the above mentioned sources depends on water circulation in the bay. El-Dekheila Harbour, like other harbours, is affected by shipping activities. Its water depth ranges between 6 and 19 m with an average of 12.4 m. The exposed panels were dangled at the container pier. Abu Qir Bay -63- Abu-Qir bay is one of the Mediterranean coastal bays. It is a shallow (mean depth 12m) semi-circular bay, lies 36 km east of Alexandria city, the area of the bay is about 360 km2 with shore line of about 50 km long. This bay receives a continuous run off (totally of about 5 million m3/d) mainly from three land-based sources, namely from west to east Tabia pumping station (mainly industrial and agricultural waste waters), Maadia outlet (mainly agricultural drainage water) and Rosetta mouth (mainly river water). Many reefs, shoals and patches of foul ground could be found in the south west part of Abu Qir bay. These ridges cause a rather limited water exchange with the open sea (Faragallah, 2004)(315). It is simultaneously used as a marine habitat, source of food, site for recreation and disposal of industrial, agricultural and domestic wastes (Aboul Dahab, 1992)(316). Abu Qir Bay is boarded from the eastern side by the Rosetta estuary of the Nile and from the western side by Abu Qir headland. The area of the bay is 360 Km2, with an average depth of 12 m and a volume of 4.32 Km3. The seaward limit of the bay is considered as the line adjoining the Rosetta mouth and Abu Qir headland. Abu Qir bay receives fresh Nile water from Rosetta estuary at its eastern side, brackish water from Lake Edku through Maadia Channel at its southern side and highly polluted waters via Tabia Pumping Station at its south-western side and the rain water was insignificant. After damming of the Nile in 1964, the quantity of the discharged Nile waters into the sea through Rosetta mouth was much reduced to 3 x 109 m3 annually (Irrigation Department). The discharged Nile water did not show an effect on the western region of Abu-Qir Bay, but decreased the surface salinity of its eastern part to about 37% during winter (El Deeb, 1977)(317). About 1400 million m3 of brackish lake water (less than 2%) were discharged from Lake Edku to Abu Qir Bay and its flushing rate was 2.5 months (Abdel-Moati, 1991)(318). The industrial wastes of several factories discharged into Abu Qir Drain result from industries including fertilizer, textile, paper, food processing and canning. Abu Qir drain flows through cultivated area till Tabia pumbing station. This heavily polluted water, which spreads out into the bay through Tabia pumping station, amounted to 2.0 x 106 m3/d and contained mainly organic and inorganic, pollutants (Saad and Badr, 2005)(319). In an attempt to evaluate the environmental quality of Abu Qir Bay, an important highly productive area in Alexandria, Egypt, an environmental risk assessment was performed by Khairy (2008)(226); including a screening level ecological risk assessment (SLERA) and a human health risk assessment (HHRA). To fulfill the goals, 30 surfacial sediment samples were collected from different locations covering the region from the harbour area till the Maadeya Outlet. Concentrations of total Ni, Co, Cr, Pb and V showed close pattern of spatial distribution in the bay sediments. Cu and Zn concentrations were much higher in front of the Abu Qir Drain and the Fertilizer Company. Hg and Sn total concentrations were higher in front of the Maadeya Outlet and in the offshore direction too reflecting the influence of the discharged agricultural wastes and shipping activities respectively. Concentrations of all metals were lower in the western part of the bay. Most of the investigated metals (except Se and Sn) showed significant positive correlation with clay content and the Fe %, which may indicate that metals could have entered the bay either adsorbed on Fe oxyhydroxides and/or scavenged by the Fe oxyhydroxides when they entered the bay waters. Burullus lagoon Burullus lagoon is one of four shallow brackish water coastal lagoons (namely: Manzala, Burullus, Edku and Maryout) of Nile Delta. It is the second largest one which has an area of about 410 km2. It lies between Longitudes 30 30 and 31 10 E and Latitudes 31 21 and 31 35 N. The lagoon width varies between 4 and 16 km, and its mean water depth varies from 60 to 150 cm. It is separated from the Mediterranean Sea by sand bars and sand -64- dunes of different widths and heights and is connected to the sea with Boughaz El-Brullus. Burullus lagoon is affected mainly by agricultural drainage water mixed with different types of wastes from fish farms (Terra drain, drain 7, drain 8 and drain 11), wastewaters effluents (Terra drain, drain 7 and El-Gharbia drain) as well as domestic drainage water discharged mainly from El-Gharbia drain and drain 11 (Khalil et al., 2007)(320). Lake Burullus has an area of 370 km2. It occupies a central position along the Mediterranean coast of Egypt. It is connected to the Mediterranean through El-Boughaz ElBurg. Water depth ranges from 50 to 160cm. The lake receives 3.6 x 106 m3 of water annually, almost from domestic and agricultural sewage (El-Sammak and El-Sabrouti, 1995)(321). El-Sammak and El-Sabrouti (1995)(321) determine the heavy metals contents in the sediments of Lake Burullus. The contamination factors were found to fall in the following sequence: Cd>Pb>Cu>Zn. Fathi and Abdelzaher (2005)(322) studied some characteristics of Lake Burullus. Data from sediment core analysis showed that, the maximum concentration of Zinc (6.2 µgg-1) and Cu (1.0 µgg-1) in sediment were observed at 6 cm and 26.5 cm sediment depth, respectively. The highest concentration Pb (7.5) µgg-1 was found at 0.5 cm depth. Twelve samples from surface sediments of Brullus lagoon and adjacent Mediterranean Sea were collected by Khalil et al. (2007)(320). They found that the variations of the measured metals (Fe, Mn, Zn, Cu, Ni, Co, Cd, and Pb) in sediments are varied depending on the locations, whereas the high levels were observed in the western area of the lagoon. They were positively correlated with each other and organic carbon suggested that the distributions of these metals are associated with the organic matter accumulation. Saeed and Shaker (2008)(323) determined concentrations of heavy metals including Iron, Zinc, Copper, Manganese, Cadmium and Lead (Fe, Zn, Cu, Mn, Cd and Pb) in water and sediments in northern Delta Lakes (Edku, Borollus and Manzala) and their accumulation in Nile tilapia (Oreochromis niloticus) organs (muscle, gills and liver) were investigated. Water, sediments and fish organs from Lake Manzala showed greater concentrations of most of the studied metals than those from Lake Edku and Lake Borollus. Fe, Mn, Cd and Pb (in Lake Manzala) and Mn and Pb in Lake Borollus showed levels above the international permissible limits in water. In sediment samples Mn (in Lake Edku) and Cd (in Lake Manzala) recorded higher values than the sediment quality guidelines. Gills and Liver of O. niloticus contained the highest concentration of most the detected heavy metals, while muscles appeared to be the last preferred site for the bioaccumulation of metals. The edible part of O. niloticus showed higher levels of Cd (in Lake Edku and Manzala) and Pb (in Lake Manzala). Nile tilapia caught from these two Lakes may pose health hazards for consumers. Port Said El Tokhi et al. (2008)(324) determined the concentration of Cu, Zn, Ni, Pb, Cd and V in the bottom sediment of the east Port Said area. They found that Cu, Zn, Ni, Pb, Cd and V concentration above the accepted level. The contamination levels were found due to anthropogenic origin. These include intensive maritime activities, disposal of waters from anchorage vessels that are waiting the crossing of the Suez Canal, lubricating oil, waters from the ships yard at the entrance of the Suez Canal and wastes from the urban centers (Port Said and Port Fouad cities) -65- There are very limited studies on the geochemical forms of trace metals in the sediments along the Mediterranean coastal area. In this section we will represent some of this studies that performed sequential extraction procedure to identify the potential impact of trace metals along the Egyptian Mediterranean Sea sediments. Nasr et al. (1990)(325) applied a sequential chemical extraction technique for the partitioning of particulate heavy metals (iron, manganese, zinc, copper and lead) into five fractions: exchangeable, bound to carbonate, bound to Fe-Mn oxides or easily reducible, bound to organic matter including sulphides and residual. This study reveals high levels of zinc, copper and lead pollution in the coastal water of Alexandria. Saad and Badr (2003)(182) used a five step sequential extraction technique to describe the chemical association of copper with major sedimentary phases; exchangeable (F1), carbonates (F2), Fe/Mn oxides (F3), organic/sulfides (F4), and residual associations (F5). They found that the Cu fractions in the Eastern harbour’s sediments decreased in the following order: F5>F4>F3>F2>F1. The distribution pattern of these fractions is mostly controlled by the mineral composition of sediments and the anthropogenic wastes introduced to the study area. The low association of copper with F1 confirms that metal was low in the soluble form. The higher value of F2 at the center of the Eastern harbour coincided with abundance of the biogenic clastics as major source of carbonates in the sediments of this area. The high concentrations of F3 in the suspended matter and sediments at the boatyard area and the Eastern harbour’s opening indicate the interaction between both phases. The high level of F4 is not surprising, due to continuous accumulation of organic matter from large amounts of domestic sewage discharging. Saad et al. (2004)(91) studied the local distribution of total lead and its species in the western harbor sediments. A five step sequential extraction scheme was applied to illustrate the contribution shared by each individual fraction in the total lead concentration in the western harbor sediments. The exchangeable fraction (F1) was very low. The bound to carbonate fraction (F2), the bound to iron-manganese oxide fraction (F3) and the bound to organic matter- sulfide fraction (F4) ranked fourth, second and third in abundance. The sediments of El-Mex Bay estuary on the southern Mediterranean Sea have been analyzed by Abdallah (2007)(292) for trace metals after sediment fractionation by sequential leaching. A sequential extraction procedure was applied to identify forms of Mn, Cu, Cd, Cr, Zn and Fe. The five steps of the sequential extraction procedure partitioned metals into: extractable (F1); carbonate extractable (F2), reducible extractable (F3); organic extractable (F4) and acid soluble residue (F5). Extracted concentrations of trace metals analyzed after all five steps, were found to be (µg/g) for Mn: 1930, Cu: 165.3, Cd: 60.9, Cr: 386.3, Zn: 2351.3 and Fe: 10895. Most of elements were found in reducible fraction except Fe found in acid soluble residue, characterizing stable compounds in sediments. Khairy (2008)(226) applied a sequential extraction procedure to surface sediments from Abu Qir Bay. Results obtained revealed that the majority of Ni and Co were incorporated in the residual fraction of the sediments, thus chemically inactive. Although the residual fraction of Fe, Cr, Mn and Zn showed the highest percentage compared to the other 4 fractions, the sum of the first four non-residual fractions were higher than the residual fraction of each element, especially the reducible fraction, which showed a significant portion of the total metal concentration in Fe and Cr. At the same time, the reducible fraction showed the highest concentrations of Pb and V. The oxidizable fraction of Cu was found to be the dominant fraction which may indicate the association of Cu with organic matter in the bay sediments. High significant positive correlation was observed between concentrations of the reducible Fe -66- and concentrations of the labile fractions of metals (F1 + F2 + F3), which confirm the strong association between metals and the reactive Fe in the bay sediments. The anthropogenic influence on the investigated trace metals concentrations was identified in most of the investigated sediment samples, especially for Se, Cd, Hg and Pb. These elements were highly enriched in relation to Al, which was used as the normalizer. The distribution of total and different chemical forms of copper and manganese has been studied by Faragallah and Khalil (2009)(326) using sequential extraction techniques. Chemical analysis of the sediment show that, in Abu-Qir bay, cupper is bonded more with the residual and organic fractions and manganese with residual and carbonate fractions. In ElMex bay, cupper is enriched in the labile fractions (exchangeable, carbonate and oxides) and manganese with carbonate fraction. The mobility and bioavailability of cupper and manganese in El-Mex bay is higher than that in Abu-Qir bay. El-Anany (2008)(327) identified the geochemical forms of aluminium (Al) in core sediments from Lake Burullus. The distribution mapping of aluminium level of the surface and subsurface sediments of different fractions were also studied. The results of the vertical distribution of Al-exchangeable fraction revealed irregular variations through the four cores. Generally, the residual fraction is the first highest percentage reached to more than 90% of the total aluminium and followed by the organic fraction which has Al level more than 2% for most intervals of the four cores. The relative percentage of Al bound to the five fractions from the total concentrations can be arranged as follows: carbonate (0.01-0.05%) < Exchangeable (0.01-0.41%) < Fe-Mn oxides (0.03-0.58%) < organic (0.41-3.12%) < Residual (more than 90%). There are very limited studies on the relationships of trace metals and AVS in the sediments along the Mediterranean coastal area. Studies on the environmental state of the Egyptian Mediterranean Coast have concentrated in the past mostly on simple chemical and bulk analysis of sediments. Okbah et al. (2011)(328) studied the relationship between Zn, Cu, Ni, Pb, Cd, and amorphous iron sulphides to predict the bioavailability and toxicity of metals in Damietta Port and offshore sediments. Sulphides were measured as acid volatile sulphides. The average values of SEM in Damietta Port sediments were 11.21±1.95, 5.16±1.18, 0.23±0.08, 1.30±0.58, 0.71±0.17, 0.11±0.04, 1.23±0.71 and 0.18±0.09 µmoleg-1, dry weight respectively for the offshore samples. Generally, the concentrations of trace metals in both areas were in the order of Zn >Pb>Cu>Cd>Ni. The difference value between AVS and SEM is an important tool of trace metals bioavailability and ecological risk. The range and average values of SEM concentration ranged from 1.96 to 29.94 (14.70 ± 8.16) µmoleg-1, the results revealed significantly between the two regions of the study area. The levels of AVS concentrations showed spatial variations, the range and average value of AVS were between 7.71 and 40.57 (24.12±9.53) µmoleg-1. The ratio of SEM/AVS was lower than 1 at all the offshore sediments except at two stations as well as at five stations located inside the port (SEM/AVS>1), which suggests that the metals have toxicity potential found in these sediments. -67- 2.4. Ecological risk assessment Ecological risk assessment is a broad framework for estimating the likelihood and severity of potential impacts to the structure, functioning, components or processess of ecological systems (ecosystems); such assessments are used routinely by many countries. Typically, these assessments follow the general ecotoxicology paradigram, identifying and assessing the exposure and effects of human and other populations to such stressors as contaminants or pathogens or habitat change. The approach has been formalized by the United States "Environmental Protection Agency" among other bodies. Significantly, the approach applies equally well to analysis of the potential ecological effects of invasive species and biological control agents (Andresen and Draggan, 2007)(329). Ecological risk assessments are developed within a risk management context to evaluate human-induced changes that are considered undesirable. As a result, these guidelines focus on stressors and adverse effects generated or influenced by anthropogenic activity. Defining adversity is important because a stressor may cause adverse effects on one ecosystem component but be neutral or even beneficial to other components. Changes often considered undesirable are those that alter important structural or functional characteristics or components of ecosystems. An evaluation of adversity may include a consideration of the type, intensity, and scale of the effect as well as the potential for recovery. The acceptability of adverse effects is determined by risk managers. Although intended to evaluate adverse effects, the ecological risk assessment process can be adapted to predict beneficial changes or risk from natural events (USEPA, 1998)(330). 2.4.1. Ecological Risk Terms Some important terms in ecological risk assessment: - Hazard: A situation that could potentially lead to ecological harm. - Stressor: The component or components of a system that may lead to a hazard or undesirable outcome. - Receptor: The component or components of a system that may be negatively influenced by a stressor. Pollutant risk assessments are always directed at such particular assessment endpoints as response of growth or fecundity to toxicity. These endpoints are focused typically on effects of chemical contaminants on individuals. However, since the scale of impacts of interest are usually population level effects (i.e. changes in abundance), ecological models are often used to perform the necessary extrapolation from the measurement endpoint (e.g. a toxic, teratogenic or developmental effect) to the assessment endpoint (the ecological characteristics or feature that is to be protected from risk, such as the abundance of some sensitive species) (Andresen and Draggan, 2007)(329). 2.4.2. Phases of Ecological Risk Assessment The ecological risk assessment process is based on two major elements: characterization of effects and characterization of exposure. These provide the focus for conducting the three phases of risk assessment: problem formulation, analysis, and risk characterization. The three phases of risk assessment are enclosed by a drak solid line. Boxes outside this line identify critical activities that influence why and how a risk assessment is conducted and how it will be used. 1- Problem formulation: the first phase is shown at the top. In problem formulation, the purpose for the assessment is articulated, the problem is defined, and a plan for analyzing and characterizing risk is determined. Initial work in problem formulation -68- includes the integration of available information on sources, stressor, effects, and ecosystem and receptor characteristics. From this information two products are generated: assessment endpoints and conceptual models. Either product may be generated first (the order depends on the type of risk assessment), but both are needed to complete an analysis plan, the product of problem formulation. 2- Analysis: shown in the middle box, is directed by the products of problem formulation. During the analysis phase, data are evaluated to determine how exposure to stressors is likely to occur (characterization of exposure) and, given this exposure, the potential and type of ecological effects that can be expected (characterization of ecological effects). The first step in analysis is to determine the strenghts and limitations of data on exposure, effects, and ecosystem and receptor characterization. Data are then analyzed to characterize the nature of potential or actual exposure and the ecological responses under the circumistances defined in the conceptual model(s). The products from these analyses are two profiles, one for exposure and one for stressor response. These products provide the basis for risk characterization. 3- Risk characterization: during risk characterization, as shown in the third box, the exposure and stressor-response profile are intergrated through the risk estimation process. Risk characterization includes a summary of assumptions, scientific uncertainities, and strenghths and limitations of the analyses. The final product is a risk description in which the results of the integration are presented, including an interpretation of ecological adversity and descriptions of uncertainity and lines of evidence (USEPA, 1998)(330). The framework for ecological risk assessment proposed by the (USEPA 1998)(330). 2.4.3. Ecological risk assessment in a management context Ecological risk assessments are designed and conducted to provide information to risk managers about the potential adverse effects of different management decisions. Attempts to eliminate risks associated with human activities in the face of uncertainties and potentially high costs present a challenge to risk managers. Although many considerations and sources of information are used by managers in the decision process, ecological risk assessments are -69- unique in providing a scientific evaluation of ecological risk that explicitly addresses uncertainty (USEPA, 1998)(330). Detailed steps of the ERA as proposed by (USEPA 1998)(330). -70- 2.4.4. Contributions of Ecological Risk Assessment to Environmental Decision Making At EPA, ecological risk assessments are used to support many types of management actions, including the regulation of hazardous waste sites, industrial chemicals, and pesticides, or the management of watersheds or other ecosystems affected by multiple nonchemical and chemical stressors. The ecological risk assessment process has several features that contribute to effective environmental decision making: - Through an iterative process, new information can be incorporated into risk assessments, which can be used to improve environmental decision making. This feature is consistent with adaptive management principles used in managing natural resources. - Risk assessments can be used to express changes in ecological effects as a function of changes in exposure to stressors. This capability may be particularly useful to the decision maker who must evaluate tradeoffs, examine different alternatives, or determine the extent to which stressors must be reduced to achieve a given outcome. - Risk assessments explicitly evaluate uncertainty. Uncertainty analysis describes the degree of confidence in the assessment and can help the risk manager focus research on those areas that will lead to the greatest reductions in uncertainty. - Risk assessments provide a basis for comparing, ranking, and prioritizing risks. The results can also be used in cost-benefit and cost-effectiveness analyses that offer additional interpretation of the effects of alternative management options. - Risk assessments consider management goals and objectives as well as scientific issues in developing assessment endpoints and conceptual models during problem formulation. Such initial planning activities help ensure that results will be useful to risk managers (USEPA, 1998)(330). 2.4.5. Factors Affecting the Value of Ecological Risk Assessment for Environmental Decision Making The wide use and important advantages of ecological risk assessments do not mean they are the sole determinants of management decisions; risk managers consider many factors. Legal mandates and political, social, and economic considerations may lead risk managers to make decisions that are more or less protective. Reducing risk to the lowest level may be too expensive or not technically feasible. Thus, although ecological risk assessments provide critical information to risk managers, they are only part of the environmental decision-making process (USEPA, 1998)(330). In some cases, it may be desirable to broaden the scope of a risk assessment during the planning phase. A risk assessment that is too narrowly focused on one type of stressor in a system (e.g., chemicals) could fail to consider more important stressors (e.g., habitat alteration). However, options for modifying the scope of a risk assessment may be limited when the scope is defined by statute (USEPA, 1998)(330). -71- Chapter III Socioeconomic and Environmental Aspects 3.1. Description of the Egyptian Mediterranean coastal environment 3.1.1. History and culture Some of the most ancient civilizations flourished around the Mediterranean. It was opened as a highway for commerce by merchants trading from Phoenicia. Carthage, Greece, Sicily and Rome were rivals for dominance of its shores and trade; under the Roman Empire it became virtually a Roman lake and was called Mare Nostrum (our sea). The city of Alexandria is located immediately west of the Nile delta and was founded by Alexander the Great 332-331 B.C. Alexandria is considered today one of the oldest, continuously existing cities of the world. It is the second largest city in Egypt and one of the major ports in the Mediterranean Sea, besides being an important commercial, business, industrial and cultural center. Furthermore, a number of submerged archaeological sites have recently been discovered off the Alexandria coastline, which is also the principle seaside resort of Egypt, attracting about two million visitors every summer. The city hosts four harbours: El-Diekhila Harbour, the Western and Eastern Harbour and Abu Qir Harbour (Frihy et al., 2004)(331). Alexandria has a deep rooted culture and heritage. The eastern harbor is separated from the western harbor, which is the main Egyptian commercial seaport; by a causeway leading to the Pharos Island that currently hold Kayet-Bay Fort, which is built on the base of the devastated old Alexandria Lighthouse (Morcos, 2003)(332) . With the opening of the Suez Canal in1869, the Mediterranean resumed its importance as a link with the East. The development of the northern regions of Africa and the oil fields in the Middle East has increased trade in the Mediterranean. Its importance as a trade link and as a route for attacks on Europe resulted in European rivalry for control of its coasts and islands and led to campaigns in the region during both world wars. Since World War II the Mediterranean region has been of strategic importance to the United States and, until its dissolution, the Soviet Union. 3.1.2. Climate The Mediterranean climate is subjected to both subtropical and mid-latitude weather systems, and climate is also partly influenced by the northern mountain ranges. The region is characterized by a windy, mild, wet winter and a relatively calm, hot and dry summer. Generally air temperature differences between winter and summer are limited to about 15, although local meteorological and geographic factors can result in extreme conditions, such as on the coasts of Libya and Egypt where the air temperature can reach 50 0C (EEAA, 1999)(283). Egypt has an area of 1.109 million km2. The climate is warm and dry. The rain is limited to the northern coastal area, while upper Egypt and the Red Sea Sinai mountainous area are flooded from time to time (UNEP, 2002)(286). Precipitation along the Mediterranean coast varies between 130 and 170 millimeters yearly and decreases gradually to the south. The tidal range is about 30 to 40 centimeters (EEAA, 2001)(333). The Mediterranean coast of Egypt experienced a successive increase in the amount of annual rainfall during the last three decades. The mean trend over the area is 0.76 millimeters per year. Rainfall has increased over the western coast of Egypt by up to 3 millimeters per year. The changes in the general circulation of the atmosphere and effects of some incidents, such as the North Atlantic -72- Oscillaiton phenomenon, seem responsible for this change. Increased intensity and frequency of marine storms will necessarily increase the risks of transportation accidents and health risks in the coastal zone (Susmita et al., 2009)(334). The amount of cloud cover has declined over most parts of Egypt except over western part of the North Coast. This decline has reached 0.02 Oct/ year. Relative humidity has increased in all parts of Egypt. The upward trend has reached 0.35% / year especially over southern part of Egypt. Mean-sea- level pressure has increased in recent years over most parts of Egypt. The positive trend has culminated to +0.05 hPa / year over southwest part of Upper Egypt (EEAA, 1999)(335). The Mediterranean coastal zone of Egypt is situated at the northern margin of the large hot and dry subtropical desert area of the Sahara and the Arabian Deserts. Winds from the Mediterranean are relatively cool and bring some moisture during the winter of the northern hemisphere. The combination of high temperature and low humidity leads to a high evaporation (especially during the summer) which far exceeds the spare precipitation. This clearly illustrates the importance of irrigation water from the Nile for agriculture in the delta region. Air pressure and sea water temperature correlate well with the seasonal variation of the mean sea level over a range of 0.17-0.19 m (Dewidar, 1997)(336). Depending on the atmospheric circulation in the Eastern Mediterranean including the Egyptian coast, three seasons have been distinguished: a-Winter season occurs from November to March, b - spring season extends from April to May and c-Summer season which covers the period from June to October (Hamed, 1983)(337). 3.1.3. Topography The Mediterranean zone is characterized by a wide flat coastal area along the sea and existence of Maryout plateau in the northwest area (Shata, 2000)(338). The shoreline between Salloum and Abu-Qir Bay is more or less straight with slight undulations forming small embayment. The depths of the continental shelf edge generally increase with increasing shelf width. The widest continental shelf in the southern Mediterranean is found in front of the Nile Delta, where a shelf more than 70 km wide has been built up by the sediments of the River Nile (Kamel, 2010)(339). The beach and coastal landscape west of Alexandria are one of the most attractive recreational sites in Egypt. The coastline is characterized by wide beaches consisting of white oolitic carbonate sand. The shore is generally linear with few protective configurations. However, the beach is not suitable for swimming because of the steep beach slope ranging 1:3 to 1:5. The beach is also characterized by hazardous rip currents (Nafaa and Frihy, 1993)(340). The shoreline of the Nile delta, from Abu Quir to Port Said, is typically of an arcuate coast. The delta beach and its contiguous coastal flat are backed by coastal dunes or by large lagoons. The three main Nile promontories at Rosetta, Burullus, and Damietta interrupt the sandy shoreline of the delta. The near-shore area is a hydrologically active zone characterized by a gentle slope varying from 1:50 to 1:100, and a dissipative wide beach (Nafaa and Frihy, 1993)(340). Meanwhile, the coastal zone of the Nile delta is presently undergoing extensive changes caused by both natural and anthropogenic influences (Stanley and Warne, 1993)(341). The Nile Delta shore consists of sandy arcuate beaches, approximately 240 km in total length. The beaches are backed by coastal flats followed by coastal dunes and three lagoons (from east to west, Manzala, Burullus, and Idko). With the exception of the sand dunes, the coastal plain is characterized by a low-relief surface <3.0 m above mean sea level. It has been designated as a vulnerable zone to the impacts of climate change and the expected rise in sealevel (El-Raey et al., 1999)(342). Assessment presumed that by the year 2100, the coastal belt with elevation below 1 m above sea level will be submerged (Stanley, 1988)(343). -73- The coastline of the Sinai Peninsula is sandy, smooth and interrupted by two protruding headlands at Port Said and the Bardawil-bulge coast. These headlands are separated by two large embayments, backed by sand dunes and lowlands made of saltpans (Sabkha). The bardawil lagoon is separated from the sea by a long, curved, narrow sand barrier. Three inlets connect it to the Mediterranean Sea. The whole coast is essentially unprotected except for the jetties built to stabilize the lagoon inlets, the fishing port at El Arish and the breakwaters of El Arish power plant (Frihy, 2001)(344). 3.1.4. Subsidence and sea level rise Local subsidence along the delta coast indicates that the entire northern Nile Delta coastal plain is subsiding with preferential northeastward tilting. A general trend of natural subsidence occurs along the northern Egyptian coast ranging from 0.4 to 5 mm/yr. This has been indicated from archeological evidence and from date core sections. On the basis of tide gauge records, recently reported a rate of subsidence of 2 mm/yr at Alexandria and 2.4 mm/yr at Port Said (Dewidar, 1997)(336). 3.1.5. Current The general pattern of circulation in the offshore area of the southern Mediterranean is from west to east, while in the nearshore area there are some deviations from this rule and some gyres and convergence zone exist (UNEP, 2002)(286). The surface circulation is dominated by an anticyclonic circulation off Salum Bay in winter, spring and summer. In nearshore areas, the current flows eastwards at the shallower levels and it flows westwards at the deeper levels. Off the Nile Delta, the current is almost eastward with a higher velocity in summer and autumn, while in spring it is very weak. Off the area between Port Said and Rafah, there is a clear cyclonic circulation appearing in all seasons except winter. At 50 and 75 m depth, the velocity of the circulation is weak. At 100 m depth, the circulation that appeared between Matruh and Alamen in summer decreases in area and magnitude at the former depths. At 200 and 300 m in winter, the current velocity is quite low. In spring the current flows southwards off the area between Rafah and Port Said. In summer, the current off the area between Port Said and Rafah is quite strong and flows to the south. The situation in autumn is quite similar to that in summer, except in the eastern area, where the current is a westward one. Investigation of the circulation pattern in the Egyptian Mediterranean water is obviously of great importance for discovering the distribution of coastal pollution and the possibility of intermediate water formation (Kamel, 2010)(339). 3.1.6. Wind movement The normal wind regime along the Mediterranean coast of Egypt is controlled by various atmospheric conditions that occur on a seasonal basis (Abdallah, 2006)(345). Along the Egyptian Mediterranean coast, winds blow predominantly (60-65% of time) from the directions from West to North. Speeds average 3-5 m/s in summer and spring; 5-7 m/s in winter with the higher velocities from North-Westerly directions (Dewidar, 1997)(336). According to Shata and Hanitsch (2006)(346) most stations have an annual mean wind speed more than 3.1 m/s except Damietta and El-Arish and the main wind direction over the Mediterranean Sea is north and northwest. The Mediterranean zone is windy. The wind speed has a maximum value of 6.3 m/s at Mersa Matruh in March, and a minimum value of 2.0 m/s at El Arish in October. This zone characterized by sea land winds. High wind speed occur in the winter and spring seasons. This may be due to the Mediterranean Sea secondary depressions (Salem, 1995)(347). -74- Mean monthly and annual wind speed (m/s) and its direction (at a height 10 m) (Shata and Hanitsch, 2006)(346) Month Annual mean Station Jan Feb Mar Apr May Jun Jul Aug Sep Oct Nov Dec Salloum 5.4 4.8 5.2 4.3 3.6 4.1 4.7 4.2 3.4 3.6 4.2 5.2 4.4 Sidi 5.6 5.7 5.9 5.7 4.7 4.6 5.2 4.5 4.0 4.2 4.6 5.6 5.0 Barrani Mersa 6.1 6.1 6.3 5.7 4.9 5.2 5.2 4.7 4.4 4.3 4.8 5.9 5.3 Matruh Eldabaa 5.5 5.8 6.1 5.8 5.1 6.0 6.0 5.6 5.0 4.2 4.5 5.5 5.4 Dekheila 4.5 4.6 4.9 4.8 4.3 4.5 4.6 4.5 4.2 3.7 3.8 4.1 4.4 Alexandria 4.4 4.4 4.6 4.3 4.0 4.0 4.4 4.0 3.7 3.1 3.4 4.1 4.0 Balteam 3.6 3.5 4.2 4.0 3.5 3.7 3.9 3.6 2.8 2.3 2.6 3.3 3.4 Damietta 2.8 3.1 3.7 3.6 3.1 3.1 2.8 2.5 2.3 2.5 2.5 2.9 2.9 Port Said 4.8 5.2 5.8 5.4 4.8 4.6 4.3 3.8 3.8 4.1 4.3 4.3 >4.6 El-Arish 2.5 2.9 3.0 2.5 2.4 2.4 2.3 2.1 2.2 2.0 2.1 2.4 2.4 -75- Wind direction 330 NW 330 NW 330 NW 330 NW 360 N 330 NW 330 NW 330 NW 360 N 330 NW 3.1.7. Waves Information on Mediterranean waves is available from observations on ships plying the Eastern Mediterranean (Hogben et al., 1986)(348) and from observations on a platform in almost 20 m of water depth in Abu Qir bay (Nafaa and Frihy, 1993)(340). Dominant wave periods are 5 to 8 seconds; extremes reach 10 seconds and more. The height and direction of the wave are affected by refraction, dissipation of energy and breaking during their propagation into shallow water near the coast. The effect depends highly on the local bathymetry which may allow only a limited window of directions to reach a certain location. These processes explain why about 70% of the waves arrive from between WNW and NNW at the location in Abu Qir Bay. The directional distribution of the wave energy along the Mediterranean Sea generally leads to a clockwise rotation of the local dominant wave direction (and to a decrease of the wave energy) as the perpendicular to the local part of the coast turns from NW to NE. The wave direction, however, always trails behind the perpendicular. This cause a resultant eastward longshore direction of the wave energy along the coasts, except in the eastern part of Abu Qir Bay, in the "shadow" of the Rosetta promontory (Wobber, 1967)(349). 3.1.8. Tides and storm surges The tidal variations of the Mediterranean Sea level are small with a range of about 0.15 m during neap tides and 0.3 m during spring. Extreme astronomical deviations from mean sea level are 0.3 to 0.4 m. The tide is slightly higher in Alexandria than Port Said. Winds and other meteorological phenomena cause deviations from the astronomical tides, leading to the occurrence of higher levels. (Delft hydraulics, 1992)(350). The tides along the Nile Delta coast are semi-diurnal in nature with two high and two low water levels in a tide day (El-Fishawi and Fanos, 1989)(351). Storm surges during winter season and swell action during summer season (Manohar, 1976)(352) may cause the increase of the water levels considerably and hence accelerate erosion along the coasts (El Fishawi and Khafagy, 1991)(353). 3.1.9. Hydrology Different water masses are found off the Egyptian coast: a surface water mass of high salinity, a subsurface water mass of minimum salinity and maximum oxygen content of Atlantic origin that extends below 50-150 m, an intermediate water mass of maximum salinity extending below 150 m to about 300-400 m depth, and deep waters of Eastern Mediterranean origin (Said and Karam, 1990)(354). Generally, the eastern part of the Egyptian Mediterranean has higher surface temperature vary between 18.12 0C in spring and 24.3 0C in summer, decreasing with depth. The surface salinity varies between 39.05 psu in summer and 38.61 psu in winter. The highest values of surface salinity observed in the offshore water. The maximum average of vertical salinity observed in summer (39.13 psu) with the minimum value (38.63 psu) found in winter. The vertical salinity values increased to 50-75 m depth, below which the salinity was almost constant (Lascaratos et al., 1999)(355). Annual evaporation exceeds rainfall and river runoff over most of the Mediterranean Sea, so that in general the Sea is characterized as having very high salinity (around 38 psu). This highly saline water flows along the bottom of the Strait of Gibraltar and out into the Atlantic Ocean, where it can be traced throughout the central Atlantic. On the other hand, relatively less dense Atlantic water flows into the Mediterranean Sea in a surface layer. This incoming Atlantic water is eventually turned into dense Mediterranean waters through -76- evaporation. The water sinks into the deep Mediterranean Sea, due to winter cooling, and exits the Mediterranean through the bottom of the Strait of Gibraltar. This cycle takes between 100 and 300 years. Tidal amplitudes in the Mediterranean Sea are small and the narrow continental shelves prevent tidal amplification along the coast (Tomczak, 1994)(356). 3.1.10. Biological diversity The Mediterranean Sea can be characterized as having low biomass per-unit volume, due to low nutrient levels, but high diversity, with over 10,000 marine species observed and with a large proportion (28%) of them endemic. Although no species disappearance has been reported in the Mediterranean Sea, changes in species composition and richness have been determined for some areas, including the introduction of exotic species (e.g. the massive introduction of tropical species from the Red Sea after the opening of the Suez Canal). Currently, there are several endangered species reported in the Mediterranean Sea, including the Monk seals, red coral, sea turtles and colonial water birds. One of the most important habitats in the Mediterranean Sea is the large seagrass meadows (Posidonia oceanica) that occur at depths down to 40m in the western and eastern basins (EEA, 1999)(283). 3.1.11. Ecosystem features The main features that characterize the ecosystem of the Egyptian Mediterranean coastal areas are: 1. Seasonal variations in water salinity ahead of Nile Delta River, during the autumn and winter seasons. The water-salinity values are mostly lower (average surface-water salinity = 38.4 psu) than for the surrounding offshore area (average surface water salinity = 39.1psu). 2. Estimated N:P ratios have higher values during winter (N:P range = 45–60) compared with other seasons (N:P range = 5–15), indicating phosphorus as a limiting factoring in winter. In contrast, the western side of the Nile Delta River is nitrogen limited during the other seasons. 3. Both algae biomass (chlorophyll-a), and zooplankton standing crop values have higher concentrations (averages=4.5mg gm-3, average=3×103 Ind. m-3, respectively) during the winter season compared with the other seasons (range = 0.5–1.5 mg m-3, range = 1–2 × 10-3 Ind. m-3, respectively). 4. A marked algae bloom in winter is mainly localized around the Nile Delta River and extends eastward. It is also important to mention that, seasonal primary productivity distribution in this area have high values during the autumn and winter seasons (average = 6.0 and 3.25 mg C m-3, respectively) compared with the other two seasons (range = 0.5–1.5 mg C m-3) (Dowidar, 1988)(357). 3.1.12. Water quality Egyptian Coastal Water Environmental Monitoring Program is one of the sustainable programs which the MSEA and EEAA are adopting to monitor marine and coastal environment area status. Within this program marine samples from selected stations along the Egyptian coasts are collected and analyzed four times a year in March, May, July and September so as to represent physical, chemical and biological conditions in the four seasons. The program, implemented in collaboration with specialized stakeholders in Egypt, focuses on the monitoring of bacterial counts and nutrient salt concentrations (ammonia, nitrates, nitrites, phosphorus and chlorophyll). In addition, other hydro-geographic measurements are also made they might help in explaining phenomena affecting marine environment conditions. According to the results of the 2010 (the study year) monitoring program there was an increase in the concentration of dissolved oxygen in sea water observed (higher than 4 mg/l) from El-Salloum to Rafah. The results were higher than the results obtained during the cruise -77- of 2009. The Salinity varied between 28.15 psu to 39.28 psu. Regarding water transparency, the highest transparency level was found in the western zone extended from El-Salloum to El Bitash (west of Alexandria) and the eastern zone extended from El Arish to Rafah, whereas, the lowest level was found in front of Nile Delta as well as drainage and lakes exists. The hydrogen ion concentrations in sea water, samples results ranged from (6.3 to 7.2) which was within the normal level of sea water. Temperature ranges from 19.8 to 31 C0 which was within the normal level of sea water. The results of nutrient salts and chlorophyll-a concentration in the Mediterranean Sea were as follows: There was a relatively decrease in the concentration of total nitrogen during the four crises. The highest value (0.29 mg/l) was observed at Port Said station during May 2010 and the lowest value (0.054 mg/l) was observed at Baghoush Station during September 2010. Comparing the results of total nitrogen during (2007-2010) there is a relatively decrease in total nitrogen concentration. The concentration of ammonia was relatively low at all stations during the year. The highest value was observed at Port Said Station (0.44 mg/l) and the lowest value was (0.003 mg/l) at Baghoush station. There was a decrease in the concentration of ammonia during 2010 comparing with the results of ammonia obtained during the period from 2008-2010. The lowest value (0.23 µg/l) of chlorophyll was obtained at the reference station in Baghosh and the highest values (15.05 and 13.03 µg/l) were obtained at Port Said and El-Gamil west stations, respectively. There was a decrease in the concentration of chlorophyll a at the year 2010 comparing with the concentrations obtained during the period from 2008-2010. The concentration of nitrite was very low at all stations. The highest value (0.03 mg/l) was found at the Eastern Harbour and the lowest value (0.001 mg/l) was found at El-Salloum station. The concentration of nitrates ranged from (0.007 to 0.115 mg/l). The total phosphorus was very low and ranged from (0.015 to 0.078 mg/l). The highest value was observed at El-Mex station and the lowest value was observed at the reference station at Baghoush. Different patterns of fecal contamination ranging between very clean stations such as Salloum, Baghoush and Rafah and other clean stations where the number of bacteria did not exceed the permissible limits. El-Dikhaila, El-Mex, Western Harbour, Eastern Abu Qir, Rashid, El-Bourg showed high level of Faecal contamination caused by the discharge of agricultural run off or sewage discharge or both in these areas (EEAA/EIMP, 2011)(358). 3.1.13. Sediment characteristics The Egyptian Mediterranean coast contains a wide variety of sediments. Coastal sediments are mainly composed of two principal types: carbonate sands and quartz-dominant sands (Hilmy, 1951)(359). The western region from Mersa Matrouh to Alexandria is mainly composed of pure oolitic carbonate (Anwar et al., 1984)(360). The oolitic grains constitute an average of 78% and 89% of the bottom and beach sediments, respectively. Further westward, sand at Salloum showed an average oolite content in the nearshore of 58% (Anwar et al., 1981; Nasr et al., 1978)(361, 362). Beach sand from Alexandria to Rashid primarily consists of quartz grains with common shell fragments (Hilmy, 1951)(359). The Nile River has been identified as the major source of quartz-rich sediments and heavy minerals on the Nile Delta beaches (Frihy, 1994)(363). As a result of the current erosion affecting beaches along the Nile delta, the eroded shorelines are characterized by high density minerals, whereas the accreted shoreline is characterized by low density minerals (Frihy et al., 1997)(364). Black sand deposits are extensive along the beaches of Rashid on the Egyptian Mediterranean coast (Saleh et al., 2004)(365). These black sands contain some important minerals such as zircon and monazite -78- (El-khatib and Abou El-khier, 1988)(366), both of which contain uranium and thorium in their chemical structures. High background radioactivity values at Rashid have been detected as a result of these black sands (El-Gamal et al., 2004)(367). Grain size analysis of El-Salloum yellow sand documents discrete size groups extending from gravel to fine sand. This sand is characterized as bimodal sediments predominantly in the fine sand size class. Alexandria, Matrouh, and Rashid sands are all characterized as unimodal sediments in the medium sand class size (El-Gamal et al., 2010)(368). 3.2. Economic Activities of the Egyptian Mediterranean coastal area The coastal area of Egypt on the Mediterranean Sea extends for about 1,200 km. It hosts a number of important residential and economic centers, like the cities of Alexandria, Port Said, Damietta, Rosseta, Matruh, and Al-Arish. The coastal strip between Alexandria and Matruh hosts tens of tourist villages, which are usually crowded by visitors during summer. Many activities are known in the coastal area, including fishing, industrial, tourism, trading and agricultural, oil and gas production, and transportation (Dorgham, 2011)(369). Highest population centers (25 million, i.e. 38% of the total population) are found at the coastal zone of Alexandria and Nile delta. The Nile river delta contributes 30–40% of agricultural production and 60% of fish catch (marine and lagoonal). Most of the fertile soils of the Nile delta are used for agriculture, irrigated by the water supplied from the Nile system. Lands near the lagoon margins, especially at locations with low elevation, have been reclaimed for the purpose of agriculture and fish farms exist. Half of Egypt’s industrial production comes from the delta, mainly from Alexandria. Main commercial ports are located at El Diekhila, Alexandria, Abu Quir, Idku, Damietta, Port Said and east of Port Said. The beaches of the Nile delta are little used whereas Alexandria coast is totally used as public resort summer beach. Main delta resort beaches are located at Gamasa, Baltim, Ras El Bar, El Gamil and Port Said. A coastal road was recently completed to connect the delta region with west of Alexandria and Sinai. In the Nile delta few people live below1 m contour, whereas populations are usually concentrated on ground more than 2 m above sea level, especially on the raised present or past alluvial channels (Sestini, 1990)(370). Commercial and industrial centers are situated above the 3 m-contour line. Economic activities in the coastal zone include agriculture, industry, fishes/aquaculture and recreation beaches are denoted in the following map: Map of the lower Nile delta showing (A) main anthropogenic features below and above mean sea level up to 4 m contour and (B) distribution of main socioeconomic elements across lower Nile delta coastal plain. -79- The coastal area may be roughly divided into three units, in accordance to the presence of the hot spots, sensitive areas and main geomorphologic characterization. The main unit is the central unit between Alexandria (west) and Port Said (east), including the Nile Delta, coastal lakes (lagoons) and wetlands, and stretched along the boundaries of six governorates. The second unit, to east from the central unit, extends from Port Said to Rafah (north Sinai Governorate), while the third unit, extends from Alexandria westwards to Salloum (Mersa Matruh Governorate). Associated with the Nile Delta are the coastal lakes and wetlands, which represent another important feature of the Mediterranean coast of Egypt. These lakes and wetlands cover a total area of at least 280,000 hectares, representing more than 25% of all natural and semi-natural wetlands of the entire Mediterranean region. Many areas in the Mediterranean coast are used for recreation by the public. The Mediterranean Coastline and coastal lakes are also major sources of fishery resources in Egypt (Barakat et al., 2011)(371). 3.2.1. Population Egypt is located in the north-eastern corner of the African continent with an area about million square kilometres. It is considered a developing country burdened by the scarcity of natural resources associated with extreme population growth (over 70 million people in total). The Egyptian terrain consists of a desert plateau interrupted by the Nile valley and delta. It is located in an arid - to semi-arid zone. The coastal zone of Egypt extends for more than 3,500 km and 40% of the population live there. Most of these people live in and around a number of major industrial and commercial cities: Alexandria, Port Said, Damietta, Rosetta, and Suez (El-Raey, 1999)(372). The coastal zone is home to several highly populated economic centers, such as the cities of Alexandria, Damietta, Hurgada, Port Said, Suez, and Sharm El-Sheik (EEAA, 2006)(373). Given the country's geography and the concentration of population and economic activities in the Nile Valley and the Nile Delta (almost 99%), Egypt faces environmental pollution problems, affecting the health of the population, and the poorest sections are exposed the most. Inadequate sewage disposal, uncontrolled industrial effluents, extremely uneven population distribution, and shortage of arable land, have created major water pollution problems (DG Environment European Commission, 2006)(374). The pressure of the human activity on the coastal resources of the Mediterranean and Red Seas are very intense. The Egyptian coasts receive the impact of the major part of the country's population. The enormous urban population and adjacent already formed agricultural lands, all, contribute to the pollution load reaching coastal waters, weather direct like the Alexandria region or via coastal lagoons (such as lake Manzala which receives the major part of the Cairo mixed waste water). Egypt industry also contributes to the pollution load in the coastal waters (UNEP, 2002)(286). Alexandria Governorate extends for about 75 km along the Mediterranean coast of Egypt. It is the main harbor of Egypt were 60% of the country's exports and imports going through it (Beltagy, 2009)(375). Alexandria covers an area of about 2758.4 km2 and the widest part of the city ranging from 4 to 5 km length (Abdrabo et al., 2002)(376). The population of Alexandria, according to the 1996 Census, reached a total of 3.33 millions (CAMPS, 1996)(377), compared to 2.917 millions in 1986 (CAMPS, 1986)(378). This means that a population increase rate of about 14.1% over a decade. The population of Alexandria, according to the 2004 Census, reached a total of 4.30 millions (CAMPS, 2004)(379), compared to 3.33 millions (CAMPS, 1996)(377). This means that a population increase at a rate of about 30% through 8 years. Being the first summer destination in the country, if receives an extra -80- of 1, 500, 5000 visitors in this season. Administratively, the Governorate is divided into six districts (Beltagy, 2009)(375). Port Said Governorate lies at the northern end of Suez Canal with a total area of 1, 344, 96 km2 and a populated area of 1,320.68 km2. It's bounded by North Sinai Governorate to the east; Damietta Governorate to the west; Lake Manzalah, Dakahlia, Sharkia and Ismailia Governorates to the south. The total population was 529,684 inhabitants in 2004. Administratively, the Governorate includes 7 districts. Activities in the Governorate are diversified as they range from agriculture, industry, to maritime services and shipyards. (Beltagy, 2009)(375). 3.2.2. Main activities sectors Agriculture More than 95% of Egypt's population and all of its agriculture are concentrated in < 5% of Egypt's land, along the banks of the Nile and throughout the 25,000 km2 Nile delta. For more than 5,000 years, Egyptians depended on the annual fall flooding on the Nile, which irrigated and fertilized the floodplain and eventually discharged to the Mediterranean Sea (Oczkowski et al., 2009)(380). Agriculture contributes 17% of the country's GDP and is the largest source of employment, constituting 30% of the labor force. About three fifths of the country's agricultural production is the low lying delta in close proximity to the Idku, Burullus, and Manzalla lagoons (Agrawala et al., 2004)(381). In the northeastern part of Nile delta the most important crops by cultivated area: clover, maize, cotton, wheat, rice, sunflower, sugar beets and soya beans, are the predominant cops of the lower coastal zone (< 2 m) (Sestini, 1992)(382). Tourism Tourism currently represents 11.3% of Egypt's GDP, 40 percent of total noncommodity exports, and 19.3% of foreign currency revenues (EEAA, 1999)(335). The Northwestern Coast of Egypt extends for about 500 km along the Mediterranean Sea from Alexandria to El-Salloum, near the Libyan border. This coast is well known in Egypt as a splendid summer resort, including numerous new tourist resorts. On the level of government policy, tourism is placed very high in development goals where the tourism sector represents about 25 % of economy sectors in Egypt. In opening up the Northwestern Coast, Egypt would enter the highly competitive beach-oriented Mediterranean tourist market, and an important part of population could be absorbed in this zone (Rabenau., 1994)(383). The northwestern coast of Egypt is distinct by white oolitic carbonate sand, clear blue water, mild weather and sun prevailing most of the year. All these privileges made this coast an attractive site to be developed rapidly for tourist and entertainment activities and for recreational uses. El-Allamien Marina large scale recreation summer tourist center is one of these rapidly developing areas on this coast at kilo 94 on Alexandria Matrouh coastal road (Iskander et al., 2008)(384). In addition to international tourism, the coastal cities of Alexandria, Bulteem, Gamasa, Port Said, and Ras El-Bar are popular destinations for local tourists, and many middle and low income Egyptian spends their summers in these towns (ElRaey, 2010)(385). The main resort at the northern part of the Nile Delta is Ras El Bar resort (Dewidar, 1997)(336). Port Said Governorate considered free trade zone and play a good role in import and export business. Also, there are some touristic sites such as, Delecips monument, Army -81- Museum, resort beaches and Suez Canal (Dewidar, 1997)(336). The coastal zone of Port Said area is socioeconomically important to most of the population in this area. Tourism is primarily oriented toward swimming and sunbathing. Therefore, the coast, its slope, and the quality of beach and sea are of prime importance to this industry. Most tourist facilities such as hotels and youth camps are located within 200 to 300 m of the coast. There are also important archaeological sites along the northern part of the Suez Canal (El-Raey et al., 1999)(342). Industrial and commercial activity Half of Egypt’s industrial production comes from the delta, mainly from Alexandria. Main commercial ports are located at El Diekhila, Alexandria, Abu Quir, Idku, Damietta, Port Said and east of Port Said (Sestini, 1990)(370). Many industrial activities, including petroleum and chemical production, and important tourism centers are located along the coasts. Trading and transportation networks and a large number of harbors are also found on the coasts (EEAA, 2006)(373). The Mediterranean coastal shoreline of Egypt includes five large lakes, which constitute about 25 % of the total wetlands in the Mediterranean region. This coastal zone has a large number or economic and industrial centers, as well as important beaches and tourist resorts (EEAA, 2001)(333). The Mediterranean coastal zone is the site of Egypt's second largest city, Alexandria, which is the country's main harbor. Located on the western side of the Nile Delta, the city sits partly on low elevation land. Alexandria is home to about 40 percent of the country's industrial capacity, in addition to being a prominent summer resort. The western harbour is heavily polluted receiving several extended and internal pollutants from various sources. The major plants and other sources discharging their wastes into the western harbor are Misr chemical Industry, Portland cement factory, discharges from Noubaria canal, effluents from Mex pumping station, cement packing unit discharged wastes from vessels during unloading and loading of the exported and imported industrial raw materials and domestic wastes discharged from the city of Alexandria (Saad et al., 2003)(386). Abu Qir drain recieves and discharges industrial wastewatres from 22 different factories of food processing and canning, paper industry, fertililzer industry and textile manufacturing (Abdeloneim and Shata, 1993)(387). El-Mex bight recieves the industrial wastes from the nearby chemical industries, chlor-alkali plant and Alexandria petroleum company (Ezzat et al., 1985)(388). Other large cities in the northern low-lying Delta region include Rosetta and Damietta. Port Said is an important regional trading center on the Suez Canal to the eastern side of the delta (El-Raey, 2010)(385). The main income of this governorate depends on revenue from Suez Canal, tourism, free trade zones and industrial activities. The industrial activities of Port Said include food canning, cloth making, carpet weaving, and the leather industry (IDSC, 1995)(389). The Nile Delta region in the Mediterranean coastal zone represents the major industrial, agricultural, and economic resource of the country. It is home to over 50 % of Egypt's population of 80 million and to about 70 % of the nation's industrial and commercial activities (EEAA, 2009)(390). Damietta is an industrial center known for its furniture, leathers, textile and sweets industries in addition to dairy products and rice mills and for its agricultural heritage. It is also a fishing industry town, with one of the largest fleets on the Mediterranean which accounts for fully half of the fishing boats of Egypt (Faragallah et al., 2009)(311). Fishing activity The coastal zone is an important source for fisheries, providing income and food security, the annual production of fish is about 875,990 tons, of which 116.560 tons (13.3 % -82- of the overall production) are from the coastal waters (EEAA, 2006)(373). Approximately 60% of Egypt's annual fish catch are from three main Delta lagoons, namely Idku, Burullus and Manzalla. Fishing is mainly done by trammel net and various primitive methods (e.g. catching by hand and collecting fishes under vegetation using a cone shaped net). Aquaculture is the largest single source of fish supply in Egypt accounting for almost 51% of the total fish production of the country with over 98% produced from privately owned farms; most aquaculture activities are located in the Nile Delta Region with fish farms usually found clustered in the areas surrounding the four Delta lagoons. Fish hatcheries are also generally located in the vicinity of the fish farms. Pollution, reclamation, fragmentation, over fishing and illegal harvesting of fish fry are the major environmental issues threatening the fragile ecosystem of the northern lagoons (UNDP, 2009)(391). The Egyptian Mediterranean coast is about 1100 km, extending from El-Sallum in the West to El-Arish in the East. The mean annual fish production from this area does not exceed 45,000 tons (1984-2005) General Authority for Fish Resources Development). There are 3 fishing methods conducted in the Egyptian Mediterranean: trawling, purse-seining, and long-lining by hand. The fishing grounds along the Egyptian Mediterranean coast are divided into 4 regions: Western region (Alexandria and El-Mex, Abu-Qir, Rasheed, El- Maadiya, and Mersa Matruh), Eastern region (Port Said and El-Arish), Demietta region, and Nile Delta region. The Port Said region is one of the most productive fishing grounds, constituting 24% of the total fish production in the Egyptian Mediterranean (Mehanna, 2007)(392). The main fishing ground in the Egyptian Mediterranean water is the continental shelf in front of the Nile Delta. Inshore fisheries widely exist with artisanal fishermen along the coast. Fishing fleet is consisted from 3129 boats from them 1095 boat are trawlers varies in length from 15 to 28m and in engine power from 50 to 850hp. Italian type bottom trawl net is common with cod end mesh size about 2cm, they targeting shrimp, cuttlefish, red mullet and different bream species. The continental shelf is generally fairly heavily exploited, trawl catch target small size fishes that requested by the market. Discards and by-catch species are the majority of the catch. Managements measurements are necessary include increasing mesh size and modify of net design for conservation of the Egyptian fish stocks (Gaber and El-Haweet, 2011)(393). Fish farming is growing in importance and is sponsored both by local government and Ministry of Agriculture. In Manzala lagoon there is also a considerable number of private frame, consisting of seasonally opened and closed basins (hoshas). Aquaculture farm is concentrated around the southern margin of Idku and Manzala lagoons and Maryut valley. Aquaculture production accounted for about 15% (62,000 t) of total fish production in 1995. Tilapia represents about 38% (129,000 t) of total fish production in 1994 (CAPMS, 1994)(394). The Egyptian Mediterranean fishing fleet Official statistics for the year 2004 (source: The Egyptian Fisheries Statistics 2004, The General Authority for Fish Resources Development, The Egyptian Ministry of Agriculture) reported 3027 fishing vessels with license registered in ports of the Mediterranean coast. However, no data were available about the western area. So, the real number of vessels is higher. Vessels are typically small, with exception of trawlers. During the interviews with artisanal fishermen in the western and eastern regions, they stated that they set the nets perpendicularly to the beach. The length of the net might range 80 to 400 meters. The net is left in the water from 8 hours to 2-3 days. -83- Number of vessels by fishing gear in 2004. Region Western Alexandria Central Eastern (Sinai) Fishing community El salloum Marsa Matruh Sidi Barani El Hamam El-Mex Anfoushi Abou Keer Total El Maadiya Edko Rousata Borg El Borolos Azzbat El Borg Domiat Total Port Said Lake Bardawil Areash Total Total Trawlers Longliners Purse seiners Set net Others total No licenses were given n the year 2004 42 192 8 48 1 291 48 90 115 107 16 614 852 208 208 1150 209 401 87 69 190 207 553 155 11 166 1120 15 23 36 28 22 16 102 39 56 95 220 140 188 101 75 1 9 186 0 347 1 5 5 157 157 163 412 703 339 0 279 229 851 0 1698 402 0 224 626 3027 3.2.3. Land use The construction of the International Coastal Highway which is located parallel to the Mediterranean shoreline, is expected to cause changes in land use /land cover. A remarkable set of wetlands is located near the coast, which, include wet Sabkhas, dry Sabkhas, and Lake Maryiout splinters. Land use in the hinterland has different trends. The local people (Bedouin) living in this region utilize natural vegetation for pasturing within some scattered cultivation in the terrestrial inland (Mohammed et al., 2000)(395). Some urban growth takes place around Lake Maryiout shorelines, mostly at the expense of the wetlands. A trend to future expansion and land use changes due to tourist sites and summer resorts along the coast is also obvious (Kaffas et al., 2000)(396). Urban and industrial expansion in Alexandria is physically restricted, by the sea on one side, and by Lake Maryut and agricultural land on the other side. This narrow strip of land is now a continuous sequence of high rise buildings. Port Said has a great potential as a commercial and industrial center at the north entrance of the Suez canal, but expansion has been limited by lack of land, being squeezed between the sea and two lagoons (Dewidar, 1997)(336). The coastal zone west of Alexandria is characterized by intensive development of new settlements of touristic villages. These recreational projects create potential problems resulting from increasing human pressure and man made interventions. These recreational projects were built without environmental impact assessment. Unexpected impact have changed the shoreline stability and expected to alter the water quality of sea (Dewidar, 1997)(336). The Port Said Governorate has a unique geographical location. It is located in a prime position for national and regional development. In addition, it is considered an extension of the Gulf of Suez and is close to the development in Sinai. Port Said has valuable resources suitable for tourism development such as the Mediterranean Sea and the Read Sea beaches, -84- lakes, protected areas and historical and archaeological sites. The economic policy and potential use of the land accelerates the growth of the governorate. Therefore, Port Said has quickly become the third largest urban governorate in Egypt with respect to population size. By the beginning of the 1980s, the East Port Said harbour was constructed to help maintain fuelling stations for ships passing through the Suez Canal waterway as well as a summer resort for Egyptians. El-Malha Lake represents a valuable natural resource for tourism development which will require infrastructure and productive wetlands. However, land use conflicts already constrain tourism development of the El-Tina plain. These conflicts prevent establishment of any significant comprehensive tourism activities along coastline and adjacent areas. These conflicts may also discourage investors from supporting development plans (El-Bastawisy et al., 2006)(397). 3.2.4. The economic importance of the coastal lakes Five water bodies lie adjacent to the Mediterranean Sea on the fringe of the Nile Delta; Lake Mariut, Nozha Hydrodrome, Lake Edku, Lake Brollus and Lake Manzalah. The current configuration of these lakes is changing rapidly, due to the natural processes and man's activities (Saad, 1990)(398). Contrary to the first two lakes, the latter three ones are connected to the Mediterranean Sea. The main water supply to the Delta lakes comes from the contaminated agricultural drains. However, the Hydrodrome is fed with the Nile water (Saad, 1974)(399). Lake Mariut, located SW of Alexandria, is the heavily polluted lake in Egypt and its water is pumped to the sea. It is now divided artificially into four basins and the area of the lake proper reaches 27.3 km2 and its depth ranges from 90-150 cm. The Nozha Hydrodrome was isolated from Lake Mariut. It has an area of 5 km2 and average water depth of 3 m. Lake Edku, situated at 30 km NE of Alexandria, has an area of 126 km2 and water depth ranging from 50-150 cm. Lake Brollus, situated between the two Nile branches, has an area of 420 km2 and water depth varying from 70-240 cm. Lake Manzalah, the largest Delta lake, is lying in the eastern region of the Nile Delta. Its area had been reduced to 1200 km2 by 1980 (Meininger and Mullie, 1981)(400). The coastal Delta lakes are used for fishery, water supply for agriculture and industry. The fish population in these lakes is comprised from fresh and marine water fish species. Many of the latter migrate for feeding in these lakes through their connections with the sea (Alsyes and Soliman, 1993)(401). These lakes are situated on the Mediterranean Coast of the Delta and cover about 6% of the non-desert surface area of Egypt. The lakes are an important natural resource for fish production in Egypt, until 1991, these lakes have always contributed more than 40% of the country's total fish production, but at present this has decreased to less than 12.22% (GAFRED, 2006)(402). Tilapia species including Oreochromis niloticus, Oreochromis aureus, Sarotherodon galilaeus and Tilapia zillii ranked first followed by Clarias gariepineus in the fish production of the lakes (Saeed and Shaker, 2008)(323). In the meantime, the lakes were subjected to a gradual shrinkage during the past few decades due to land reclamation and transformation of significant parts of the lakes to fish farms, particularly along the southern regions. In addition, large parts of the lakes are overgrown with aquatic vegetation which reduces the open water to nearly half of its total area, speeding up the process of land transformation (Saeed and Shaker, 2008)(323). These lagoons are considered as reservoir for agricultural, industrial, and municipal wastes, which are discharged from surrounding cities and cultivated lands. The Egyptian -85- Mediterranean coast receives huge volumes of waste waters every year through coastal lagoons and from other land based effluents. These wastes are loaded by variable amounts and types of pollutants, in addition to great amount of nitrogenous and phosphorus compounds, which in turn cause high level of eutrophication along a significant part of the Mediterranean coast, particularly of both the Nile Delta region and Alexandria coast (Dorgham, 2011)(369). 3.2.5. The economic importance of the Egyptian Mediterranean ports There are three main Egyptian ports on the Mediterranean; Alexandria ports, Port Said and Damietta port, beside a number of terminals for oil transportation. Alexandria hosts three harbors: namely the Western Harbor, which is the main harbor of the country, El'Dekhiela Harbor just west of the Western Harbor, and the Eastern Harbor (fishing and yachting). It also hosts about 40% of the country's industries (Beltagy, 2009)(375). Alexandria port overlooks the Mediterranean in the north east of Africa and is considered as the main port of the Arab Republic of Egypt. It is 4.8 km long and is 2 km wide at its widest point. It covers 8.5 km2 of water surface area (EMDB, 2003)(403). Alexandria Port is situated on the north coast of Egypt, west of the Nile Delta, approximately 200 km from Cairo. It is the main port in Egypt (Abdrabo et al., 2002)(376). Alexandria port covers capacity of production 23.7 million ton / year, ship size 15000 gross weight and 14 berths for petroleum, oil, fertilizers, cement, coal, and molase. The tankers of oil terminal specified for the supply of the ships operating the port is considered as one of the possible main sources of oil pollution of the port (APA, 2005)(404). The Western Harbor receives the vast majority of Egyptian external trade. It is considered as one of the most important and biggest harbors in the Mediterranean Sea from the economical point of view (Saad et al., 2003)(386). The western Harbor of Alexandria is the major trade port of the Northern Territory of Egypt. Industrial activities have increased dramatically in this area over the past 20 years. The harbor handles approximately 75% of all ship-borne cargo of the country. As a result of aggressive urbanization and industrialization of the Alexandria region, the coastal waters in general and the Western Harbor in particular have received considerable amounts of treated and untreated industrial, agricultural and domestic wastes (Salem and Sharkawi, 1981)(299). The Eastern Harbor is the most important embayment on the Mediterranean coast for Egypt as well as for the world heritage, since it contains thousands of the ancient Egyptian artefacts which encourage the idea of establishing a natural museum of underwater archeology in the harbour. It is a relatively small semi-closed basin on the central part of Alexandria coast, occupying an area of 2.53 km2, with an average depth of 6m. The harbour is isolated from the open sea by a high thick breakwater, but connecting to the sea through two narrow openings, Qayet Bey (Boughaz) and Silsila. The harbour is exposed to several kinds of human activities, including fishing, yachts port, anchoring offishing ducks and ships, landbased effluents, boat building workshops, and recreation (El Rayis and Hinckley, 1999)(405). El-Dekheila Port is the second largest port in Alexandria city. The port of El-Dekheila is situated at 5 km west of Alexandria harbour. Dekheila port is a natural extension to Alexandria port; constructions started in 1980 and the port became operational in 1986 with the operation of the minerals berth. Dekheila port takes the place of the former airport westward Alexandria Port, 7 km distanced from sea and 10 k m from land. El-Dekheila is an extension to the port of Alexandria, it is newly constructed to accommodate and operate bigger draft and size ships. It started to operate in 1986 and still under completion (EMDB, -86- 2003)(403). El-Dekheila port was planned to serve Alexandria Iron and Steel factory. It lies to the east of El-Agami head and to the west of El-Mex Bay (Abd-Alla et al., 1995)(406). The area of the port is situated on the north coast of Egypt, west of the Nile Delta, approx. 210 km from Cairo. El-Dekheila and Alexandria Port are the main port in Egypt. El-Dekheila is located at the north east of the Mediterranean and is considered as the main port of Alexandria. It covers total area of 6 km2, 2.74 km2 of water and land area of 3.2 km2. The capacity of productivity is 15 million ton/year, ship size is 17000 GRT and 15 berths for minerals, oil, grain, containers, multi-purpose (EMDB, 2005)(403). Port Said is situated at the end of the Suez Canal on the Mediterranean Sea and is around 4.8 km long and approximately 0.8 km wide with a water surface of about 2.8 km2. Suez port is situated at the end of the Suez Bay with a water surface of about 2.85 km 2 including Adabia port. The Suez Canal is connected to the water surface in the south and the ship's waiting area for those crossing the canal in the north. Port Said Port is situated on the Northern entrance of the Gulf of Suez. It is considered one of the main Egyptian ports due to its distinguished location at the crossroad of the most important world sea trade route between East and Europe via Suez Canal, and the most extensive transshipment port in the world (EMDB, 2003)(403). Damietta Port is situated 8.4 km west of the Nile estuary of Damietta branch westward Raas El-Bar, and it is 70 km distance from Port Said with a water surface of about 3.2 km2 (EMDB, 2003)(403). The economic contribution of the ports and economic impact value of trade passing through Egyptian ports consists of four components: 1- foreign trade (imported and exported cargo) 2- ship calling and passengers 3- containers handling 4- customers duties Egypt's major ports handled 95.4% of Egyptian's waterborne trade in 2004 and 91.8% of all Egypt container trade. Between 1994 and 2004 the containers volume at Egypt major ports increased by 435% while total Egyptian ports volume increased by 473.8% (EMDB, 2005)(407). Foreign trade (imports) exceeded 46.1 million tons at 2004 while the total foreign trade was 82.2 million tons. In 2003 the total foreign trade exceeded 73.7 million ton while imports were 42.5 million ton. The volume of foreign trade was $ 24.1 billion (free on board) imports and $ 14.33 billion (free on board) exports through the ports of Alexandria, ElDekheila, Damietta, Port Said and Suez Port (EMDB, 2005)(407). The volume of maritime foreign trade was 90% of Egypt's total import/export cargo. Alexandria and El-Dekheila ports handled 35.4 billion tons, with a trade value of 18.7 billion dollars. These figures rank the port at the top position among Egypt's five major ports (Alexandria and El-Dekhaila, Port Said, Damietta, Suez and Adabia and El-Sokhna) (EMDB, 2005)(407). The second component, were ship calling and passengers through the major ports (14.2%) and (1%) respectively. Services provided to vessels as they call at the ports is a major part of the impact of the ports on the local area economy. These services include navigation services; the loading and unloading of the cargo itself; local arrangements, accounting, purchase of supplies; the supplies themselves; fuel that is sold to the vessels, cargo packing services, and customer services. The number (32776) of ships passes through Egyptian ports including Suez Canal during 2004, while in 2003 that reached (29194). -87- However, the total number of ships in Egyptian ports have been increased with a percentage of 12.3% where as the total number of passengers was (2,810,734) (EMDB, 2003)(403). The third component was the growth of foreign container trade (27.3%). Containers trade includes exports (1,422,008) and imports (1,477,702). They are illustrating the strong competitiveness and the magnitude of the consumer population. Domestic container trade increased with a percentage of 27.5% in relation to foreign trade. In 2004, containers activity was 569867 while import one was 557528 (EMDB, 2005)(407). The forth components is the vital yearly flow which is around $4440 million into the regional economy from port operations, in addition to $1100 million from traffic in Suez Canal and 12100 million from trade related. The port's activities would significantly impact Egyptian's economic growth and add considerable costs to import and help in creating job opportunities (EMDB, 2005)(407). 3.3. Environmental Aspects The Egyptian coastal zone bordering the Mediterranean Sea has high economic, ecological, aesthetic, and recreational importance. Developments in this zone may affect the terrestrial, coastal, and marine ecosystems. The vast majority of Egypt's coastal areas are under increasing stress from both natural (erosion, dune quarrying, and subsidence and rising sea level) and anthropogenic influences caused by population growth and increasing development (Stanley and Warne, 1993)(341). The whole of the Egyptian Mediterranean coast is polluted with Non-biodegradable Ocean borne debris such as plastic, rubber and nylon, most beaches are also polluted to a greater or lesser degree with oil and tar the most polluted areas were in the western region, the majority of beaches being classified as "moderately" "heavily" or "very heavily" polluted (Clarke et al., 2000)(408). The pressure on the environment of the coastal zone of Egypt is very intense, as it combines intensive socio-economic activities and urbanized areas. Along the Mediterranean coast of Egypt, there are eight coastal governorates. These are from west to east Matruh, Alexandria, Behaira, Kafr El-Sheikh, Damietta, Daqahliya, Port Said, and North Sinai. The enormous urban population and adjacent agricultural areas, all contribute to the pollution load reaching coastal waters. These derived either directly from coastal cities discharge points; the Rosetta branch of the River Nile, the Mahmudiya and Nubariya irrigation canals, drainage canals discharged directly to the sea, such as "El-Tabia and El -Ummum", or from coastal lagoons "lakes" Maryut, Idku, Burullus and Manzala. These sources discharge about 8 billion m/y into the Mediterranean. This includes heavy loads of pollutants from various sources. The maritime transport in the eastern Mediterranean, including oil tankers, commercial ships and passenger ships, affect the coast to a large extent. The entire beaches are frequently polluted by oil lumps, litter and plastic debris; even in the very far remote areas of the coast where there are no related activities. Large parts of the Nile Delta suffer from severe coastal erosion, although adequate protection and mitigation measures have been considered. Most of the coastal lagoons "lakes" are however in crisis, suffering from the excessive discharge of industrial ,agricultural and domestic sewage flow. Large parts of the Nile Delta suffer from severe coastal erosion, although adequate protection and mitigation measures have been considered. (UNEP, 1999((185). Environmental issues of the Nile delta coast have become more prominent recently due to increasing population and intensifying industry (El-Rayis, 2005)(409). Four large coastal lagoons are being ecologically degraded owing to the discharge of untreated wastewaters into the lakes. For example, sewerage output has extended to Mariut lagoon from Alexandria on the northwestern Nile coast and that from Port Said, Demietta and -88- Matariya to Manzala lagoon on the northeastern coast, where heavy metals are significantly enriched in the water and sediments. Cu and Cd in Manzala Lake have gone up almost 60% and Zn has increased almost twofold. Nowadays, Mariut and Manzala lagoons are the most polluted and Idku and Burullus follow behind. Presently these two lakes are facing more environmental pressures from local industries and urbanization with the increasing pollutants being expelled towards the lake coast (Kamal and Magdy, 2005)(410). Heavy metals and related environmental conservation of the Nile coast calls for more attention. Many projects implemented have targeted heavy metal distribution and transportation in relation to aquacultural health and societal response. Abdel-Moati and El-Sammak (1997)(411) found that Cd and Pb expelling into the lagoons has increased by 8-70 times during the past 25 years. Pancreatic risk in the Manzala region seems to be closely associated with cadmium concentration (Soliman et al., 2006)(412). Siegel et al. (1994)(413) stated that Pb, Zn, Hg and Cu enriched in Manzala lagoon were primarily due to cheaper power generators after High Aswan dam emplacement in 1964. This has considerably degraded aquacultural products both in quantity and quality in the Manzala region, where it has long been the most important aquacultural base, by providing more than 50% of aquacultural products for Egyptian. Alexandria governorate coastal zone receives a large amount of metal pollution form the principle industries of this region include fertilizers, agrochemicals, pulp, paper, power plant, food processing, detergents, fibers, dysestuffs, textile, and building materials where, the daily average industrial discharge amounts to 30,000 and 128-261,000 m3 per day domestic sewage and 1-2 million cubic meters per day of agricultural wastes (El-Nemr et al., 2007a)(61). -89- Chapter IV Material & Methods 4.1. Study area The Egyptian Mediterranean coast extends between longitude 250 30/ E and 340 15/ E and extends northward to latitude 330 N, Figure 1. It has a surface area of about 154840 km2 and its water volume is 224801 km3 (Said and Rajkovic, 1996)(414). The coastal zone of Egypt on the Mediterranean extends from Rafah in the eastern region to El-Salloum to in the western region for over 1200 km. It hosts five large lakes; namely Bardawil, Manzala, Burullus, Edku and Maryut which represent about 25% in area of the total wetland of the Mediterranean. It also hosts a number of important residential and economic centers of the country including the cities of Alexandria, Matruh, Damietta, Rosetta, Port Said, and Al Arish. Activities on the coastal zone including fishing, industrial activities, tourism, trading and agricultural activities in the delta region (SMART, 2005)(415). 4.2. Sample collection, preservation and storage Twenty surfacial sediment samples were collected from different selected stations from El-Salloum at the west to Rafah at the east along the northern coast of Egypt (Southeastern Mediterranean Sea) during July 2010. Egypt's Mediterranean coast is naturally divided into three regions, the Eastern (Sinai) region from Rafah to Port Said, the Central (Delta) region from Port Said to Alexandria, and the Western region from Alexandria to ElSalloum (Clarke et al., 2000)(408). The study area was divided into three regions as following: region I located in the western area of the coast, represented by 11 stations from El-Salloum to El-Maadia. Region II located in the Delta area, represented by 7 stations from Rashid west to El-Gamil east and Region III located in the eastern region of the coast, represented by 2 stations from Port Said to Rafah (Figure 1 and Table 1). The samples from the top (2-3) cm layer of sediments were collected using Peterson grab sampler. The samples was placed into sealed polyethylene bags, carried to the laboratory in an ice box and stored at -200C in the dark until analysis. Separate samples were collected at the same time for the measurement of SEM/AVS. Samples were collected in such a manner that exposure to atmospheric O2 is minimized, or sulfides will be oxidized. Samples were collected in wide mouth jars with a minimum of head space and stored at -20 0C. Under these conditions, no significant loss of AVS is observed during storage for up to 2 weeks. Sample holding time must not exceed 14 days. 4.3. Sample pre-treatment The samples, which were previously deep frozen at polyethylene bags at approximately -20C0 in order to limit biological and chemical activities, were removed from the freezer, thawed and placed in glass pettri-dishes then dried in an oven at 40 C0 until total dryness. Subsamples of the dried samples were sieved through a clean sieve <2mm mesh size to remove coarse materials such as pebbles, coarse organic pebbles and shells. Samples then were homogenized with a pestle and mortar in order to normalize for variations in grain size distribution. The dried homogenized sediment samples were packed in a clean well Stoppard plastic containers and stored in a cool dry place until analysis. To remove any contamination, all glassware and plastic vials used were initially cleaned with soap, rinsed thoroughly with tap water and distilled water, and then soaked in 14% HNO3 (v/v) for 24 hr, cleaned thoroughly with deionized water and dried. All solutions were prepared using Milli Q water. -90- 1 El-Saloum 2 13 8 9 11 6 3 4 5 10 12 1 7 1 1 1 11 111111 14 111 16 15 1718 19 1 1 11 1 11 11 Figure (1): Satellite Map of Egyptian Mediterranean coast representing the sampling sites of the study area -91- 20 Rafah Table (1): Description of the study area and sources of marine pollution Region Station Latitude Longitude Location Western Region 1 2 3 4 5 6 7 8 9 10 Middle Region 11 12 13 14 15 16 17 18 Eastern Region 19 31 33 30 N 31 10 40 N 31 05 15 N 31 08 10 N 31 09 21 N 31 09 18 N 31( 12( 52(( N 31( 12( 20(( N 31( 18( 29(( N 31( 15( 53(( N 31 16 40 N 31 26 56 N 31 27 46 N 31 27 46 N 31 3010 N 31( 30( 20(( N 31( 17( 10(( N 31( 18( 16(( N 31( 16( 44(( N 25 04 42 E 27 40 07 E 29 42 51 E 29 49 17 E 29 50 42 E 29 49 17(( E 29( 52( 59(( E El-Salloum Baghoush El-Nobarreya El-Dikhaila El-Mex Western Harbour NIOF 29( 52( 59(( E Eastern Harbour 30( 04( 11(( E Abu Qir 30( 08( 55(( E Power Station 30 09 12 E 30 21 33 E 30 21 53 E 30( 58( 28(( E 31( 47( 22(( E 31( 48( 36(( E Maadia Rashid West Rashid East Burullus New Damietta Ras El-Barr 31( 45( 58(( E El-Gamil West 32( 10( 28(( E El-Gamil East 32( 15( 29(( E Port Said Sources of pollution Main sites of pollution Industrial waste water and domestic sewage from residential areas and tourist resort areas. Much of the wastewater is discharged into the coastal lakes which are connected to the sea. Shipping activities El-Nobarreya drain El-Mex Out fall Abu Qir Drain (El-Amiaa) Lake Edku outlet Western harbour El-Dikhaila harbour Eastern Harbour Nile water and agricultural drains contaminated with hazardous industrial waste, domestic sewage, organic matter, fertilizers and pesticides. The Lake Manzalah receive the sewage from Cairo via El-Baqar canal Shipping activities Resetta branch of the Nile Damietta branch of the Nile The outlet from Lake ElManzala (El-Gamil outfall) Burullus outlet New Damietta Port Oil production and oil terminals Shipping activities Port said -92- 20 31( 17( 07(( N 34 09 47 E Rafah -93- 4.4. Physicochemical characterization of sediment 4.4.1. Determination of water content (%WC) Water or moisture content is the ratio of the weight of water to the weight of sediment in a given volume of sediment, expressed as a percentage. Water content is useful when contaminant concentration is to be reported on a dry weight basis, even if determined in wet samples. Water content was determined according to Loring and Rantala, (1992)(416). For water content determination, a known weight of each sample was placed in pre-cleaned and weighed Petri dish. Petri dishes were then placed in an oven previously heated to 105 оC and samples were left for 24 hours. Petri dishes were then removed from the oven and placed in a desiccator until reaching room temperature. Finally, Petri dishes were weighed and these steps are repeated until constant weight is reached. The percentage (%) of water content was calculated from the following equation: %WC WB WA 100 WB Where, % WC= percent of water content WB= weight of sample before drying WA = weight of sample after drying 4.4.2. Determination of pH Approximately 10g of dried sediment sample were suspended in 50 ml distilled water and agitated for 10 min. The suspension was allowed to rest for about 1 hour with occasional shaking until the pH was measured. A combined glass electrode connected to a pH meter (Schott-Gerate GmbH) was used for pH measurements (Yan et al., 2010)(417). 4.4.3. Determination of grain size analysis Grain size determination was made on the dried samples by the conventional sieving method. About 50 gm split of each of the quartered sample was placed into the top most sieve and the entire column was shaken on a mechanical shaker for about 15 min. The sieve meshes give the class intervals 1000, 500, 250, 125, 63, 37 µm. These correspond to the phi classes of 0, 1, 2, 3, 4, 5, respectively (Folk and Ward, 1957)(418). 4.4.4. Determination of total carbonate Total carbonate content of the sediment samples was determined by titration technique (Black, 1965)(419). Procedure 1- Weigh 1 g of sediment and transfer into a 250 ml Erlenmeyer flak. 2- Add 30 ml of standardized 0.5 N HCl 3- The released amount of CO2 was determined by back titration with previously standardized 0.25 N NaOH solution using phenolphthaline indicator. 4- The CaCO3 percentage was determined by the following equation: Calculation % CaCO3 = 100 x 0.05 x [NHCl x VHCl] – [NNaOH x VNaOH] -94- 4.4.5. Determination of total organic carbon (TOC) Total organic carbon (TOC %) was determined according to Walkely-Blak’s wet oxidation method (Baruah and Bathakur, 1997)(420). 0.5-1 g of oven dried and fine grained sediment; 10 ml of 1 N K2Cr2O7 and 20 ml of concentrated sulfuric acid (H2SO4) were added. The mixture was gently shaken and allowed to stand for 30 min until completion of the oxidation reaction. The mixture was diluted with 200 ml of distilled water, then 10 ml of 85% phosphoric acid (H3PO4) and 1 ml of diphenylamine indicator were added. Finally, the mixture was back titrated against 0.5 N ferrous sulfate (Fe (NH4)2(SO4)2.6H2O), until violet color was observed. A blank titration was carried out in the similar manner, then TOC% was calculated according to the following formula: TOC%= (B-S) x 0.5 x 0.003x (100/W) x 1.3 x 1.724 Where, B: volume in ml of ferrous sulfate needed for blank titration, S: volume in ml of ferrous sulfate needed for sample titration, W: weight in grams of sample, 0.5 is normality of potassium dichromate, 0.003 is grams of organic carbon, 1.3 is Walkely correction factor and 1.724 is von Bemmlen factor. 4.5. Determination of total metals 4.5.1. Sample preparation Sediment samples were oven dried at 40 0C for almost a week. After drying, sediments were ground with an agate grinder and stored in a plastic vial until analysis. Total elemental analyses of sediments were determined according to Oregioni and Aston (1984)(421). 1- Weigh out accurately between 0.25-0.5 g of dried sediment into a clean Teflon beaker cleaned with concentrated nitric acid and deionized double distilled water and dried at 105 0C. 2- Add 2 ml of concentrated HNO3 to the Teflon beaker evaporate to dryness at 80 0C. Add 5 ml of HNO3/HClO4/HF (3:2:1) mixture and evaporate to dryness, gradually increasing the temperature to 120 0C to remove the HClO4 residue. 3- Cool to room temperature and use 5 ml of 0.1M HCl to rinse the beaker and transfer to a 25 ml measuring flask. 4- Add another 5 ml of 0.1 M HCl to the beaker and transfer to the flask. Make up the volume with 0.1 M HCl. 5- Check that the entire residue has dissolved and, if necessary, repeat the digestion procedure. 6- Total heavy metals (Fe, Mn, Zn, Cu, Pb, Co, Cr, Cd and Ni), were determined using Flame Atomic Absorption Spectrophotometer (AAS). The concentrations of each trace metals was calculated from the following equation: Metal concentration (µgg-1) = (25/W) x µg ml-1 Where, 25 = final volume of each digested sample W = dry weight of digested sample µg ml-1 = concentration of each metal in the resulting solution measured by AAS 4.5.2. Measuring system The determination of the metals in the sediment samples were performed with a SHIMADZU AA6650 atomic absorption spectrophotometer. An atomizer with an air/acetylene burner was used for determining all the investigated elements. All instrumental settings were those recommended in the manufacture's manual book. The wavelengths (nm) -95- used for the determination of the analytes were as follows: Cr (357.9), Cd (228.8), Co (240.7), Ni (232.0), Cu (324.8), Zn (213.9), Pb (283.3), Mn (279.5), Fe (248.3) 4.5.3. Analysis of certified reference materials In order to check for the quality of the method applied for the analysis of trace metals, certified reference materials (IAEA-405: Estuarine sediment, International Atomic Energy Agency, Vienna, Austria) were analyzed with the developed method. Replicate analysis of this reference material showed good accuracy, with recovery rates for metals between 91.11% and 104.99 % (Table 2). To determine the precision of the analytical processes, three samples were analyzed in triplicate. The average values of the variation coefficients obtained (in general, < 10%) can be considered satisfactory for environmental analysis. Table 2: Concentrations of metals (µgg-1) obtained from the analysis of the Standard Reference Materials (IAEA-405) and their recovery Element Cd Co Cr Cu Fe Mn Ni Pb Zn Certified value (gg-1) 0.73 13.7 84 47.7 37400 495 32.5 74.8 279 Determined value (gg-1) 0.70 14.38 78.02 50.01 38334.35 460.08 31.45 77.44 254.2 Recovery % 95.89 104.99 92.88 104.84 102.50 92.95 96.76 104.99 91.11 4.6. Determination of leachable metals Acid leachable metals were determined according to the method described by Tanner and Leong (1999)(422). About 1 g of each dry sediment sample was extracted at room temperature with 25 mL of 1 N HCl with continuous agitation on a shaker (Mistral MultiMixer) for 16 hours. Samples were centrifuged at 2000 rpm for 15 minutes and the supernatant was separated by means of a pipette and kept in polypropylene bottles for analysis. The resulting solutions were analyzed by Atomic Absorption Spectrophotometer (Shimadzu AA 6650 Spectrophotometer). The concentration of metals (μgg-1) in each sample was calculated using the following equation: 25 x µg mL-1 Metal concentration (µgg-1) = W Where, 25 = volume of the acid added W = dry weight of the extracted sediment sample μgmL-1 = Concentration of each metal in the resulting solution measured by AAS -96- 4.7. Sequential extraction procedure for trace metals Use of total metal concentrations as a criterion to assess the potential effects of sediments contamination, implies that all chemical forms of a given metal have equal impacts on the environment, which is highly improbable (Tessier et al., 1979)(15). Sequential extraction procedures, as opposed to bulk sample analysis, allow for the differentiation of the relative binding strengths of the trace metals to the various solid phases by successive leaching with chemicals of increasing strength and selectivity (Kersten and Forstner, 1985)(423). This procedure provides much more data on the origin of pollutants, their reaction pathways, biological and physico-chemical availability and possible remobilization, than does bulk sample analysis (Abdallah, 2007a)(292). In order to define the fractions of the trace metals (exchangeable, carbonate, Mn and Fe-oxides, organic matter and residual fraction) and explore the metals bioavailability, the sequential extraction technique represented in Figure 2 was performed according to the procedure reported by Tessier et al. (1979) (15). (i) Exchangeable: The sediment was extracted at room temperature for 1 h with 8 ml of sodium acetate solution (1 M NaOAc, pH 8.2) with continuous agitation. (ii) Bound to carbonate: The residue from (i) was leached at room temperature with 8 ml of 1 NaOAc adjusted to pH 5 with acetic acid (HOAc). Continuous agitation was maintained for 5 hrs. (iii) Bound to Fe-Mn Oxides: The residue from (ii) was extracted with 20 ml 0.04 M NH2OH.HCl in 25% (v/v) HOAc. This was performed at 96 ± 3 0C with occasional agitation for 6 hrs. (iv) Bound to Organic Matter: To the residue from (iii) were added 3 ml of 0.02 M HNO3 and 5 ml of 30% H2O2 adjusted to pH 2 with HNO3, and the mixture was heated to 85 ± 2 0C for 2 h occasional agitation. After cooling, 5 ml of 3.2 M NH4OAc in 20% (v/v) HNO3 was added for 30 min. (v) Residual: The residue from (iv) was transferred to Teflon beaker and digested with HNO3-HClO4- HF mixture according to Oregioni and Aston (1984)(421). The selective extractions were conducted in centrifuge tubes (polypropylene, 50 ml) to minimize losses of solid material. Between each successive extraction, separation was effected by centrifuging at 10 000 rpm for 30 min. The supernatant was removed with a pipette and analyzed for trace metals, whereas the residue was washed with 8 ml of deionized water; after centrifugation for 30 min, this second supernatant was discarded. The volume of rinse water used was kept to a minimum to avoid excessive solubilization of solid material, particularly organic matter. The metal concentrations in each fraction were measured using Atomic Absorption Spectrophotometer (Shimadzu AA 6650 Spectrophotometer) Deionized water used in preparing stock solutions and in each step of the leaching procedure was obtained from a Millipore Milli-Q3RO / Milli-Q2 system. All glassware used for the experiments was previously soaked in 14% HNO3 (v/v) and rinsed with deionized water. All reagents used in this study were of analytical grade. -97- Dry sediment (1 g) 8 ml of 1 M (1 M NaOAc, pH=8.2) continuous agitation. 1 h Centrifugation Liquid extract Exchangeable phase Residue 8 ml of 1 M (1 M NaOAc, pH=5 with HOAc) continuous agitation. 5 h Centrifugation Liquid extract Carbonate phase Residue 20 ml 0.04 M NH2OH.HCl in 25% (v/v) HOAc, at 96 ± 3 0C, occasional agitation for 6 hrs. Centrifugation Liquid extract Fe-Mn Oxide phase Residue 3 ml of 0.02 M HNO3 and 5 ml of 30% H2O2 adjusted to pH 2 with HNO3, heated to 85 ± 2 0C for 2 h occasional agitation. Cooling, 5 ml of 3.2 M NH4OAc in 20% (v/v) HNO3 was added for 30 min. Centrifugation Liquid extract Sulphides & Organic phase Residue Digestion with digested with HNO3-HClO4- HF mixture Silicates & residual phase Figure 2: Flow chart of the sequential extration scheme used in this study -98- 4.8. SEM/AVS analysis procedure The procedures for AVS; acid volatile sulphide and SEM; simultaneously extracted metals analysis were stemmed from the method described by Allen et al. 1993(424) with some modifications in the flow rate of nitrogen. 4.8.1. Reagents Hydrochloric acid Sodium hydroxide Sodium sulfide standard (Na2S. 9H2O) Mixed diamine reagent: 660 ml H2SO4, 340 ml reagent water, 2.25 g N-N-dimethyl-pphenylenediamine oxalate mixed with 5.4 g FeCl3.6H2O, 100 ml HCl, 100 ml reagent water. 4.8.2. Generation of H2S Sample reaction train - The apparatus for the colorimetric method utilized a series of four flasks connected to one another with Tygon tubing. The first was gas washing bottle, a 500 ml round bottom flask containing reagent water immediately after the N2 cylinder. - The second flask was the reaction vessel, a 250 ml round bottom flask with a side arm and septum. - Following were two 125 ml flat bottom boiling flasks containing the trapping reagents. 4.8.3. Procedure - To release AVS from the sediment sample, 100 ml of reagent water, minus the volume of water expected to be in the wet sediment sample, is added to the round bottom flask. - Traps are filled with 80 ml of 0.5 M NaOH and the system is purged for 2 minutes at 280 ml/min with nitrogen gas. Make sure that the flow rate is not so high that the 0.5 M NaOH trapping solution is displaced from the tubes. - Transfer about 10 g of wet sediment to a strip of parafilm on a tared top pan balance. Record the wet weight of the sample. - Transfer the weighed sample with the minimum of delay to the reaction flask. - Purge for 2 minutes at 280 ml/min. - Turn off the nitrogen flow (at the flowmeter), and using a clean plastic disposable syringe add 20 ml of 6 N hydrochloric acid through the sidearm. - Start the magnetic stirrer and adjust the speed to enable moderate stirring of the sample. - Bubble nitrogen through the sample for 30 minutes at 280 ml/min. -99- 4.8.4. Analysis of sulfide Colorimetric method Trapped sulfide is measured by adding 10 ml of mixed diamine reagent to the contents of the first NaOH trap and diluting to 100 ml with reagent water. Absorbance is measured at 670 nm after color develops for 30 minutes. Samples are compared with calibration standards made up in 0.5 N NaOH (low range = 0-80 µg S2-, high range = 0-640 µg S2-). If sample absorbance exceeds 0.6, the sample should be diluted with 1 M NaOH. 4.8.5. Calculation of AVS - The sediment dry weight/wet ratio (R) must be determined separately; acid volatile sulfide can be oxidized or altered to non volatile forms during drying. - Transfer an aliquot of the sediment to a 100 ml evaporating dish. Weigh the dish plus the wet sediment. Calculate the wet weight of the sample. Dry the sediment at 103105 0C and weigh. Calculate the dry weight of sediment. - Determine the ratio of dry weight to wet weight for the sediment sample: R = Wd/Ww Where R = ratio of dry weight to wet weight, Wd = dry weight of sediment sample (g), and Ww= wet weight of sediment sample (g) - Compute the sulfide concentration per gram dry weight of sediment S AVS (µmole/g) = R x Ww Where S = the amount of AVS in sediment (µmoles) 4.8.6. Determination of simultaneously extracted metals (SEM) - After AVS generation has been completed the contents of the sample flask is filtered through an acid resistant membrane filter and diluted to 120 ml with milli Q water. - Metals (Cd, Cu, Pb, Ni, and Zn) are determined by atomic absorption spectrophotometer model: AA6650 Shimadzu, comparing samples with calibration standards. - Individual metals are reported as µmol/g dry sediment, calculated as conc µmol = conc sol'n x 120 g dry weight R x W x AWSEM where, conc sol’n = the concentration of the element of interest in solution, in units of µg/ml, R = the ratio of dry to wet weight; -100- W = the weight of wet sediment added to the sample flask, and AWSEM = the atomic weight of the element of interest. - The toxicity of metals to organisms is estimated from the ratio of SEM: AVS, where both are in units of µmol/g dry sediment. SEM is the sum of all metals analyzed (e.g. C, Cu, Pb, Ni, and Zn). Previous work has indicated that ratios greater than unity were associated with sediment toxicity. -101- Chapter V Results 5.1. Physico-chemical Parameters The results of physical-chemical parameters of various sites along the Egyptian Mediterranean coastal area were tabulated in Table 3. The measurements were carried out parallel to the sediment sampling of the present study. 5.1.1. Seawater Temperature Temperature is affected by several factors including weather, removal of shading stream bank vegetation and storm water (Faragallah et al., 2009)(311). The Egyptian Mediterranean seawater temperature during the sampling time were in the range from 28.24 to 31.00 C (average: 29.34 C). The highest value was found at electrical power station (Station 10), while the lowest value found at staion 1 in El-Salloum and station 4 in ElDikhaila (Table 3). 5.1.2. pH value The pH values in surface seawater of the Egyptian Mediterranean coastal area from El-Salloum in the West to Rafah in the East are listed in Table 3. It ranged between 7.21 and 8.30. The highest value was reported at station 1 (El-Salloum) and the lowest value was reported at station 20 (Rafah). The wide variety of aquatic animals prefers of pH ranged between 6.50 and 8.00. Outside this range the diversity may be reduced because it stresses the physiological systems of most organisms and can reduce reproduction. Low pH can also allow toxic elements to become more available for uptake by aquatic plants and animals. This can produce conditions that are toxic to aquatic life (Faragallah et al., 2009)(311). 5.1.3. Salinity Salinity, as temperature, is an important factor which affects the marine environment. The results of surface salinity of the seawater along the Egyptian Mediterranean coast are shown in Table 3. The results showed that salinity of seawater during the sampling time ranged between 28.15-38.3 PSU with an average: 36.32 PSU. The highest value was found at Rafah and Baghoush and the lowest value was found at El-Gamil West. A relatively decrease of salinity was observed in the Mediterranean seawater in front of drainages and the Nile delta. For example, it was 35.64 PSU at Rashid west (station 12) and 35.31 PSU at Rashid east (station 13), 28.15 PSU at El-Gamil west (station 17) and 30.95 PSU at El-Gamil east (station 18) in front of Manzala lake. 5.1.4. Dissolved oxygen Dissolved oxygen (DO) is considered as one of the most important and useful parameters in identification of different water masses and in assessing the degree of pollution especially with organic pollutants which affects fish and other marine life through oxygen reduction or depletion (Nessem et al., 2005)(425). The distribution pattern of DO along the Egyptian Mediterranean coast is presented in Table 3. Dissolved oxygen in seawater fluctuated between a minimum value of 4.99 mg/l at station 7 (NIOF) and a maximum value of 7.56 mg/l at station 17 (El-Gamil west). -102- Table 3: Physical parameters of the surface seawater of the study area. Region Western Region Middle region Eastern region Min. Max. Average Station 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 Temperature (oC) 28.24 28.25 29.67 28.24 28.47 28.44 29.45 28.98 29.29 31.00 29.66 29.16 29.07 29.40 30.30 30.33 29.24 29.17 29.97 30.46 28.24 31 29.34 -103- DO (mg/l) 6.64 5.57 6.76 5.02 5.03 5.86 4.99 5.73 5.89 6.13 5.74 6.26 6.06 6.80 7.19 7.14 7.56 7.13 5.97 7.19 4.99 7.56 6.23 Salinity (%) 38.18 38.30 36.49 33.83 35.86 36.07 38.06 37.83 37.63 38.09 37.87 35.64 35.31 36.30 38.02 38.12 28.15 30.95 37.37 38.30 28.15 38.30 36.32 pH 8.30 8.24 8.05 8.04 8.14 8.09 8.10 8.16 8.19 8.22 8.05 8.14 8.22 8.09 8.18 8.11 8.07 8.16 7.95 7.21 7.21 8.30 5.2. Geochemical Analysis The Mediterranean sea is an area where sediments have different geochemical composition (Abdallah, 2007b)(303). The results of sediment characteristics including sediment texture, organic carbon, and carbonate of the study area are given in Table 4. 5.2.1. pH The pH values in surface sediments of the Egyptian Mediterranean coastal area from El-Salloum in the West to Rafah in the East are listed in Table 4. It ranged between 7.20 and 8.38. The highest value was reported at station 8 in the Eastern Harbour (western region) and the lowest value was reported at station 14 in Burullus (Middle region). The pH values indicated that the surface sediments are slightly alkaline. It is worth to mention that, the variation of the pH value influences the release or adsorption of each metal into the sediment fraction (Smith, 1994)(426). 5.2.2. Calcium Carbonate (CaCO3) Carbonate is often an important component of marine sediments and has been found to be an important indicator of provenance and dispersal of terrigenous material (Loring and Rantala, 1992)(416). The co-precipitation with carbonate minerals is of importance for a number of metals, such as cadmium and zinc (Forstner and Wittman, 1983)(427). The results of the analysis of carbonate content of the sediments are listed in Table 4 and Figure 3. The range and the average of total carbonate percentage in the surface sediments of the Egyptian Mediterranean coast were found to vary from 2.85 to 95.57 (37.78%). The highest value of CaCO3 was observed at station 6 in the Western harbour (western region) and the lowest value was observed at station 13 in Rashid East (Middle region). 5.2.3. Total Organic Matter (TOM%) Total organic matter (TOM) is one of the most important collectors of pollutants in the marine sediments. Organic matter tends to form strong organometallic complexes with metals, rendering them immobile. An increase in TOM content may results in an increase in the levels of metals in marine sediment (Massoud et al., 2007)(294). Table 4 and Figure 4 represented the distribution of organic matter content in the study area. The range and the average of TOM in the surface sediments of the study area were found to vary from 0.082 to 1.72 % (0.56%). The highest value of TOM was observed at station 7 in NIOF (western region) and the lowest value was observed at station 12 in Rashid West (Middle region). 5.2.4. Water Content (%WC) The results of water content of all samples from different locations are presented in Table 4 and Figure 5. In general, surface sediments of the Mediterranean Coast of Egypt were characterized by moderate water content (average: 20.43%). Figure 5 illustrates the same trend except NIOF and Western harbour. The maximum value of water content (35.45%) was reported at station 7 in NIOF (western region) and the minimum value of water content (7.49%) was reported at station 6 in the Western harbour (Western region). 5.2.5. Grain Size The grain size of the sediment is a specific parameter, this is one of the major or controlling factors for the distribution of trace metals in coastal areas (Ip et al., 2007)(428). The percent of sand, silt and clay together with the texture of all samples are shown in Table 4. Textural characteristics of the sediments are showed according to the classification of -104- Shepard (Shepard and Moore, 1954)(429). Result showed that fine sand (0.250-0.125 mm) and very fine sand (0.125-0.062 mm) were the dominated fractions of all sediment samples. The range and average of sand were 86.85 to 100% (99.15%). Course sand (1.0-0.5 mm) was observed only at station 6 in the Western harbour (Western region). The highest value of sand content (100%) was observed at stations 3, 5, 6 at Nobareya, El-Mex and Western harbour, respectively in the Western region and station 12 in Rashid west (Middle region) and station 20 at Rafah (Eastern region) and the lowest value (86.85%) was observed at station 1 in El-Salloum (Western region). Table 4: Calcium carbonate (CaCO3%), total organic matter (OM%), Water Content (WC%), pH, grain size and type of sediments along the Egyptian Mediterranean Coastal area. Region Western region Middle region Station CaCO3 % OM% W.C.% pH 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 34.79 94.45 95.49 85.42 67.24 95.57 91.64 93.56 22.11 14.69 15.64 3.83 2.85 5.09 6.08 4.87 4.85 5.64 7.32 6.33 95.57 2.85 37.87 0.46 0.55 1.23 0.59 0.40 0.54 1.72 0.97 0.38 1.36 0.48 0.08 0.18 0.31 0.51 0.24 0.32 0.35 0.24 0.35 1.72 0.08 0.56 24.60 19.92 18.03 24.83 17.81 7.49 35.45 19.003 18.92 17.72 19.57 19.28 19.64 19.97 22.23 24.78 21.5 23.77 19.28 15.39 35.45 7.49 20.43 8.26 8.21 8.26 8.31 7.98 7.82 7.84 8.38 8.19 7.80 8.02 7.93 7.41 7.20 7.97 7.63 7.56 7.77 7.48 7.79 8.38 7.20 7.89 Eastern region Max. Min. Average -105- Sand 86.85 99.99 100 99.96 100 100 98.26 99.99 99.98 99.89 99.96 100 99.93 99.93 99.67 99.57 99.72 99.76 99.60 100 100 86.85 99.15 Grain size analysis Mud Texture (Silt & clay) 13.15 Very fine sand 0.01 Fine sand 0.0 Fine sand 0.04 Fine sand 0.0 Coarse sand 0.0 Very corse sand 1.74 Fine sand 0.01 Fine sand 0.02 Fine sand 0.11 Fine sand 0.04 Fine sand 0.0 Fine sand 0.07 Fine sand 0.07 Fine sand 0.33 Very Fine sand 0.43 Very Fine sand 0.28 Very Fine sand 0.24 Very Fine sand 0.40 Very Fine sand 0.0 Fine sand 13.15 0 0.85 - % CaCO3 100 90 80 70 60 50 40 30 20 10 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 Figure 3: Distribution of CaCO3 % in surface sediments along the Egyptian Mediterranean Coast. % TOM 2 1.8 1.6 1.4 1.2 1 0.8 0.6 0.4 0.2 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 Figure 4: Distribution of TOM% in surface sediments along the Egyptian Mediterranean Coast. % Water Content 40 35 30 25 20 15 10 5 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 Figure 5: Distribution of % Water Content in surface sediments along the Egyptian Mediterranean Coast. -106- 5.3. Trace Metals Distribution The study of marine sediments represents a useful tool for determining the actual state of environmental pollution and for understanding the origin and mechanism of the phenomena. Sediments could be regarded as a historical reflection to changes occurring in the overlying water system and can be used as good indicators for metals in any study area (Salomons and Forstner, 1984)(181). 5.3.1. Total Metals The total concentrations of metals (Fe, Mn, Zn, Cu, Ni, Cr, Co, Pb and Cd) in surface sediments of the Egyptian Mediterranean Coast are given in Table 5. The range and average ± SD concentrations (µgg-1) were 243.48–38045.05 (13255.69± 12911.36) for Fe, 17.251085.72 (380.71 ±305.38) for Mn, 2.05-62.21 (22.19 ±15.84) for Zn, 0.46-26.26 (8.46 ±6.22) for Cu, 1.65-60.25 (25.93 ±20.96) for Ni, 4.08-297.95 (82.74 ±90.18) for Cr, 0.43-26.39 (8.24 ±8.40) for Co, 3.34-53.67 (13.17 ±11.90) for Pb, 0.04-0.47 (0.22 ±0.15) for Cd. 5.3.1.1. Total Iron (TFe) Most ferrous compounds in aquatic environments resulting in iron precipitate in alkaline and oxidizing conditions (Abdulla et al., 1973)(430). Iron behaves similarly to manganese in seawater, as both elements undergo oxidation. In Oxygenated seawater, Fe+2 oxidized to Fe+3, which is strongly hydrolyzed in the marine environment, forming various (oxy) hydroxide phases of very low solubility (Millero, 1996)(431). The results of the total iron concentration in the Egyptian Mediterranean coastal sediments are listed in Table 5 and illustrated at Figure 6. The study area was divided into three regions, which revealed differences in the distribution of total Fe concentration. In the Western region, the lowest level of Fe (243.48 µgg-1) was found at station 2 in Baghoush, while the highest value (11478.38 µgg-1) was found at station 9 in Abu Qir Bay. The distribution of total Fe concentration in the Middle region revealed low level at station 12 in Rashid west (9653.67 µgg-1) and high concentration (38045.05 µgg-1) at station 15 in New Damietta. Finally, the lowest level (1422.39 µgg-1) of Fe in the Eastern region was found at station 20 in Rafah, while the highest concentration of Fe (33971.5 µgg-1) was found at station 19 in Port Said. In general, the highest level of total iron in the surfacial sediments along the Egyptian Mediterranean Coast was observed at station 15 in New Danietta (the Middle region) and the lowest level was observed at station 2 in Baghoush (the Western region). The average concentration of iron in the three regions along the Egyptian Mediterranean Coast can be arranged as follows: Middle region (25516.22±10090.14µgg-1) > Eastern region (17696.95±23015.7µgg-1) > Western region (4646.03±3459.61µgg-1) 5.3.1.2. Total Manganese (TMn) Manganese is found in minerals mostly as carbonates, oxides, silicates and sulphides. It may occur as a particulate manganese or precipitating coating on mineral species, organic matter, and iron manganese hydroxides (Masoud et al., 2005)(432). The results of the analysis of total manganese concentrations in surface sediments of Egyptian Mediterranean Coastal area, during the study area are given in Table 5 and illustrated at Figure 6. The manganese concentration in sediment of the Western region was fluctuated between a minimum of (17.25 µgg-1) at station 3 in El-Nobarreya and a maximum of (526.53 µgg-1) at station 9 in Abu Qir Bay (average: 208.60±163.08 µgg-1). The lowest concentration of Mn in the Middle region was found at station 12 in Rashid west (257.30µgg-1) while the highest concentration (822.60µgg-1) was found at station 15 in New -107- Damietta. The average of Mn in the Middle region was (597.02±203.84µgg-1). The distribution of total Mn concentration in the Eastern region of the Egyptian Mediterranean coast revealed low value (54.76 µgg-1) at station 20 in Rafah and high level (1085.72 µgg-1) at station 19 in Port Said. The average value of the Mn in the Eastern region was (570.24±729.00µgg-1). The average concentration of manganese in the different regions along the Egyptian Mediterranean Sea coast can be arranged as follows: Middle region (597.02±203.84µgg-1) > Eastern region (570.24±729.00µgg-1) > Western region (208.60±163.08 µgg-1). 5.3.1.3. Total Zinc (TZn) Zinc is essential for growth of marine organisms and its concentration affected by plankton communities (Hayward, 1969)(433). The kinetics of removal of zinc in aquatic systems is strongly affected by the rates of biological processes. It is also a common pollutant found in several industrial effluents such as those produced by textile, basic chemicals, electroplating, motor and other industries (Masoud et al., 2005)(432). The concentrations of total Zinc in the surface sediments of the Egyptian Mediterranean coastal area are listed in Table 5 and illustrated at Figure 6. The results of Zn concentration in the Western region ranged from 2.05 to 62.21 with an average 23.43±20.07µgg-1. The highest concentration (62.21µgg-1) was found at station 7 in NIOF and the lowest value (2.05µgg-1) was found at station 2 in Baghoush. In the Middle region, the minimum concentration of Zn was 10.49 µgg-1 at station 12 in Rashid west, while the maximum concentration (29.82 µgg-1) was found at station 16 in Ras El-Barr. The average value of total Zn in this region was 21.90±6.81µgg-1. Zinc level in the sediment of the Eastern region was fluctuated between a minimum of 2.61 µgg-1 at station 20 in Rafah and a maximum of 30.05 µgg-1 at station 19 in Port Said (16.33±19.40 µgg-1). The average concentration of zinc in the different regions along the Egyptian Mediterranean coast can be arranged as follows: Western region (23.43±20.07µgg-1)> Middle region (21.90±6.81µgg-1) > Eastern region (16.33±19.40 µgg-1). 5.3.1.4. Total Copper (TCu) Copper is an essential element in the normal metabolism of plants, animals and human life, however in high levels, cause many disease (Graten et al., 2003)(434). It is uses in electrical equipments, alloys, antifouling paint for ships's shull, as an algaecide and wood preservative (WHO, 1998)(435). The concentrations of total Copper in surface sediments of the Egyptian Mediterranean Coastal area are given in Table 5 and illustrated at Figure 7. In the Western region, the range and average concentration of Cu was between 0.46 and 26.26 (7.93±7.36µgg-1). The highest concentration (26.26 µgg-1) was found at station 7 (NIOF) and the lowest concentration (0.46 µgg-1) was found at station 2 in Baghoush. The minimum concentration of Cu in the sediments of the Middle region was (3.44µgg-1) at station 12 in Rashid West, while the maximum concentration (17.27µgg-1) was found at station 16 in Ras El-Barr. The average value of this region was (9.86±4.47µgg-1). In the Eastern region, the lowest level of Cu (1.57 µgg-1) was observed at station 20 in Rafah, while the highest level of Cu (11.39µgg-1) was found at station 19 in Port Said. The average value of this region was (6.48±6.94µgg-1). The average concentration of copper in the different regions along the Egyptian Mediterranean Sea coast can be arranged as follows: Middle region (9.86±4.47µgg-1)> Western region (7.93±7.36µgg-1)> Eastern region (6.48±6.94µgg-1) -108- 5.3.1.5. Total Nickel (TNi) Nickel (Ni) is one of the major elements on the earth, constituting about 2% by weight (Nriagu,1980)(436). However, nickel is a common pollutant resulting from various industrial activities like mining and refining, electroplating, production of Ni-Cd batteries, waste incineration etc., domestic wastewater, and to a lesser from natural weathering (El-Nemr et al., 2006)(437). The results of total Nickel concentration in surface sediments of the Egyptian Mediterranean coast during this study are listed in Table 5 and illustrated at Figure 7. The range and average concentrations of Ni was 1.65-60.25 (25.93 µgg-1) respectively. The lowest concentration of Ni (1.65 µgg-1) was found at station 2 in Baghoush in the Western region and the highest concentration (60.25 µgg-1) was found at station 17 in El-Gamil West in the Eastern region. In the Western region, the lowest value of Ni (1.65 µgg-1) was found at station 2 in Baghoush, while the highest level (19.36 µgg-1) was observed at station 9 in Abu Qir Bay. The average value in this region was 8.81±5.72µgg-1. The nickel level in sediment of the Middle region was fluctuated between a minimum of (36.38 µgg-1) at station 12 in Rashid west and a maximum of (60.25 µgg-1) at station 17 in El-Gamil West (average: 49.48±8.64 µgg-1). The lowest concentration of Ni (27.79 µgg-1) in the Eastern region was found at station 20 in Rafah, while the highest concentration of Ni in this region (47.42µgg-1) was observed at station 19 in Port Said; (average: 37.61±13.88 µgg-1). The average concentration of nickel in the different regions along the Egyptian Mediterranean coast can be arranged as follows: Middle region (49.48±8.64 µgg-1) > Eastern region (37.61±13.88 µgg-1)> Western region (8.81±5.72µgg-1) 5.3.1.6. Total Chromium (TCr) Chromium is one of the biochemically active transition metals in aquatic environment (Masoud et al., 2005)(432). The primary sources of chromium includes domestic wastewater, manufacturing processes, involving metals and the dumping of sewage sludge (Beltagy, 1973)(438). The results of total Chromium (Cr) concentrations in surface sediments of the Egyptian Mediterranean Coastal area are listed in Table 5 and illustrated at Figure 7. Its concentration gave minimum and maximum values fluctuated between 4.08 µgg-1 and 297.95 µgg-1 at stations 2 (Baghoush) and 13 (Rashid East), respectively. The lowest concentrations of Cr (4.08µgg-1) in the sediment of the Western region was found at station 2 in Baghoush, while the highest levels of Cr (85.48 µgg-1) was observed at station 9 in Abu Qir Bay. The average level in this region was 24.76±22.97µgg-1. In the Middle region, the minimum concentration of Cr (79.04µgg-1) was found at station 15 in New Damietta, while the highest level (297.95µgg-1) was found at station 13 in Rashid East. The average of Cr in this region was 146.53±84.69µgg-1. Finally, the lowest level (72.43 µgg-1) of Cr in the Eastern region was found at station 20 in Rafah, while the highest concentration of Cr (284.30 µgg-1) was found at station 19 in Port Said (average: 178.37±149.81µgg-1). The average concentration of chromium in the different regions along the Egyptian Mediterranean coast can be arranged as follows: Eastern region (178.37±149.81µgg-1)> Middle region (146.53±84.69µgg-1)> Western region (24.76±22.97µgg-1). 5.3.1.7. Total Cobalt (TCo) Cobalt is a very important element in aquatic environment. It is moderately toxic to most aquatic species more than Cr3+ and Cr6+ but much less toxic than Cd2+ and Cu2+. Higher levels of cobalt have been found in the open ocean, but these are probably due to -109- contamination with phytoplankton and other organisms that metabolize vitamin B12 (Masoud et al., 2005)(432). The results of total Cobalt in the surface sediments of the Mediterranean Coast of Egypt are listed in Table 5 and illustrated in Figure 8. The range and average concentrations of Co were 0.43-26.39 µgg-1 (8.24 µgg-1) respectively. The highest concentration of Co 26.39 µgg-1 was found at station 16 in Ras El-Burr and the lowest concentration (0.43 µgg-1) was observed at station 2 in Baghoush. In the Western region, the lowest conent of Co (0.43 µgg-1) was found at station 2 in Baghoush, while the highest level (6.63 µgg-1) was observed at station 11 in Maadia. The average value of total Co in this region was 2.46±1.89 µgg-1. The minimum concentration of Co in the Middle region (7.94µgg-1) was observed at station 12 in Rashid west and the maximum level of Co (26.39µgg-1) was observed at station 16 in Ras El-Barr with an average of 16.96±6.91µgg-1. The concentration of cobalt in the sediments of the Eastern region was fluctuated between a minimum of 1.93 µgg-1 at station 20 in Rafah and a maximum of 17.07 µgg-1 at station 19 in Port Said (average: 9.50±10.71 µgg-1). The average concentration of cobalt in the different regions along the Egyptian Mediterranean coast can be arranged as follows: Middle region (16.96±6.91µgg-1)> Eastern region (9.50±10.71 µgg-1)> Western region (2.46±1.89 µgg-1). 5.3.1.8. Total Lead (TPb) Lead in sediments is chemically precipitated from the surface water solution, and the remainder has been transported in detrital particles. However, lead occurring in sediments has two distinct mineral associations, one with the clay minerals and the other with authigenic minerals and/or biogenous debris (Masoud et al., 2005)(432). The concentrations of total Lead in surface sediments of the Egyptian Mediterranean Coastal area are listed in Table 5 and illustrated at Figure 8. The concentration of Pb ranged from 3.34 to 53.67 with and average value of 13.17±11.90µgg-1. The highest concentration of Pb (53.67µgg-1) was observed at station 5 in El-Mex Bay, while the lowest level of Pb (3.34 µgg-1) was observed at station 20 in Rafah. The lowest concentration of total Pb (4.41 µgg-1) in the Western region was found at station 2 in Baghoush, while the highest level (53.67µgg-1) was observed at station 5 in ElMex Bay. The average value of total Pb in this region was 18.93±13.73 µgg-1. In the Middle region, the lowest level of total Pb (4.61µgg-1) was observed at station 12 in Rashid West, while the highest level (8.83µgg-1) was observed at station 15 in New Damietta. The average of total Pb in this region was 6.70±1.37 µgg-1. The distribution of total Pb concentration in the Eastern region revealed low value (3.34µgg-1) at station 20 in Rafah and high value (6.67µgg-1) at station 19 in Port Said. The average value of Pb in this region was 5.01±2.35µgg-1. The average concentration of Pb in the different regions can be arranged as follows: Western region (18.93±13.73)> Middle region (6.70±1.37µgg-1)> Eastern region (5.01±2.35µgg-1) 5.3.1.9. Total Cadmium (TCd) The major specific sources on the worldwide basis are atmospheric deposition, smelting and refining of nonferrous metals, manufacturing processes related to chemicals and -110- metals, and domestic waste water (Huzinger, 1980)(439). The concentrations of total cadmium (Cd) in surface sediments of the Egyptian Mediterranean Coastal area are listed in Table 5 and illustrated in Figure 8. The range and average concentrations of Cd in the sediments of the Egyptian Mediterranean coast were 0.04-0.47 (0.22µgg-1). The data revealed that all stations in the study area showed relatively low concentrations of cadmium. The distribution of total cadmium levels in the western region revealed low concentration (0.06µgg-1) at station 3 in El-Nobarreya and high concentration (0.47µgg-1) at station 6 in the Western Harbour. The average value of Cd in this region was 0.29±0.15µgg-1. In the Middle region, the lowest concentration of Cd (0.04µgg-1) was found at station 15 in New Damietta, while the highest level (0.23µgg-1) was found at station 14 in Burullus. The average value of Cd in the Middle region was 0.12±0.07µgg-1. The lowest concentration of Cd (0.04µgg-1) in the Eastern region was found at station 19 in Port Said, while the highest concentration (0.18µgg-1) was observed at station 20 in Rafah. The average value of Cd in this region was 0.11±0.10µgg-1. The average concentration of Cd in the three regions can be arranged as follows: Western region (0.29±0.15µgg-1) > Middle region (0.12±0.07µgg-1) > Eastern region (0.11±0.10µgg-1) -111- Table 5: Total trace metals concentration (µgg-1 dry weight) in surfacial sediments along the Egyptian Mediterranean Coastal area. Region Western Region Middle Region Eastern Region All Regions Station 1 2 3 4 5 6 7 8 9 10 11 Min. Max. Average SD 12 13 14 15 16 17 18 Min. Max. Average SD 19 20 Min. Max. Average SD Min. Max. Average SD Fe Mn 7166.6 116.31 243.48 26.13 277.34 17.25 3946.02 175.32 3565.22 104.33 1527.85 230.61 4813.8 178.81 3440.82 136.3 11478.38 526.53 6620.29 413.32 8026.49 369.73 243.48 17.25 11478.38 526.53 4646.03 208.60 3459.61 163.08 9653.67 257.3 27044.33 818.74 25164.02 538.97 38045.05 822.6 37398.1 721.08 18271.33 508.01 23037.04 512.44 9653.67 257.30 38045.05 822.60 25516.22 597.02 10090.14 203.84 33971.5 1085.72 1422.39 54.76 1422.39 54.76 33971.50 1085.72 17696.95 570.24 23015.70 729.00 243.48 17.25 38045.05 1085.72 13255.69 380.71 12911.36 305.38 Zn 38.66 2.05 9.49 22.93 55.43 6.28 62.21 20.02 15.99 10.05 14.64 2.05 62.21 23.43 20.07 10.49 24.78 17.00 26.33 29.82 18.4 26.51 10.49 29.82 21.90 6.81 30.05 2.61 2.61 30.05 16.33 19.40 2.05 62.21 22.19 15.84 Cu 13.87 0.46 0.86 9.69 7.34 4.13 26.26 10.94 5.7 2.99 4.95 0.46 26.26 7.93 7.36 3.44 7.06 9.92 12 17.27 7.3 12.04 3.44 17.27 9.86 4.47 11.39 1.57 1.57 11.39 6.48 6.94 0.46 26.26 8.46 6.22 -112- Ni 7.58 1.65 9.5 8.74 5.71 3.68 8.71 2.71 19.36 17.89 11.43 1.65 19.36 8.81 5.72 36.38 56.54 43.55 44.31 56.41 60.25 48.93 36.38 60.25 49.48 8.64 47.42 27.79 27.79 47.42 37.61 13.88 1.65 60.25 25.93 20.96 Cr 31.56 4.08 5.26 16.37 23.19 7.08 25.41 9.45 85.48 33.85 30.59 4.08 85.48 24.76 22.97 84.01 297.95 116.93 79.04 102.18 233.7 111.93 79.04 297.95 146.53 84.69 284.3 72.43 72.43 284.30 178.37 149.81 4.08 297.95 82.74 90.18 Co 2.03 0.43 1.35 1.73 1.34 1.38 1.87 1.35 4.65 4.3 6.63 0.43 6.63 2.46 1.89 7.94 14.86 12.32 24.91 26.39 12.53 19.75 7.94 26.39 16.96 6.91 17.07 1.93 1.93 17.07 9.50 10.71 0.43 26.39 8.24 8.40 Pb 16.36 4.41 14.68 15.94 53.67 20.32 29.91 24.46 9.46 12.06 6.92 4.41 53.67 18.93 13.73 4.61 6.41 5.8 8.83 6.96 6.45 7.86 4.61 8.83 6.70 1.37 6.67 3.34 3.34 6.67 5.01 2.35 3.34 53.67 13.17 11.90 Cd 0.29 0.07 0.06 0.34 0.16 0.47 0.44 0.38 0.19 0.39 0.45 0.06 0.47 0.29 0.15 0.14 0.09 0.23 0.04 0.05 0.15 0.13 0.04 0.23 0.12 0.07 0.04 0.18 0.04 0.18 0.11 0.10 0.04 0.47 0.22 0.15 40000 35000 Fe (µgg-1) 30000 25000 20000 15000 10000 5000 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 1200 1000 Mn (µgg-1) 800 600 400 200 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 80 70 Zn (µgg-1) 60 50 40 30 20 10 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 Stations Figure 6: Distribution of Fe, Mn and Zn in surface sediments collected from the Egyptian Mediterranean coastal area -113- 40 35 Cu (µgg-1) 30 25 20 15 10 5 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 70 Ni (µgg-1) 60 50 40 30 20 10 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 300 Cr (µgg-1) 250 200 150 100 50 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 Stations Figure 7: Distribution of Cu, Ni, and Cr in surface sediments collected from the Egyptian Mediterranean coastal area -114- 30 Co (µgg-1) 25 20 15 10 5 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 60 Pb (µgg-1) 50 40 30 20 10 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 1 Cd (µgg-1) 0.8 0.6 0.4 0.2 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 Stations Figure 8: Distribution of Co, Pb and Cd in surface sediments collected from the Egyptian Mediterranean coastal area -115- 5.3.2. Leachable Metals The concentrations of leachable metals (Fe, Mn, Zn, Cu, Ni, Cr, Co, Pb and Cd) in surface sediments of the Egyptian Mediterranean Coastal area during July 2010 are given in Table 6 and Figure 9, 10 and 11. The range and average concentrations (µgg-1) were: 94.986831.61 (1930.77±1777.05) for Fe, 10.83-307.27 (126.74±81.82) for Mn, 0.11-49.48 (7.40±10.94) for Zn, 0.23-8.20 (2.19±2.29) for Cu, 0.15-11.16 (3.04±3.23) for Ni, 0.56-8.22 (2.61±2.01) for Cr, 0.10-8.77 (2.35±2.82) for Co, 0.54-51.35 (8.14±11.97) for Pb, 0.02-0.23 (0.06±0.05) for Cd. 5.3.2.1. Leachable Iron (LFe) Table 6 and Figure 9 show the results of leachable Iron (LFe) in the surface sediments of the coastal area of the Egyptian Mediterranean Sea. The highest concentration of LFe (6831.61 µgg-1) was found at station 15 in New Damietta and the lowest concentration of LFe (94.98 µgg-1) was found at station 20 in Rafah. The study area was divided into three regions, which revealed differences in the distribution of leachable iron. The lowest level of LFe (106.63µgg-1) in the sediments of the Western region was observed at station 3 in Nobarreya, while the highest value (2100.42µgg-1) was observed at station 11 in Maadia. The average LFe concentration was 1023.40±614.80µgg-1. In the Middle region, the lowest concentration of LFe (1494.21µgg-1) was observed at station 12 in Rashid west, while the highest value (6831.61µgg-1) was observed at station 15 in New Damietta. The average LFe level was -1 -1 3370.81µgg ±2092.12µgg . The distribution of LFe concentration in the Eastern region revealed low level (94.98µgg-1) at station 20 in Rafah and the high concentration was found at station 19 in Port Said (3667.31µgg-1). The average LFe level in this region was 1881.14±2526.02µgg-1. 5.3.2.2. Leachable Manganese (LMn) The results of the analysis of leachabel Manganese (LMn) in surface sediments at all stations are represented in Table 6 and Figure 9. Data showed that the highest concentration of LMn (307.27µgg-1) in the surfacial sediments of the Egyptian Mediterranean coast was found at station 15 in New Damietta in the Middle region and the lower concentration of LMn (10.83µgg-1) was found at station 3 in Nobarreya in the Western region. In the Western region, the lowest concentration of LMn (10.83µgg-1) was observed at station 3 (Nobarreya), while the highest concentration (261.85µgg-1) was observed at station 9 (Abu Qir Bay) with an average (113.86±76.59µgg-1). The lowest level of LMn (29.99µgg-1) in the Middle region was observed at station 13 in Rashid east, while the highest level (307.27µgg-1) was observed at station 15 in New Damietta. The average of LMn in the Middle region was 154.39±91.30µgg-1. The distribution of LMn concentration in the Eastern region revealed low value at Rafah (Station 20; 30.20µgg-1), and the high value at Port Said (Station 19; 171.53µgg-1). The average measured concentration of LMn in this region was 100.87±99.94µgg-1. 5.3.2.3. Leachable Zinc (LZn) The concentrations of leachable Zinc (LZn) in surface sediments at all stations of the Egyptian Mediterranean coastal area are presented in Table 6 and Figure 9. Data showed that the highest concentration of LZn in the western region (49.48 µgg-1) was observed at station 5 in El-Mex Bay and the lowest concentration of LZn (0.11 µgg-1) was observed at station 3 in Nobarreya (average: 10.89±13.92µgg-1). In the Middle region, the minimum concentration of LZn was (1.49 µgg-1) at station 17 in El-Gamil west and the maximum concentration of LZn -116- was (6.54µgg-1) at station 15 in New Damietta, with an average value of (3.51±2.15µgg-1). The distribution of LZn concentration in the eastern region revealed that the lowest concentration was observed at Rafah (Station 20; 0.15µgg-1) and the highest concentration was observed at Port Said (Station 19; 3.63µgg-1). The average of LZn was 1.89±2.46µgg-1. 5.3.2.4. Leachable Cupper (LCu) The results of the analysis of leachable Cupper (LCu) in surface sediments of the Egyptian Mediterranean coastal area are shown in Table 6 and Figure 10. In the Western region, the highest concentration of LCu (8.20 µgg-1) was found at station 7 in NIOF and the lowest concentration of LCu (0.23 µgg-1) was found at station 2 in Baghoush; the average value of LCu in this region was (2.98±2.85µgg-1). The minimum concentration of LCu in the sediments of the Middle region of the Egyptian Mediterranean coast (0.56µgg-1) was found at station 12 in Rashid west, while the maximum concentration (2.08µgg-1) was found at station 15 in New Damietta. The average value of this region was (1.29±0.57µgg-1). In the Eastern region, the lowest value of LCu (0.27µgg-1) was observed at station 20 in Rafah and the highest value (1.79µgg-1) was observed at station 19 in Port Said. The average value of LCu in the Middle region was 1.03±1.07µgg-1. 5.3.2.5. Leachable Nickel (LNi) Table 6 and Figure 10 showed the results of Leachable Nickel (LNi) in the surfacial sediments of the Egyptian Mediterranean coast. Stations 15 and 16 in New Damietta and Ras El-Barr in the Middle region considered having the highest concentrations of LNi (11.16 and 10.00 µgg-1), respectively. The leachable nickel concentration in sediment of the Western region was fluctuated between a minimum of 0.27 µgg-1 at station 3 in El-Nobarreya and a maximum of 3.29 µgg-1 at station 11 in Maadia (average: 1.17±0.85 µgg-1). In the Middle region, the lowest value of LNi (2.70µgg-1) was observed at station 12 in Rashid west, while the highest level (11.16µgg-1) was observed at station 15 in New Damietta, the average value was 5.88±3.53µgg-1. The distribution of LNi concentration in the Eastern region revealed low concentration (0.15µgg-1) at station 20 in Rafah and high concentration (6.72µgg-1) at station 19 in Port Said, the average value of LNi was 3.44±4.64µgg-1. 5.3.2.6. Leachable Chromium (LCr) The concentrations of leachable Chromium (LCr) in surface sediments at all stations are shown in Table 6 and Figure 10. The highest concentration of LCr (8.22 µgg-1) was observed at station 5 in El-Mex Bay in the Western region and the lowest concentration of LCr (0.56µgg-1) was found at station 12 in Rashid west at the Middle region of the study area. The obtained results showed relatively low concentrations of LCr. The lowest concentrations of LCr (1.26µgg-1) in the sediment of the western region was observed at station 3 in Nobarreya, while the highest levels of LCr (8.22µgg-1) was observed at station 5 in El-Mex Bay, the average level was 3.30±2.38µgg-1. In the midle region, the minimum concentration of LCr (0.56µgg-1) was found at station 12 in Rashid west, while the maximum level (2.97µgg-1) was found at station 16 in Ras El-Barr, the average of LCr was 1.77±1.05µgg-1. The distribution of LCr concentration in the Eastern region revealed low concentration (0.75µgg-1) at station 20 in Rafah and high concentration (2.73µgg-1) at station 19 in Port Said, the average value of LCr was 1.74±1.40µgg-1. 5.3.2.7. Leachable Cobalt (LCo) The concentrations of leachable Cobalt (LCo) in surface sediments are shown in Table 6 and Figure 11. The highest concentration of LCo (8.77µgg-1) was found at station 15 in -117- New Damietta at the Middle region, while the lowest concentration of LCo (0.10µgg-1) was found at the western region at station 2 in Baghoush. In the western region, the lowest level of LCo (0.10µgg-1) was found at station 2 in Baghoush, while the highest level (2.85µgg-1) was observed at station 11 in Maadia, the average value of LCo was 0.67±0.81µgg-1. The minimum concentration of LCo in the middle region was (1.88µgg-1) at station 12 in Rashid west, while the maximum concentration was (8.77µgg-1) in station 15 at New Damietta, the average level of LCo was 4.49±2.81µgg-1. In the eastern region, the lowest concentration of LCo (0.34µgg-1) was found at station 20 in Rafah and the highest concentration of LCo (7.84µgg-1) was observed at station 19 in Port Said, the average value of LCo was (4.09±5.30µgg-1). 5.3.2.8. Leachable Lead (LPb) The concentrations of leachable Lead (LPb) at all stations of the present study are shown in Table 6 and Figure 11. The highest concentration of LPb (51.35µgg-1) was found at the western region (station 5) in El-Mex Bay, while the lowest concentration of LPb (0.54µgg1 ) was found at the Eastern region (station 20) in Rafah. The lowest concentration of LPb (1.78µgg-1) in the Western region was observed at station 11 in Maadia, while the highest level (51.35µgg-1) was observed at station 5 in El-Mex Bay, the average of LPb was 13.36±14.30µgg-1. In the Middle region, the lowest concentration of LPb was (0.77µgg-1) at station 17 in El-Gamil west, while the highest level of LPb was (3.98µgg-1) at station 15 in New Damietta. The average level of LPb was 1.96±1.34µgg-1. The distribution of LPb concentration in the Eastern region revealed low value of (0.54µgg-1) at station 20 in Rafah and high value of (1.56µgg-1) at station 20 in Port Said, the average value of LPb was 1.05±0.72µgg-1. 5.3.2.9. Leachable Cadmium (LCd) The concentrations of leachabel Cadmium (LCd) in surface sediments at all stations are shown in Table 6 and Figure 11. The highest concentration of LCd (0.23 µgg-1) was found at station 1 in El-Salloum in the Western region, while the lower concentration of LCd (0.02µgg-1) was found at station 15 in New Damietta at the Middle region. The LCd level in sediment of the Western region was fluctuated between a minimum of 0.03µgg-1 at station 2 and 3 (Bahgoush and Nobarreya), respectively and a maximum of (0.23µgg-1) at station 1 in El-Salloum (average: 0.08±0.05µgg-1). In the Middle region, the minimum concentration of LCd (0.02 µgg-1) found at station 15 in New Damietta and the maximum level of LPb (0.07µgg-1) was observed at station 17 in El-Gamil west. The average concentration of LPb in this region (Middle) was 0.04±0.02µgg-1. The distribution of LPb level in the Eastern region revealed low value (0.02µgg-1) at station 20 in Rafah and high concentration (0.03µgg-1) at station 19 in Port Said. -118- Table 6: Leachable trace metals concentration (µgg-1 dry weight) of surfacial sediments along the Egyptian Mediterranean coastal area. Region Western Region Middle Region Eastern Region All Regions Station 1 2 3 4 5 6 7 8 9 10 11 Min. Max. Average SD 12 13 14 15 16 17 18 Min. Max. Average SD 19 20 Min. Max. Average SD Min. Max. Average SD Fe 1059.41 169.11 106.63 1565.96 946.81 626.00 1568.98 1417.76 1042.36 653.88 2100.42 106.63 2100.42 1023.40 614.80 1494.21 2026.41 2225.87 6831.61 5481.41 1658.24 3877.94 1494.21 6831.61 3370.81 2092.12 3667.31 94.98 94.98 3667.31 1881.14 2526.02 94.98 6831.61 1930.77 1777.05 Mn 55.11 19.59 10.83 149.06 95.63 162.54 94.43 114.94 261.85 82.41 206.08 10.83 261.85 113.86 76.59 118.89 29.99 110.42 307.27 239.82 130.70 143.61 29.99 307.27 154.39 91.30 171.53 30.20 30.20 171.53 100.87 99.94 10.83 307.27 126.75 81.82 Zn 5.23 0.52 0.11 11.44 49.48 4.27 17.42 14.72 4.01 5.32 7.31 0.11 49.48 10.89 13.92 1.66 2.17 2.61 6.54 6.40 1.49 3.69 1.49 6.54 3.51 2.15 3.63 0.15 0.15 3.63 1.89 2.46 0.11 49.48 7.41 10.94 Cu 1.96 0.23 0.32 4.53 6.34 1.28 8.20 6.21 0.51 2.29 0.86 0.23 8.20 2.98 2.85 0.56 1.01 1.05 2.08 1.93 0.88 1.51 0.56 2.08 1.29 0.57 1.79 0.27 0.27 1.79 1.03 1.07 0.23 8.20 2.19 2.29 -119- Ni 0.74 0.34 0.27 1.33 1.23 0.79 1.74 0.48 1.54 1.09 3.29 0.27 3.29 1.17 0.85 2.70 3.89 3.77 11.16 10.00 2.70 6.90 2.70 11.16 5.88 3.53 6.72 0.15 0.15 6.72 3.44 4.64 0.15 11.16 3.04 3.23 Cr 2.67 2.51 1.26 3.17 8.22 1.79 7.40 4.04 1.35 1.61 2.30 1.26 8.22 3.30 2.38 0.56 2.73 0.78 2.81 2.97 0.98 1.58 0.56 2.97 1.77 1.05 2.73 0.75 0.75 2.73 1.74 1.40 0.56 8.22 2.61 2.01 Co 0.30 0.10 0.29 0.57 0.42 0.18 0.61 0.36 1.42 0.23 2.85 0.10 2.85 0.67 0.81 1.88 2.52 3.06 8.77 7.89 2.38 4.88 1.88 8.77 4.49 2.81 7.84 0.34 0.34 7.84 4.09 5.30 0.10 8.77 2.35 2.82 Pb 7.74 3.15 5.40 10.39 51.35 12.50 19.96 23.10 4.28 7.27 1.78 1.78 51.35 13.36 14.30 1.33 0.94 1.28 3.98 1.66 0.77 3.77 0.77 3.98 1.96 1.34 1.56 0.54 0.54 1.56 1.05 0.72 0.54 51.35 8.14 11.97 Cd 0.23 0.03 0.03 0.07 0.06 0.10 0.09 0.10 0.06 0.07 0.05 0.03 0.23 0.08 0.05 0.06 0.03 0.03 0.02 0.04 0.07 0.04 0.02 0.07 0.04 0.02 0.03 0.02 0.02 0.03 0.03 0.00 0.02 0.23 0.06 0.05 7500 6500 LFe (µgg-1) 5500 4500 3500 2500 1500 500 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 LMn (µgg-1) 250 200 150 100 50 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 50 LZn (µgg-1) 40 30 20 10 0 1 2 3 4 Stations Figure 9: Concentration of LFe, LMn and LZn in surfacial sediments along the Egyptian Mediterranean coastal area. -120- 10 LCu (µgg-1) 8 6 4 2 0 LNi (µgg-1) 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 14 12 10 8 6 4 2 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 10 LCr (µgg-1) 8 6 4 2 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 Stations Figure 10: Concentration of LCu, LNi, LCr in surfacial sediments along the Egyptian Mediterranean coastal area. -121- 10 LCo (µgg-1) 8 6 4 2 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 1 2 3 4 5 7 8 9 10 11 12 13 14 15 16 17 18 19 20 60 50 LPb (µgg-1) 40 30 20 10 0 6 0.3 0.25 LCd (µgg-1) 0.2 0.15 0.1 0.05 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 Stations Figure 11: Concentration of LCo, LPb, LCd in surfacial sediments along the Egyptian Mediterranean coastal area. -122- 5.3.3. Partitioning of Metals It is now widely accepted that the role of aquatic sediments as a sink or as a source of pollutants cannot fully be assessed by measuring total metal concentrations. In addition, determination of total elements does not give an accurate estimate of the likely environmental impact. Instead, it is desirable to have information on the potential availability of metals (whether toxic or essential) to biota under various enviornmental conditions (Davidson et al., 1994)(440). The total content of a given metal is not informative as it does not describe the amount of the metal available for living organisms and thus may overestimate the real threat. The most important from the ecological point of view is to know which part of the total concentration of a given metal is available to living organisms as it determines the real toxic effect of this metal (Bernhard and Neff, 2001)(441). This need demanded development of new analytical methods of bottom sediment study based on fractionation (Glosinska et al., 2005)(442). Speciation is very useful, not only for determining the degree of association of the metals to the sediments but also for differentiating metals with a lithogenic origin from those with an anthropogenic origin (Izquierdo et al., 1997)(443). In the present study, it has been investigated the partitioning of six metals (Fe, Mn, Zn, Ni, Cr, Pb) among different fractions in the sediments of the Egyptian Mediterranean Sea. 5.3.3.1. Fractionation of Iron (Fe) The results of iron concentrations of the different chemical phases: exchangeable (F1), bound to carbonate (F2), bound to Fe/Mn oxides (F3), bound to organic matter (F4) and residual fraction (F5) in the Egyptian Mediterranean coast are listed in Table 7 and the relative percent contribution from the total concentration are shown in Figure 12. The iron concentrations associated with the exchangeable fraction ranged between (0.11µgg-1) at stations 3, 15 in Nobarreya and New Damietta, respectively and (1.02µgg-1) at station 13 in Rashid east with an average (0.29±0.22µgg-1). The regional distribution of Fe concentration in the three zones ranged from a minimum (0.20 µgg-1) at the western region to a maximum (0.43 µgg-1) at the middle region (Table 7 and Figure 14). The amount of iron associated with the carbonate fraction varied from 0.54µgg-1 at station 7 in NIOF and 5.30 µgg-1 in station 10 at electrical power station with an average (2.194±1.34µgg-1) (Table 7). The regional distribution of iron level in the three regions along the coastal area ranged between a minimum (2.00µgg-1) at the western region to a maximum (3.39µgg-1) at the eastern region (Table 7 and Figure 14). The amount of Fe associated with the Fe-Mn oxides fraction varies from 64.59 -1 µgg at station 20 (Rafah) in the eastern region to 1523.75µgg-1 at station 15 (New Damietta) in the middle region with an average (625.60±430.11µgg-1) (Table 7). The regional distribution of Fe level in the three regions ranged from 475.78µgg-1 at the eastern region to 825.74µgg-1 at the middle region (Table 7 and Figure 14). The amount of Fe associated with the organic matter fraction varied from 15.82µgg-1 at station 2 (Baghoush) in the western region and 2655.46µgg-1 at station 16 in Ras El-Barr in the middle region with an average (712.73±664.20 µgg-1) (Table 7). The regional distribution of Fe level in the three regions ranged from 357.10µgg-1 at the western region and 1294.69µgg-1 at the middle region (Table 7 and Figure 14). The amount of Fe associated with the residual fraction varied from 156.96 µgg-1 at station 2 (Baghoush) at the western region and 31423.59 µgg-1 in station 16 (Ras El-Barr) in the middle region with an average (10388.84±9815.05 µgg-1) (Table 7). The regional -123- distribution of Fe concentration in the three regions ranged from 3892.37µgg-1 at the western region and 19967.46µgg-1 at the middle region (Table 7 and Figure 14). 5.3.3.2. Fractionation of Manganese (Mn) The results of Mn concentration of the different chemical phases: exchangeable (F1), bound to carbonate (F2), bound to Fe/Mn oxides (F3), bound to organic matter (F4) and residual fraction (F5) in the surface sediments of the study area from El-Salloum to Rafah are listed in Table 8 and the relative percent contribution from the total concentration are shown in Figure 12. Data listed in Table 8 showed that the amount of Mn associated with the exchangeable fraction varied from ND at station 3 in El-Nobarreya (Western region) to 1.16 µgg-1 at station 18 in El-Gamil east (Eastern region) with an average (0.39 ±0.40 µgg-1). The regional distribution of Mn level in the three regions ranged from 0.15µgg-1 at the Western region to 0.73µgg-1 at the Middle region (Table 8 and Figure 15). Table 8 showed that wide range in the distribution of Mn associated with the carbonate fraction, varied from 0.71 µgg-1 at station 3 in El-Nobarreya (Western region) to 101.38 µgg-1 at station 19 in Port Said (Eastern region) with an average (30.28±32.17 µgg-1). The regional distribution of Mn concentrations in the three regions ranged from 17.46µgg-1 at the Western region to 54.24µgg-1 at the Eastern region (Table 8 and Figure 15). From the obtained data at Table 8, it is observed that the amount of Mn associated with the Fe-Mn fraction varied from 11.43 µgg-1 at station 20 (Rafah; Eastern region) to 186.20 µgg-1 at station 11 (Maadia; Western region) with an average (82.43 ±57.81µgg-1). The regional distribution of Mn concentrations in the three regions ranged from 30.96µgg-1 at the Eastern region to 95.04µgg-1 at the Western region (Table 8 and Figure 15). Table 8 represented that the amount of Mn associated with organic fraction varied from 0.49µgg-1 at station 20 in Rafah (Eastern region) to 32.10 µgg-1at station 15 (New Danietta; middle region) with an average (10.45 ± 9.35µgg-1). The regional distribution of Mn concentrations in the three zones ranged from 6.46µgg-1 at the Western region to 16.00µgg-1 at the Middle region (Table 8 and Figure 15). Data listed in Table 8 showed that the amount of Mn associated with the residual fraction varied from 0.46µgg-1 at station 3 in El-Nobarreya to 599.23µgg-1 at station 19 in Port Said (Eastern region) with an average (178.50±193.00µgg-1). The regional distribution of Mn concentrations in the three regions ranged from 53.53µgg-1 at the Western region to 337.32µgg-1 at the Middle region (Table 8 and Figure 15). 5.3.3.3. Fractionation of Zinc (Zn) The results of Zinc concentrations of the different chemical phases: exchangeable (F1), bound to carbonate (F2), bound to Fe/Mn oxides (F3), bound to organic matter (F4) and residual fraction (F5) in surface sediments of the study area from El-Salloum to Rafah are listed in Table 9 and the relative percent contribution from the total concentration are shown in Figure 12. Table 9 represented that the Zn concentrations associated with the exchangeable fraction ranged from ND at station 16 in Ras El-Barr (Middle region) to 0.25µgg-1 at station 1 in El-Salloum (Western region) with an average 0.04±0.05µgg-1. The regional distribution of Zn levels in the three regions ranged from 0.01µgg-1 at the Middle region to 0.06µgg-1 at the Western region (Table 9 and Figure 16). The amount of Zn associated with the carbonate fraction varied from 0.04µgg-1 at station 18 in El-Gamil East (Middle region) to 2.49µgg-1 at station 5 in El-Mex Bay (Western region) with an average 0.59±0.76µgg-1 (Table 9). The regional distribution of Zn levels in -124- the three zones ranged from 0.06µgg-1 at the Middle region to 1.02µgg-1 at the Western region (Table 9 and Figure 16). From the obtained data at Table 9, it is observed that the amount of Zn associated with the Fe-Mn fraction varied from 0.08 µgg-1 at station 3 in El-Nobarreya (Western region) to 11.01 µgg-1 at station 7 in NIOF (Western region) with an average 3.14±3.48µgg-1. The regional distribution of Zn levels in the three regions ranged from 0.62µgg-1 at the Eastern region to 4.93µgg-1 at the Western region (Table 9 and Figure 16). Table 9 represented that the amount of Zn associated with organic matter fraction varied from ND at station 2, 3, 20 in Baghoush, El-Nobarreya and Rafah, respectively to 4.94µgg-1 at station 7 in NIOF (Western region) with an average 1.21±1.37µgg-1. The regional distribution of Zn concentrations in the three regions ranged from 0.51µgg-1 at the Eastern region to 1.42µgg-1 at the Western region (Table 9 and Figure 16). Data listed in Table 9 showed that the amount of Zn associated with the residual fraction varied from 0.70µgg-1 at station 6 in Western harbour to 35.77µgg-1 at station 7 in NIOF (Western region) with an average 12.49±9.25µgg-1. The regional distribution of Zn concentrations in the three regions ranged from 10.62µgg-1 at the Eastern region to 14.68µgg-1 at the Middle region (Table 9 and Figure 16). 5.3.3.4 Fractionation of Nickel (Ni) The results of application of sequential extraction of Ni in five different chemical phases: exchangeable (F1), bound to carbonate (F2), bound to Fe/Mn oxides (F3), bound to organic matter (F4) and residual fraction (F5) in surface sediments of the study area from ElSalloum to Rafah are presented in Table 10 and the relative percent contribution from the total concentration are shown in Figure 13. The levels of Ni concentrations associated with the exchangeable fration of surface sediments of the Egyptian Mediterranean sea are fluctuated between a minimum of 0.02µgg-1 at station 20 in Rafah (Western region) and a maximum of 0.26µgg-1 at station 16 in Ras El-Barr (Middle region) with an average 0.13±0.06µgg-1 (Table 10). Table 10 and Figure 17 showed the nickel concentration in the three zones, which was 0.11µgg-1 at the eastern region to 0.14µgg-1 at the Middle region. The amount of nickel associated with the carbonate fraction varied from 0.011µgg-1 at station 11 (Maadia; Western region) and station 15 and 17 (New Damietta and El-Gamil west respectively; Middle region) to 0.12 µgg-1 at station 4 and 5 in Dekhaila and El-Mex Bay, respectively with an average 0.06±0.04µgg-1 (Table 10). Table 10 and Figure 17 showed the average of Ni concentration from the total in the three regions, it ranged between 0.04µgg-1 at the Eastern region to 0.07µgg-1 at the western region. Nickel associated with Fe-Mn oxides fraction varied from 0.20µgg-1 at station 2 in Baghoush (Western region) to 6.05µgg-1 at station 15 in New Damietta (Middle region) with an average (1.68±1.76µgg-1) (Table 10). Table 10 and Figure 17 showed the average of Ni concentration from the total in the three regions from the Egyptian Mediterranean coast, it ranged from 0.59µgg-1 (Western region) to 3.45µgg-1 (Middle region). Data listed in Table 10 showed that the amount of Ni associated with the organic matter fraction varied from 0.05µgg-1 at station 20 in Rafah (Eastern region) to 5.70µgg-1 at station 16 in Ras El-Barr (Middle region) with an average 1.43±1.74µgg-1. Table 10 and Figure 17 reperesented Ni concentration associated with the organic matter for the three -125- regions. These amounts represented portions varying from 0.45µgg-1 (Western region) to 3.00µgg-1 (Middle region) from the total. The amount of Ni associated with the residual fraction varied from 0.88 µgg-1 at station 2 in Baghoush (Western region) to 42.67 µgg-1 at station 17 in El-Gamil west (Middle region) with an average (16.51±13.62µgg-1). The regional distribution of Ni levels in the three regions ranged from 5.64µgg-1 at the Western region to 30.85µgg-1 at the Middle region (Table 10 and Figure 17). 5.3.3.5. Fractionation of Chromium (Cr) The results of application of sequential extraction of Cr in five different chemical phases: exchangeable (F1), bound to carbonate (F2), bound to Fe/Mn oxides (F3), bound to organic matter (F4) and residual fraction (F5) in surface sediments of the Egyptian Mediterranean coastal area from El-Salloum to Rafah are listed in Table 11 and the relative percent contribution from the total concentration are shown in Figure 13. Table 11 represented that the chromium concentrations associated with the exchangeable fraction ranged between 0.02µgg-1 at station 18 in El-Gamil east (Middle region) and station 19 in Port Said (Eastern region) to 0.12µgg-1 at station 1 in Salloum (Western region) with an average 0.04±0.03µgg-1. The average concentration of Cr associated with the exchangeable phase in the three regions (Table 11 and Figure 18) ranged from 0.04µgg-1 (Middle region) to 0.05µgg-1 (the Eastern and Western region) from the total. From the obtained data at Table 11, it is observed that the amount of chromium associated with the carbonate fraction varied from 0.03µgg-1 at station 14 in Burullus (Middle region) to 0.89µgg-1 at station 8 in Eastern harbour (Western region) with an average 0.19±0.18µgg-1. Table 11 and Figure 18 showed the average concentration of Cr associated with the carbonate fraction for the three regions, it fluctuated between 0.07µgg-1 (Eastern region) to 0.28µgg-1 (Western region) from the total. Table 11 represented that the amount of Cr associated with Fe-Mn oxides fraction fluctuated between a minium of 0.19 µgg-1 at station 10 in Power station (Middle region) to 4.30 µgg-1 at station 7 in NIOF (Middle region) with an average 1.06±1.02µgg-1. The average concentration of Cr from the total (Table 11 and Figure 18) in the three regions ranged between 0.52µgg-1 (Middle region) to 1.48µgg-1 (Western region). Data listed in Table 11 showed that the amount of Cr associated with the organic fraction varied from 0.15µgg-1 at station 3 in El-Nobarreya (Western region) to 2.39µgg-1 at station 16 in Ras El-Barr (Middle region) with an average 1.05±0.66µgg-1. The average concentration of Cr from the total (Table 11 and Figure 18) in the three regions fluctuated between 0.74µgg-1 (Western region) and 1.54µgg-1 (Middle region). The amount of Cr associated with the residual fraction varies from 1.19µgg-1 at station 2 in Bagous (Western region) to 230.69 µgg-1 at station 13 in Rashid east (Middle region) with an average 63.34±68.62µgg-1. The average concentration of Cr from the total was represented in Table 11 and Figure 18, it ranged from 17.63µgg-1 (Western region) to 125.73 µgg-1 (Eastern region). 5.3.3.6. Fractionation of Lead (Pb) The results of Lead concentrations of the different chemical phases exchangeable (F1), bound to carbonate (F2), bound to Fe/Mn oxides (F3), bound to organic matter (F4) and -126- residual fraction (F5) in surface sediments of the Egyptian Mediterranean coastal area from El-Salloum to Rafah are listed in Table 12 and the relative percent contribution from the total concentration are shown in Figure 13. Data listed in Table 12 showed that the amount of Pb associated with the exchangeable fraction fluctuated from a minimum of 0.05µgg-1 at station 9 in Abu Qir Bay to 0.50µgg-1 at station 13 in Rashid East with an average 0.25±0.14µgg-1. The average concentration of Pb from the total was represented in Table 12 and Figure 19, it ranged from 0.22µgg-1 (Western region) to 0.30µgg-1 (Middle region). The amount of Pb associated with the carbonate fraction fluctuated between a minimum of 0.04µgg-1 at station 12 in Rashid west (Middle region) to 25.88 µgg-1 at station 5 in El-Mex Bay (Western region) with an average 2.74±5.95µgg-1 (Table 12). The average concentration of Pb from the total was represented in Table 12 and Figure 19, it ranged from 0.29µgg-1 (Middle region) to 4.72µgg-1 (Western region). From the obtained data at Table 12, it is observed that the amount of Pb associated with the Fe-Mn fraction varied from 0.37µgg-1 at station 17 in El-Gamil west (Middle region) to 15.71 µgg-1 at station 5 in El-Mex Bay (Western region) with an average 3.70±4.12µgg-1. The average concentration of Pb from the total was represented in Table 12 and Figure 19, it ranged from 1.07µgg-1 (Middle region) to 5.84µgg-1 (Western region). Table 12 represented that the amount of Pb associated with organic matter fraction varied from 0.25µgg-1 at station 12 (Rashid west) to 3.41µgg-1 at station 8 in Eastern harbour (Middle region) with an average 0.95±0.78µgg-1. The average concentration of Pb from the total was represented in Table 12 and Figure 19 it fluctuated between 0.38µgg-1 (Eastern region) to 1.18µgg-1 (Western region). Data listed in Table 12 showed that the amount of Pb associated with the residual fraction varied from 0.66µgg-1 at station 6 in Western harbour (Western region) to 7.49µgg-1 at station 10 in power station (Middle region) with an average 4.59±2.08µgg-1. The average concentration of Pb from the total was represented in Table 12 and Figure 19 it fluctuated between 3.42µgg-1 (Eastern region) to 5.16µgg-1 (Middle region). -127- Table 7: Fractionation of Fe concentration coastal area. Region Station F1 0.14 1 0.12 2 0.11 3 0.16 4 0.22 5 0.25 6 Western Region 0.16 7 0.37 8 0.21 9 0.26 10 0.24 11 0.20 Average 0.29 12 1.02 13 0.49 14 0.11 15 Middle region 0.27 16 0.69 17 0.12 18 0.43 Average 0.27 19 0.27 Eastern region 20 0.27 Average 0.29 Average 0.22 SD All region 0.11 Minimum 1.02 Maximum (µgg-1) and its relative percentage from the total in sediments of the Egyptian Mediterranean % 0.002 0.041 0.038 0.003 0.007 0.019 0.004 0.011 0.002 0.003 0.003 0.012 0.003 0.005 0.003 0.000 0.001 0.004 0.000 0.002 0.001 0.022 0.012 0.009 0.012 0.000 0.041 F2 2.47 1.52 0.89 1.17 0.91 1.36 0.54 1.66 3.02 5.30 3.18 2.00 2.08 2.19 0.90 1.37 2.51 3.55 2.50 2.16 5.28 1.50 3.39 2.19 1.34 0.54 5.30 % 0.03 0.52 0.30 0.03 0.03 0.10 0.01 0.05 0.03 0.07 0.03 0.11 0.02 0.01 0.00 0.00 0.01 0.02 0.01 0.01 0.02 0.13 0.07 0.07 0.13 0.00 0.52 -128- F3 441.43 118.49 70.67 723.10 485.16 482.64 1371.76 856.24 369.17 287.79 573.75 525.47 464.47 397.84 526.10 1523.75 1478.51 522.64 866.88 825.74 886.98 64.59 475.78 625.60 430.11 64.59 1523.75 % 5.18 40.45 24.25 15.47 16.28 35.61 32.65 26.48 4.02 3.58 5.88 19.08 5.23 1.82 2.73 5.51 4.16 3.09 3.55 3.73 3.38 5.40 4.39 12.24 12.58 1.82 40.45 F4 199.80 15.82 18.51 405.54 299.13 174.99 530.78 321.86 656.57 240.01 1065.11 357.10 700.67 578.10 1115.20 1878.56 2655.46 913.98 1220.87 1294.69 1098.11 165.58 631.85 712.73 664.20 15.82 2655.46 % 2.34 5.40 6.35 8.67 10.04 12.91 12.63 9.95 7.14 2.98 10.92 8.12 7.89 2.64 5.78 6.79 7.47 5.40 4.99 5.85 4.19 13.85 9.02 7.42 3.43 2.34 13.85 F5 7876.49 156.96 201.18 3545.21 2195.12 695.97 2298.38 2053.70 8164.81 7515.20 8113.02 3892.37 7708.55 20890.14 17662.76 24243.63 31423.59 15482.45 22361.07 19967.46 24224.97 963.68 12594.33 10388.84 9815.05 156.96 31423.59 % 92.44 53.59 69.05 75.83 73.65 51.35 54.70 63.51 88.81 93.37 83.17 72.68 86.85 95.52 91.49 87.69 88.37 91.49 91.45 90.41 92.41 80.60 86.50 80.27 14.50 51.35 95.52 Table 8: Fractionation of Mn concentration (µgg-1) and its relative percentage from the total in sediments of the Egyptian Mediterranean coastal area. Region Station F1 % F2 % F3 % F4 % F5 % 0.249 0.22 4.69 4.19 41.166 36.78 4.073 3.64 61.736 55.16 1 0.02 0.08 0.87 3.50 21.01 84.73 1.30 5.24 1.60 6.46 2 ND 0.01 0.71 4.44 13.99 87.31 0.86 5.36 0.46 2.87 3 0.04 0.02 14.55 8.68 114.68 68.41 8.55 5.10 29.81 17.78 4 0.07 0.06 7.05 6.08 100.40 86.52 5.08 4.38 3.44 2.97 5 0.17 0.10 10.69 6.52 133.29 81.27 7.17 4.37 12.68 7.73 6 Western region 0.08 0.05 9.53 6.29 102.11 67.35 10.18 6.72 29.71 19.60 7 0.01 0.01 3.55 2.78 105.43 82.57 5.84 4.57 12.85 10.07 8 0.36 0.09 65.61 16.83 173.52 44.52 12.75 3.27 137.54 35.29 9 0.17 0.05 14.79 4.76 53.60 17.26 3.85 1.24 238.04 76.68 10 0.45 0.14 60.04 18.82 186.20 58.36 11.39 3.57 60.97 19.11 11 0.15 0.08 17.46 7.54 95.04 65.01 6.46 4.31 53.53 23.06 Average 0.64 0.32 11.70 5.91 33.31 16.82 6.77 3.42 145.68 73.54 12 0.04 0.01 5.35 0.87 14.09 2.29 5.57 0.91 590.23 95.93 13 0.55 0.14 16.74 4.25 36.17 9.19 9.69 2.46 330.40 83.95 14 0.80 0.13 75.64 11.91 167.17 26.33 32.10 5.06 359.14 56.57 15 1.14 0.20 65.76 11.35 157.30 27.15 32.06 5.53 323.07 55.77 16 Middle region 0.78 0.18 57.35 13.53 63.81 15.06 9.87 2.33 291.94 68.89 17 1.16 0.24 72.51 15.11 69.42 14.47 15.97 3.33 320.77 66.85 18 0.73 0.17 43.58 8.99 77.32 15.90 16.00 3.29 337.32 71.64 Average 1.05 0.14 101.38 13.04 50.49 6.49 25.54 3.28 599.23 77.05 19 0.07 0.18 7.09 17.81 11.43 28.72 0.49 1.24 20.72 52.06 20 Eastern region 0.56 0.16 54.24 15.43 30.96 17.60 13.02 2.26 309.97 64.55 Average 0.39 0.12 30.28 8.83 82.43 43.08 10.45 3.75 178.50 44.22 Average 0.40 0.09 32.17 5.50 57.81 30.74 9.35 1.57 193.00 30.94 SD All region ND 0.01 0.71 0.87 11.43 2.29 0.49 0.91 0.46 2.87 Minimum 1.16 0.32 101.38 18.82 186.20 87.31 32.10 6.72 599.23 95.93 Maximum ND= Not detected -129- Table 9: Fractionation of Zn concentration (µgg-1) and its relative percentage from the total in sediments of the Egyptian Mediterranean coastal area. Region Station F1 % F2 % F3 % F4 % F5 % 0.25 0.85 0.56 1.87 3.11 10.47 0.06 0.18 25.75 86.62 1 0.07 3.84 0.12 7.26 0.15 8.62 ND 0.12 1.36 80.17 2 0.03 0.50 0.08 1.11 0.08 1.22 ND 0.03 6.55 97.14 3 0.04 0.23 0.91 5.31 7.35 42.83 1.70 9.89 7.17 41.74 4 0.06 0.16 2.49 6.34 10.36 26.38 4.44 11.31 21.92 55.81 5 0.03 0.37 1.13 14.89 5.08 67.26 0.62 8.16 0.70 9.32 6 Western region 0.08 0.15 2.37 4.37 11.01 20.33 4.94 9.12 35.77 66.03 7 0.02 0.11 1.32 8.90 8.53 57.53 1.47 9.92 3.49 23.54 8 0.03 0.21 0.56 4.56 2.04 16.64 0.47 3.83 9.16 74.75 9 0.05 0.38 1.10 9.20 2.52 21.09 0.30 2.50 7.99 66.83 10 0.02 0.15 0.56 4.62 3.98 32.91 1.57 13.01 5.96 49.31 11 0.06 0.63 1.02 6.22 4.93 27.75 1.42 6.19 11.44 59.20 Average 0.02 0.26 0.05 0.67 0.56 6.99 0.50 6.28 6.81 85.80 12 0.02 0.11 0.07 0.42 0.84 4.82 0.33 1.86 16.24 92.78 13 0.01 0.10 0.05 0.36 0.90 6.96 0.75 5.82 11.16 86.76 14 0.01 0.03 0.06 0.29 1.56 7.31 2.00 9.35 17.72 83.03 15 Middle region ND 0.00 0.08 0.34 2.03 8.28 2.28 9.29 20.13 82.09 16 0.01 0.10 0.07 0.50 0.55 4.01 0.59 4.36 12.39 91.03 17 0.01 0.06 0.04 0.20 0.92 4.47 1.24 6.02 18.32 89.25 18 0.01 0.10 0.06 0.40 1.05 6.12 1.10 6.14 14.68 87.25 Average 0.04 0.16 0.07 0.32 1.01 4.62 1.03 4.72 19.62 90.18 19 0.03 1.61 0.09 4.34 0.24 12.06 ND 0.10 1.62 81.89 Eastern region 20 0.03 0.89 0.08 2.33 0.62 8.34 0.51 2.41 10.62 86.03 Average 0.04 0.47 0.59 3.79 3.14 18.24 1.21 5.79 12.49 71.70 Average 0.05 0.87 0.76 4.01 3.48 18.58 1.37 4.11 9.25 24.17 SD All region ND 0.00 0.04 0.20 0.08 1.22 ND 0.03 0.70 9.32 Minimum 0.25 3.84 2.49 14.89 11.01 67.26 4.94 13.01 35.77 97.14 Maximum ND= Not detected -130- Table 10: Fractionation of Ni concentration (µgg-1) and its relative percentage from the total in sediments of the Egyptian Mediterranean coastal area. Region Station F1 % F2 % F3 % F4 % F5 % 0.12 2.17 0.06 1.11 0.56 10.11 0.48 8.70 4.30 77.92 1 0.09 6.97 0.03 2.43 0.20 15.74 0.08 6.11 0.88 68.75 2 0.17 2.23 0.10 1.25 0.41 5.36 0.16 2.09 6.79 89.08 3 0.05 0.79 0.12 1.74 0.72 10.80 0.15 2.19 5.64 84.48 4 Western region 0.17 3.78 0.12 2.64 0.35 7.92 0.12 2.73 3.65 82.94 5 0.15 5.24 0.05 1.94 0.59 21.13 0.07 2.37 1.93 69.32 6 0.15 2.10 0.08 1.20 0.73 10.36 0.24 3.38 5.82 82.97 7 0.18 9.35 0.03 1.53 0.50 25.38 0.25 12.82 1.00 50.92 8 0.11 0.66 0.07 0.41 0.50 2.96 1.05 6.29 15.03 89.68 9 0.04 0.33 0.06 0.47 0.45 3.42 0.41 3.08 12.25 92.70 10 0.11 1.32 0.01 0.13 1.48 17.80 1.91 22.97 4.81 57.78 11 0.12 3.18 0.07 1.35 0.59 11.91 0.45 6.61 5.64 76.96 Average 0.05 0.19 0.09 0.32 1.49 5.29 1.12 4.00 25.32 90.20 12 0.18 0.41 0.02 0.05 1.86 4.30 0.94 2.17 40.21 93.07 13 0.13 0.37 0.06 0.17 2.54 7.23 1.93 5.49 30.42 86.74 14 Middle region 0.16 0.52 0.01 0.04 6.05 19.46 5.36 17.25 19.49 62.74 15 0.26 0.62 0.08 0.19 5.81 13.81 5.70 13.56 30.19 71.82 16 0.08 0.16 0.01 0.02 2.60 5.48 2.06 4.34 42.67 90.00 17 0.09 0.25 0.11 0.31 3.81 10.72 3.92 11.02 27.63 77.69 18 0.14 0.36 0.06 0.16 3.45 9.47 3.00 8.26 30.85 81.75 Average 0.20 0.58 0.06 0.18 2.49 7.37 2.54 7.52 28.45 84.34 19 Eastern region 0.02 0.09 0.01 0.05 0.42 1.75 0.05 0.22 23.65 97.90 20 0.11 0.34 0.04 0.12 1.46 4.56 1.30 3.87 26.05 91.12 Average 0.13 1.91 0.06 0.81 1.68 10.32 1.43 6.91 16.51 80.05 Average 0.06 2.55 0.04 0.85 1.76 6.63 1.74 5.90 13.62 12.75 SD All region 0.02 0.09 0.01 0.02 0.20 1.75 0.05 0.22 0.88 50.92 Minimum 0.26 9.35 0.12 2.64 6.05 25.38 5.70 22.97 42.67 97.90 Maximum -131- Table 11: Fractionation of Cr concentration (µgg-1) and its relative percentage from the total in sediments of the Egyptian Mediterranean coastal area. F4 Region Station F1 % F2 % F3 % % F5 % 1 2 3 4 5 Western region 6 7 8 9 10 11 Average 12 13 14 Middle region 15 16 17 18 Average 19 Eastern region 20 Average Average All Region SD Minimum Maximum 0.12 0.09 0.04 0.03 0.04 0.04 0.03 0.03 0.05 0.03 0.02 0.05 0.06 0.03 0.04 0.04 0.03 0.04 0.02 0.04 0.02 0.08 0.05 0.04 0.03 0.02 0.12 0.48 2.79 1.04 0.25 0.16 0.57 0.15 0.41 0.07 0.10 0.09 0.56 0.08 0.01 0.04 0.07 0.03 0.02 0.02 0.04 0.01 0.16 0.08 0.33 0.63 0.01 2.79 0.24 0.29 0.09 0.25 0.17 0.19 0.30 0.89 0.20 0.22 0.20 0.28 0.13 0.19 0.03 0.11 0.08 0.06 0.08 0.10 0.07 0.08 0.07 0.19 0.18 0.03 0.89 0.97 9.65 2.26 2.03 0.64 2.93 1.65 12.17 0.32 0.69 0.84 3.10 0.19 0.08 0.03 0.17 0.08 0.03 0.08 0.09 0.03 0.14 0.09 1.75 3.27 0.03 12.17 -132- 1.01 0.93 0.55 1.79 2.40 1.33 4.30 2.74 0.74 0.19 0.34 1.48 0.48 0.52 0.40 0.57 0.40 0.76 0.55 0.52 0.65 0.61 0.63 1.06 1.02 0.19 4.30 4.05 30.45 14.23 14.64 9.17 20.92 23.79 37.34 1.16 0.59 1.45 14.34 0.70 0.22 0.47 0.89 0.38 0.42 0.54 0.52 0.32 1.16 0.74 8.14 11.52 0.22 37.34 1.24 0.55 0.15 0.26 0.60 0.19 1.88 0.34 0.61 0.84 1.44 0.74 1.03 1.13 1.33 2.11 2.39 1.05 1.74 1.54 1.59 0.54 1.07 1.05 0.66 0.15 2.39 4.99 17.98 3.98 2.10 2.31 2.95 10.38 4.61 0.95 2.57 6.20 5.37 1.51 0.48 1.57 3.30 2.27 0.58 1.72 1.63 0.79 1.02 0.90 3.61 4.12 0.48 17.98 22.27 1.19 3.02 9.88 22.94 4.60 11.58 3.33 62.52 31.33 21.25 17.63 66.82 230.69 82.77 61.21 102.07 178.97 98.85 117.34 199.72 51.75 125.73 63.34 68.62 1.19 230.69 89.51 39.14 78.49 80.98 87.72 72.63 64.03 45.46 97.50 96.06 91.41 76.63 97.53 99.20 97.89 95.58 97.24 98.94 97.63 97.72 98.85 97.52 98.19 86.17 17.96 39.14 99.20 Table 12: Fractionation of Pb concentration (µgg-1) and its relative percentage from the total in sediments of the Egyptian Mediterranean coastal area. Region Station F1 % F2 % F3 % F4 % F5 % 0.09 0.64 1.97 14.30 3.72 26.96 0.64 4.64 7.38 53.46 1 0.23 4.91 0.69 14.93 1.66 36.05 0.39 8.52 1.64 35.59 2 0.23 2.31 4.55 45.63 3.23 32.34 0.53 5.34 1.44 14.38 3 0.21 1.54 1.14 8.33 4.51 32.84 0.74 5.35 7.14 51.94 4 0.38 0.80 25.88 54.40 15.71 33.03 2.32 4.87 3.28 6.90 5 0.17 0.92 9.98 54.51 7.00 38.28 0.49 2.68 0.66 3.61 6 Western region 0.32 1.45 5.01 22.60 10.45 47.12 1.73 7.80 4.66 21.03 7 0.05 0.24 1.36 6.41 10.54 49.83 3.41 16.13 5.79 27.38 8 0.05 0.54 0.46 5.42 1.68 19.75 1.47 17.25 4.85 57.04 9 0.45 3.53 0.58 4.59 3.51 27.68 0.65 5.11 7.49 59.09 10 0.27 3.31 0.31 3.87 2.24 27.89 0.64 8.00 4.57 56.93 11 0.22 4.72 4.72 21.36 5.84 33.80 1.18 7.79 4.45 35.21 Average 0.31 5.67 0.04 0.82 1.84 34.01 0.25 4.69 2.96 54.82 12 0.50 6.64 0.14 1.82 0.76 10.13 0.53 6.98 5.61 74.44 13 0.35 5.56 0.53 8.36 1.11 17.56 0.51 8.06 3.80 60.46 14 Middle region 0.28 3.04 0.46 5.08 0.65 7.09 1.07 11.73 6.67 73.07 15 0.40 4.89 0.27 3.27 1.49 18.26 1.28 15.68 4.72 57.90 16 0.17 2.27 0.26 3.43 0.37 4.92 1.01 13.23 5.79 76.15 17 0.07 0.74 0.31 3.58 1.25 14.29 0.52 5.90 6.60 75.49 18 0.30 4.12 0.29 3.76 1.07 15.18 0.74 9.47 5.16 67.47 Average 0.45 5.81 0.45 5.81 1.50 19.51 0.26 3.35 5.02 65.53 19 Eastern region 0.13 3.60 0.40 10.76 0.87 23.42 0.50 13.42 1.82 48.81 20 0.29 4.70 0.42 8.28 1.18 21.47 0.38 8.38 3.42 57.17 Average 0.25 2.92 2.74 13.90 3.70 26.05 0.95 8.44 4.59 48.70 Average All region 0.14 2.07 5.96 17.09 4.12 12.32 0.78 4.52 2.08 22.83 SD 0.05 0.24 0.04 0.82 0.37 4.92 0.25 2.68 0.66 3.61 Minimum 0.50 6.64 25.88 54.51 15.71 49.83 3.41 17.25 7.49 76.15 Maximum -133- Fe 100 80 60 40 20 0 1 2 F1 3 4 5 6 F2 7 8 9 10 11 12 13 14 15 16 17 18 19 20 F3 F4 F5 Mn 100 80 60 40 20 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 F1 F2 F3 F4 F5 Zn 100 80 60 40 20 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 F1 F2 F3 F4 F5 Figure 12: Percent contribution of Fe, Mn and Zn fractions from the total concentration in surfacial sediments of the Egyptian Mediterranean coastal area -134- Ni 100 80 60 40 20 0 1 2 3 F1 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 F2 F3 F4 F5 Cr 100 80 60 40 20 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 F1 F2 F3 F4 F5 Pb 100 80 60 40 20 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 F1 F2 F3 F4 F5 Figure 13: Percent contribution of Ni, Cr, and Pb fractions from the total concentration in surfacial sediments of the Egyptian Mediterranean coastal area -135- Western region 0% 0% 19% 8% 73% Middle region 0% 4% 6% 90% Eastern region 0% 4% 9% 87% F1 F2 F3 F4 F5 Figure 14: The relative percentage of Fe fractions from the total concentration in the three regions, Egyptian Mediterranean coastal area -136- Western region 0% 23% 8% 4% 65% Middle region 0% 9% 16% 3% 72% Eastern region 0% 15% 18% 65% 2% F1 F2 F3 F4 F5 Figure 15: The relative percentage of Mn fractions from the total concentration in the three regions, Egyptian Mediterranean Sea sediments -137- Western region 1% 6% 28% 59% 6% Middle region 0% 0% 6% 6% 88% Eastern region 1% 2% 8% 2% 87% F1 F2 F3 F4 F5 Figure 16: The relative percentage of Zn fractions from the total concentration in the three regions, Egyptian Mediterranean Sea sediments -138- Western region 3% 1% 12% 7% 77% Middle region 0% 0% 9% 8% 83% Eastern region 0% 0% 5% 4% 91% F1 F2 F3 F4 F5 Figure 17: The relative percentage of Ni fractions from the total concentration in the three regions, Egyptian Mediterranean Sea sediments -139- Western region 1%3% 14% 5% 77% Middle region 0% 1% 2% 0% 97% Eastern region 0% 0% 1% 1% 98% F1 F2 F3 F4 F5 Figure 18: The relative percentage of Cr fractions from the total concentration in the three regions, Egyptian Mediterranean Sea sediments -140- Western region 2% 21% 35% 8% 34% Middle region 4% 4% 15% 9% 68% Eastern region 5% 8% 21% 58% 8% F1 F2 F3 F4 F5 Figure 19: The relative percentage of Pb Fractions from the total concentration in the three regions, Egyptian Mediterranean Sea sediments -141- 5.3.4. Acid volatile sulfide (AVS) and simultaneously extracted metals (SEM) Acid volatile sulfide (AVS) is one of the major chemical components that control the activities and availability of metals in the interstitial waters of sediments. Sulfide reacts with several divalent transition metal cations (cadmium, copper, nickel, lead, and zinc) to form highly insoluble compounds that are not bioavailable (USEPA, 2004)(444). The concentrations of reactive sulfide in anoxic sediments play a major role in the bioavailability and toxicity of specific cationic metals of environmental concern (e.g. Cu, Cd, Pb, Ni, and Zn). Because these metals are capable of forming relatively insoluble sulfide minerals, the reaction between soluble metal species with sulfide serves to partition metals from porewater into the solid phase (Edenborn, 2005)(445). The concentration of AVS and SEM (µmoleg-1, dry weight) in the sediments of the Egyptian Mediterranean coast from El-Salloum to Rafah are shown in Table 13. From the obtained data in Table 13, it is observed that the range and average concentrations of SEM were 0.0001-0.0011 µmole/g (Average: 0.0002 µmole/g) for Cd, 0.002-0.017 µmoleg-1 (Average: 0.0095 µmoleg-1) for Cu, 0.003-0.029 µmole/g (Average: 0.016µmoleg-1) for Ni, 0.004-0.008 (Average: 0.006 µmoleg-1) for Pb and 0.003-0.025 (Average: 0.014 µmoleg-1) for Zn. The distribution of SEM in the western region revealed low concentration (0.016µmoleg-1) at station 2 and 3 in Baghoush and El-Nobarreya, respectively and high concentration (0.241µmoleg-1) at station 5 in El-Mex Bay. The average value of SEM in this region was (0.128±0.075µmoleg-1). In the Middle region, the lowest concentration of SEM (0.045µmoleg-1) was found at station 17 in El-Gamil west, while the highest concntration (0.133µmoleg-1) was found at station 15 in New Damietta. The average value of SEM in the Middle region was (0.079±0.036µmoleg-1). The lowest concentration of SEM (0.012 µmoleg-1) in the Eastern region was observed at station 20 in Rafah, while the highest concentration (0.079µmoleg-1) was observed at station 19 in Port Said. The average value of SEM in this region was (0.046±0.047µmoleg-1). Figure 21 showed that the average concentration of SEM in the three regions can be arranged as follows: Western region (0.128±0.075µmoleg-1) > Middle region(0.079±0.036µmoleg-1) > Eastern region(0.046±0.047µmoleg-1). The lowest concentration of AVS (0.015µmoleg-1) in the western region was observed at station 2 in Baghoush, while the highest concentration (31.326µmoleg-1) was observed at station 7 in NIOF. The average value of AVS in this region was (3.307±9.348 µmoleg-1). In the Middle region, the lowest concentration of AVS (0.038 µmoleg-1) was found at station 18 in El-Gamil East, while the higest concentration (0.11µmoleg-1) was observed at station 15 in New Damietta. The average of AVS in this region was (0.058±0.025µmoleg-1). The distribution of AVS level in the Eastern region revealed low value (0.029µmole g-1) at station 19 in Port Said and high value (0.119 µmole g-1) at station 20 in Rafah. The average value of AVS in this region was (0.074±0.064 µmoleg-1). Figure 22 showed that the average concentration of AVS in the different regions can be arranged as follows: Western region (3.307±9.348 µmoleg-1) > Eastern region (0.074±0.064 µmoleg-1) > Middle region (0.058±0.025µmoleg-1) -142- Table 13: Concentration of AVS and SEM (µmoleg-1, dry weight) in surfacial sediments of the Egyptian Mediterranean coastal area from El-Salloum to Rafah Region Station 1 2 3 4 5 6 7 Western 8 region 9 10 11 Average SD Min Max 12 13 14 15 16 Middle 17 region 18 Average SD Min Max 19 20 Eastern Average region SD Min Max AVS 3.505 0.015 0.036 0.26 0.335 0.032 31.326 0.058 0.576 0.123 0.116 3.307 9.348 0.015 31.326 0.049 0.052 0.044 0.11 0.043 0.071 0.038 0.058 0.025 0.038 0.11 0.029 0.119 0.074 0.064 0.029 0.119 Pb 0.026 0.009 0.008 0.018 0.033 0.011 0.008 0.014 0.016 0.023 0.011 0.016 0.008 0.008 0.033 0.006 0.009 0.004 0.009 0.008 0.005 0.007 0.007 0.002 0.004 0.009 0.008 0.004 0.006 0.003 0.004 0.008 Cd 0.0011 0.0001 0.0001 0.0005 0.0006 0.0001 0.0003 0.0004 0.0003 0.0002 0.0002 0.0004 0.0003 0.0001 0.0011 0.0003 0.0001 0.0002 0.0001 0.0001 0.0003 0.0001 0.0002 0.0001 0.0001 0.0003 0.0001 0.0003 0.0002 0.0001 0.0001 0.0011 -143- Zn 0.071 0.004 0.002 0.091 0.174 0.038 0.141 0.139 0.049 0.07 0.083 0.078 0.056 0.002 0.174 0.017 0.019 0.022 0.047 0.056 0.021 0.03 0.030 0.015 0.017 0.056 0.025 0.003 0.014 0.016 0.003 0.025 Cu 0.031 0.002 0.005 0.021 0.023 0.008 0.029 0.046 0.011 0.039 0.019 0.021 0.014 0.002 0.046 0.011 0.009 0.012 0.017 0.017 0.009 0.012 0.012 0.003 0.009 0.017 0.017 0.002 0.0095 0.011 0.002 0.017 Ni 0.022 0.002 0.002 0.016 0.011 0.009 0.024 0.007 0.014 0.008 0.021 0.012 0.008 0.002 0.024 0.016 0.028 0.011 0.059 0.041 0.01 0.038 0.029 0.018 0.01 0.059 0.029 0.003 0.016 0.018 0.003 0.029 SEM 0.151 0.016 0.016 0.147 0.241 0.066 0.201 0.206 0.089 0.14 0.134 0.128 0.075 0.016 0.241 0.05 0.064 0.049 0.133 0.122 0.045 0.087 0.079 0.036 0.045 0.133 0.079 0.012 0.046 0.047 0.012 0.079 Western region 10% 13% 0% 17% 60% Middle region 9% 0% 37% 38% 16% Eastern region 13% 35% 0% 31% 21% SEMPb SEMCd SEMZn SEMCu SEMNi Figure 20: The relative percentage of simultaneously extracted metals in the three regions, Egyptian Mediterranean Sea sediments -144- 0.15 0.1 0.05 0 Western region M iddle region Eastern region Figure 21: The average of SEM in the three regions, Egyptian Mediterranean Sea sediments 4 3 2 1 0 Western region M iddle region Eastern region Figure 22: The average of AVS in the three regions, Egyptian Mediterranean Sea sediments -145- Chapter VI Discussion The study of marine sediments represents a useful tool for determining the actual state of environmental pollution and for understanding the origin and mechanism of the phenomena. Sediments could be regarded as a historical reflection to changes occurring in the overlying water system and can be used as good indicators for metals in any study area (Salomons and Forstner, 1984)(181). Marine sediment contamination by persistent anthropogenic chemicals poses one of the worst problems to coastal and estuarine ecosystems around the world. The accumulation of urban, industrial and agricultural contaminants in marine sediments enters the sea through river mouths or by direct discharge (Usero et al., 2008)(446). Due to its ecological importance, the evaluation of marine sediment quality constitutes an important area of research (Silva et al., 2004)(447). Sediments may accumulate various kinds of hazardous and toxic substances, including trace metals levels many times higher than water column concentrations, causing a serious problem due to their toxicity and their ability to accumulate in the biota (Usero et al., 2008)(446). The most crucial property of heavy metals is that they are bioavailable and not biodegradable in the environment. In aquatic ecosystem, sediments are the main sink for trace metals (Ridgway and Shimmield, 2002)(448). Metal fractionations in sediments are strongly dependent on substrata geochemical conditions, such as pH and redox potential. When environmental conditions change, some of the sediment-bound contaminants can remobilize and be released back into the water acting as a source of pollution that can have adverse effects on living organisms (Li et al., 2001)(235). The toxicity and fate of the metal in sediment depend on its chemical form, and therefore, quantification of the different forms of a metal is more meaningful than the estimation of its total concentration (Usero et al., 2008)(446). In this study, fractionation of metals in sediment has been investigated to determine its speciation and ecotoxic potential, as well as evaluation of metal potential toxicity based on the simultaneously extracted metals (SEM) and acid volatile sulfides (AVS) analysis. 6.1. Geochemical Analysis 6.1.1. Grain size distribution Trace metals introduced into aquatic environment can have a detrimental effect on the organisms living in that environment, as well as, on food chain, sediments are able to store and accumulate metals to some extent, due to their adsorption capacity (Stigliani, 1991)(449). Sediment exists as complex and dynamic mixtures of mineral particles, particular organic material (detritus) and microbes. The flocculated chemicals and contaminants in sediments may be associated with any of these sediment fractions (Tabata et al., 2009)(213). Grain size plays a significant role in determining elemental concentrations in sediments (Szefer et al., 1996)(450). Studies on the grain size effect are important to both environmental studies and environmental management (Zhang et al., 2002)(451). Trace metals may occur in both fine and sand fractions of sediments. However, most natural and anthropogenic substances (metals and organic contaminants) show a much higher affinity to fine particulate matter than the coarse fraction. In marine sediments, anthropogenic trace metals are usually preferentially associated with finer grains (Ewais et al., 2000)(452). Sediment grain size is therefore -146- important in determining how sediments are transported and deposited in the marine environment, and in the distribution of both natural and anthropogenically introduced concentrations of metals in the marine environment (Stevenson, 2001)(453). The accumulation of trace metal in fine grained estuarine sediments may cause a significant long term contamination problem, as reworking of contaminated sediments and possible early diagenetic release of heavy metals may cause continued input into the environment even after cessation or reduction in industrial discharges (Rosales Hoz et al., 2003)(454). In the present study Particle size analysis was carried out by dry sieving through screens; particles <63µm were not differentiated into their clay and silt components. The percent of sand, silt and clay together with the texture of all samples are shown in Table 4. The obtained results showed that the particle size distributions for sediments samples from Rafah to El-Salloum were dominated by sand particles (>63µm) with high percentages 86.85100% (average: 99.15%). In general, the particle size distribution was specific to the respective sediments. Fine sand (0.250-0.125 mm) and very fine sand (0.125-0.062 mm) were the dominated fractions of all sediment samples. Course sand (1.0-0.5 mm) was observed at station 5 in El-Mex Bay and station 6 in the Western harbour (Western region). The highest value of sand content (100%) was observed at stations 3, 5, 6 at Nobareya, ElMex Bay, Western harbour, respectively in the Western region and station 12 in Rashid west (the Middle region) and station 20 at Rafah (the Eastern region) and the lowest value (86.85%) was observed at station 1 in El-Salloum (the Western region). These results are in agreement with those obtained by El-Nemr et al. (2007a)(61). The Middle region was dominated by fine and very fine sand. This is in agreement with El-Fishawi et al. (1976)(455) who stated that the beach sands of the Nile delta are mostly fine grained sand (0.13-0.25 mm) with some local medium sand (0.25-0.5 mm) and composed of quartz and feldspares with smaller amounts of heavy minerals and shell fragments, being 13%. 6.1.2. Total carbonate Carbonate is often an important component of marine sediments and has been found to be an important indicator of provenance and dispersal of terreginous material (Loring and Rantala, 1992)(416). The interaction between trace metals and carbonate minerals is of an environmetnal interest since they influence the distribution of ions in the aquatic environment and the association with carbonate minerals can provide important pathways for scavenging toxic metals like Zn, Pb, and Cd (Korfali and Davies, 2004)(456). The Egyptian Mediterranean coast contains a wide variety of sediments. Coastal sediments are mainly composed of two principal types: carbonate sands and quartz dominant sands (Hilmy, 1951)(359). The results of carbonate as % CaCO3 in the Egyptian Mediterranean coastal sediments are listed in Table 4 and Figure 3. The study area was divided into three regions, which revealed differences in the distribution of CaCO3. In the Western region, the results showed that the sediments at station 1 (El-Salloum) are characterized by relatively medium CaCO3 percentage (34.79%). Sediments from station 2 at Baghoush to station 8 at the Eastern harbour (west of Alexandria) are characterized by high percentage of CaCO3 ranged from 67.24 at station 5 (El-Mex) to a maximum percentage (the western harbour) (95.57%). The major sources of carbonate in the western harbor's sediments are the detrital fragmental molluscal shells and skeletons in addition to the tubiform skeletons of Hydroids norvegicus (Saad et al., 2004)(91). These results are in agreement with the results of Anwar et al. (1984)(360) who stated that the western region from Mersa Matrouh to Alexandria is mainly composed of pure oolitic carbonate. The non-arrival of riverine muds or terrestrial discharge -147- also plays a leading role in keeping the sediments of the western part of the Egyptian shelf as highly carbonate content (El-Wakeel et al., 2006)(285). The oolitic grains constitute an average of 78% and 89% of the bottom and beach sediments, respectively. Further westward, sand at El-Salloum showed an average oolite content in the nearshore of 58% (Anwar et al., 1981)(361). Also, Nasr (1978)(362) found that the carbonate content of beach sand west of Alexandria varies between 44 and 99% The relative percentage of CaCO3 at eastern region of Alexandria was characterized by relatively low % (14.69, 15.64, 22.11%) at Power station, Maadia and Abu Qir Bay, respectively. The lowest value of carbonate were found in the marine sediments where quartz sand was predominates. It is thus evident that the shells of organisms are the principle contributors of carbonate in sediments (Khalil et al., 2007)(320). This result is in agreement with those of Selim (1974)(457) who found that the sediment along the coast west of Alexandria consists mainly of calcareous material, which creates from limestone rocks and ridges. These sediments differ from those found east of Alexandria, which creates from the Nile Delta. The seaward calcareous ridges consist of Pleistocene carbonates with a marine nature. In the middle region, the relative percentage of CaCO3 was low ranged from 2.85% at station 13 (Rashid east) to 6.08% at station 15 (New Damietta). This is in agreement with Hilmy (1951)(359) who mentioned that beach sand from Alexandria to Rashid primarily consists of quartz grains with common shell fragments. The Nile River has been identified as the major source of quartz-rich sediments and heavy minerals on the Nile Delta beaches (Frihy, 1994)(363). In the eastern region, the relative percentages of CaCO3 are low, 6.33% at station 20 (Rafah) and 7.32% at station 19 (Port Said). 6.1.3. Organic matter Organic carbon is determined to assess the role played by the organic fraction of sediments in the transport, deposition and retention of trace metals (Loring and Rantala, 1992)(416). Organic matter in the sediment played an important role in the adsorption of trace metals. Further, it was suggested that the organic matter content in general could be used as a simple pollution index of the sediment (Ottosen and Villumsen, 2006)(458). The composition and structure of the organic matter in the sediment are varying due to its origin and geological history in the marine and aquatic environment. Phytoplankton and zooplankton are the most abundant sources of the organic material in the sediments (Grathwohl, 1990)(459). The organic matter content of the sediment is a result of the contribution of terrigenous materials and the decomposition of plants and animals by the action of bacteria (Draz, 1983)(460). Total organic matter (TOM) is one of the most important collectors of pollutants in the marine sediments. Organic matter tends to form strong organo-metallic complexes with metals, rendering them immobile. An increase in TOM content may result in an increase in levels of metals in the marine sediment (Massoud et al., 2007)(294). Total organic carbon added to the sediments, primarily through the decomposition of plant and animal matter, can directly binds and/or adsorb heavy metals and also contains heavy metals accumulated by plants that have been exposed to contaminated sediment during their life time (Peltier et al., 2003)(461). Nonetheless, high percentage of organic matter -148- and/or small grains in sediments, reduces the metals availability, and undoubtedly plays a major role in controlling metal's concentration in the pore water (Ankley et al., 1996)(23). Organic carbon has a significant role in geochemical cycles of major and trace metals that accumulate in sediments; it may be used as an index of depositional environment and sedimentary processes (Seralathan et al., 1993)(462). The results of organic matter contents in the Egyptian Mediterranean coastal sediments are listed in Table 4 and Figure 4. The organic matter values ranged from 0.08 to 1.72 % with a mean value of 0.56%, obtaining the highest percentage from station 7 (NIOF; western region). The common values for coastal sediments are from 0.32% to 1.76% (Diaz-de alba, 2011)(463). Therefore, the present study showed relatively low organic matter content at most of the locations. Low organic carbon values were observed which might be due to the mixing processes and marine sedimentation at the sediment water interface, where the rate of delivery, as well as the rate of degradation by microbial-mediated processes, can be high (Canuel and Martens, 1993((464). The present work findings are agreeable with Revelle and Shepard (1938)(465), who mentioned that the decrease in the organic carbon seaward is explained by the increase of the grain size and the carbonate content. El-Wakeel (2006)(285) mentioned that the relatively lower values of organic carbon in the beach sediments of the western region from El-Dakhaila to Sidi Kirir can be the result of: a) the position of this area further away from the riverine input or terrestrial discharge which is regarded as the main contributer of the organic detritus; b) the remarkable increase of carbonate; and c) waves and longshore and rip currents may remove the fine particles and the associated organic carbon away from the beach. 6.2. Trace metal distribution 6.2.1. Total metals With the rapid industrialization and economic development in coastal region trace metals are continuing to be introduced to estuarine and coastal environment around the world (Santos et al., 2005)(466). Various studies have demonstrated that sediments from coastal areas greatly contaminated by trace metals. Therefore, the evaluation of metal distribution in surface sediments is useful to assess pollution in the marine environment (Jayaprakash et al., 2008)(467). These trace metals participate in various biogeochemical mechanisms that have significant mobility, which affects the ecosystems through bioaccumulation and biomagnification processes and are potentially toxic for environment and human life (Ip et al., 2007)(428). Metals such as Ni, Cd, Cr and Zn, etc. are used in contamination studies in marine systems due to their relationship with anthropogenic activities (Burton et al., 2004)(468). The range and the average values of trace metal (Fe, Mn, Cr, Ni, Zn, Pb, Cu, Co, Cd) concentrations enter the aquatic marine environment from both natural and anthropogenic sources were given in Table 5 and Figures 6, 7, and 8. Metal contents ranged in the following intervals: Fe: 243.5-38045.05µgg-1; Mn: 17.3-1085.7µgg-1; Cr: 4.1-297.95µgg-1; Ni: 1.760.3µgg-1; Zn: 2.1-62.21µgg-1; Pb: 3.34-53.67µgg-1; Cu: 0.46-26.3µgg-1; Co: 0.4-26.4µgg-1; Cd: 0.04-0.47µgg-1 dry weight. The average contents of the study area were Fe: 13255.7µgg-1; Mn: 380.7µgg-1; Cr: 82.7µgg-1; Ni: 25.9µgg-1; Zn: 22.2µgg-1; Pb: 13.2µgg-1; Cu: 8.5µgg-1; Co: 8.2µgg-1; Cd: 0.22µgg-1 dry weight, allow arranging trace metals as the following: Fe> Mn> Cr> Ni> Zn> Pb> Cu> Co> Cd. In order to give more information about the level of pollution of the studied sediments, the measured metals concentrations were also compared with those given in the literature by Taylor and Wedepohl (1961)(469), Taylor (1964)(470), Bowen (1979)(471), Salomons and Forstner (1984)(181), Taylor and Mclennan (1995)(472), Wedepohl (1995)(473). -149- The distribution patterns of metal concentrations increases towards the Middle region of the study area. Metals concentrations were found to be higher in the middle region of the study area compared to the eastern and the western region. It has been observed that the average of the total trace metals (Fe, Mn, Zn, Ni, Cr, Co) contents in the western region was lower than the average of those metals in the middle and the eastern region. Whereas, the average of the total Pb and Cd content in the western region was higher than the average of the total Pb and Cd content of the middle and eastern region. The average of the total cupper content in the western region was higher than the average of the total cupper content in the eastern region and lower than the average of the cupper content in the middle region. On the other hand, the average of the CaCO3 in the western region was higher than the average of CaCO3 in the middle and the eastern region. This result may be explained as carbonate usually contains insignificant amounts of trace metals and act mainly as dilutents. Under certain circumstances, however, carbonates can fix contaminants such as cadmium and copper (UNAP/Med POL, 2000)(474). Total Iron (TFe) Iron was the most abundant metal measured and there were large variations in the levels of total Fe among sites. The average of total Fe levels in µgg-1 dry weight at the studied regions were: the middle region (25516.22 ± 10090.1)>the eastern region (17696.95 ± 23015.70)>the western region (4646.03 ± 3459.61) as shown in Figure 23. Table 14 showed that the concentration of Fe in the sediments along the Egyptian Mediterranean coast was below the crustal average (Taylor, 1964)(470), Average shale (Turekian and Wedeohl, 1961)(469), mean sediment concentration (Salomons and Forstner, 1984)(181) and the average continental crust (Wedepohl, 1995)(473) at all locations. While, the concentration of iron at New Damietta (Stations 15; 38045.05µgg-1) and at Ras El-Barr (station 16; 37398.1µgg-1) (the middle region) exceeds the upper crust concentration reported by Taylor and Mclennan (1995)(472). The results of Fe (unpolluted area) were in the range from 3,000 to 40,820 µgg-1 (Santamaria-Fernandez et al., 2005; Svete et al., 2001)(475, 476), while polluted regions had higher values in the range between 51,000 and 116,000 µgg-1 (Buykx et al., 2000; Sulivan and Taylor, 2003)(477, 478) compared to these studies, the sediments along the Egyptian Mediterranean coast are considered unpolluted by Fe. By comparing the obtained results with previous results of other Mediterranean regions, the results were slightly higher than that reported by Mostafa et al. (2004)(298) for the western harbour, Egypt (8819-36140µgg-1), Legorburu and Canton (1991)(479) for the Pasajes harbour, Spain (3830-35500µgg-1), Buccolieri et al. (2006)(160) for Taranta Gulf, Italy (26313-36098µgg-1), Khairy (2008)(226) for Abu Qir Bay (1120-37100µgg-1) and lower than the range reported by Gargouri et al. (2010)(480) for the coast of Safax (41011-50163µgg-1) and the range reported by Diaz de Alba et al. (2011)(463) for Algeciras Bay, Spain (18285-42756µgg-1) (Table 15). Total Manganese (TMn) Distribution of Mn in the study area ranged from 17.2µgg-1 to 1085.72µgg-1 dry weight with an average value of 380.71µgg-1 (Figure 23). The average Mn levels (µgg-1 dry weight) measured for the three regions was in the following sequence: the middle region (597.02±203.84)> eastern region (570.24±729.00)> the western region (208.60±163.08). The concentration of Mn in the study area was below the crustal average reported by Taylor (1964)(470) and the average shale reported by Turekian and Wedepohl (1961)(469) at all locations except station 19 in Port Said at the eastern region (1085.72µgg-1). Stations 13 (Rashid East) and station 15 (New Damietta), at the Middle region and station 19 (Port Said) in the eastern region exceeds the Mean sediment (Salomons and Forstner, 1984)(181). The obtained results are higher than the results reported by Mostafa et al. (2004)(298) for the western harbour, Egypt, Pasajes harbour, Spain reported by Legorburu and Canton (1991)(479), -150- Nables harbour (Italy) reported by Adamo et al. (2005)(184), El-Mex Bay (Egypt) reported by Abdallah (2007a)(292), Abu Qir bay reported by Khairy (2008)(226) and quite similar with the results obtained by Diaz-de Alba et al. (2011)(463) for Algeciras bay, Spain and Themaikos Gulf, Greece reported by Violintzis et al. (2009)(481) and lower than the results obtained by Buccolieri et al. (2006)(160) for Taranto Gulf, Italy (Table 15). From the obtained results, Fe and Mn display quite similar pattern of distribution. This is in agreement with the results of Sarkar and Bhattacharya (2010)(482) who stated that this might be due to the early diagenetic processes as well as the strong association to the geochemical matrix between the two elements. The total Fe and Mn concentrations were low at the western region of the study area, which is dominated by high CaCO3 and sand content, whereas the middle and the eastern indicates high values of total Fe and Mn. It seems likely that the enrichment results in the reduction of Fe in the sediment during the oxidation of organic matter (Francois, 1988)(483). The iron and manganese can be converted to complex hydroxyl compounds that may eventually precipitate (Riley and Chester, 1971)(31). It is well established that iron and manganese oxides are excellent scavengers for trace metals (Tessier et al., 1979)(15). This would lead the co-precipitation of other metals in the water column and so increase the concentration of many metals in sediments. Nasr et al. (1990)(325) stated that the occurrence of these two metals is mainly controlled by natural processes such as Nile water supply, or even coastal erosion deposition. Total Chromium (TCr) Chromium and Ni displays quite similar pattern of distribution, these elements are used as markers of metal industries (Loska et al., 2004)(484). The mean Cr concentration in µgg-1 dry weight for the three regions were (178.37±149.81; eastern region) > (146.53±84.69; Middle region) > (24.76±22.97; western region) as represented in Figure 23. There was large variability in the levels of Cr among the sites. The highest concentration (297.95µgg-1) of Cr was found at station 13 (Rashid east; Middle region) and the lowest concentration (4.08µgg-1) of Cr was found at station 2 (Baghoush; Western region). Cr concentrations in the middle region and the eastern region are in agreement with previous studies which reported high values of Cr in polluted sediments. For example, it was reported that the levels of Cr in sediments from the Aegean Sea (Greec) were in the range of 44.6-154.0µgg-1 (Aloupi and Angelidis, 2002)(485) and 53.0117.0 µgg-1 in sediments from the Gulf of Finland (Leivouri, 1998)(134). The concentration of Cr at station 9 (Abu Qir Bay; western region), stations 12, 13, 14, 15, 16, 17, 18 (Rashid west, Rashid east, Burullus, Ras El-Burr, El-Gamil west and El-Gamil east, respectively; middle region) and stations 19, and 20 (Port Said and Rafah; eastern region) was higher than the upper crust background (35µgg-1) (Taylor and Mclennan, 1995)(472) and the Average continental crust background (35 µgg-1) (Wedepohl (1995)(473), which explained a new input of toxic Cr to those stations. On the other hand, according to Taylor (1964)(470) and Bowen (1979)(471), the concentration of Cr at stations 13, 14, 16, 17, 18, and 19 exceeds the background concentration of the upper crust and the mean crust (Table 14). Cr concentrations in the western region are in agreement with the results obtained by Alomary and Belhadj (2007)(120) in sediments from the Algerian Mediterranean Sea sediments which were in the range (2.6-18.9µgg-1), which considered unpolluted with Cr. The results were in agreement with the results obtained by Diaz de Alba et al. (2011)(463) for Algeciras bay, Spain and higher than reported by Gargouri et al. (2010)(480) for the Coast of Safax, Taranto Gulf, Italy (Buccolieri et al. (2006)(160), Nables Harbour, Italy (Adamo et al., 2005)(184), El-Mex Bay, Egypt reported by Abdallah et al. (2007a)(292) and lower than the range reported for the western harbour reported by Mostafa et al. (2004)(298) (Table 15). -151- Total Nickel (TNi) Figure 24 showed that the average Ni levels (µgg-1 dry weight) measured for the three regions were in the following sequence: (49.48±8.64; Middle region) > (37.61±13.88; eastern region) > (8.81±5.72, western region). There was large variability in the level of Ni among sites. The highest concentration of Ni (60.25µgg-1) was observed at station 17 (El-Gamil west; Middle region) and the lowest concentration of Ni (1.65µgg-1) was found at station 2 (Baghoush; western region). These results are in agreement with those of Gargouri et al. (2010)(480) for the coast of Sfax, Tunisia, which was in the range (7-55µgg-1) and Alomary and Belhadj (2007)(120) for the Algerian Mediterranean Sea (0.8-54.9µgg-1) Table 15. Table 14 showed that stations 13, 16, 17 (Rashid east, Ras El-Burr, El-Gamil west; Middle region) are considered polluted with Ni when compared to mean sediment (52µgg-1) reported by Salomons and Forstner (1984)(181) and the average continental crust (56µgg-1) reported by Wedepohl (1995)(473). On the other hand, all sediments samples considered as unpolluted with Ni when compared with the crustal average (75µgg-1) (Taylor, 1964)(470) and the average shale (68µgg-1) (Turekian and Wedepohl, 1961)(469). Total Zinc (TZn) The average Zn levels (µgg-1 dry weight) at the studied regions were in the following sequence: the western region (23.43±20.07) > the middle region (21.90±6.81) > the eastern region (16.33±19.40) as shown in Figure 24. There were slight variations in the levels of Zn at the three regions. High concentration of Zn (62.21µgg-1) was observed at station 7 (NIOF; the western region). Zn was observed to be lower than the crustal average reported by Taylor (1964)(470), the upper crust (Taylor and Mclennan, 1995)(472), Mean crust (Bowen, 1979)(471), Average shale (Turekian and Wedepohl, 1961)(469), Mean sediment (Salomons and Forstner, 1984)(181) and the average continental crust reported by Wedepohl (1995)(473) at all stations (Table 14). The levels of Zn in the sediments are within the permissible levels which indicate its normal concentration and reflect the background value in sediments. These results are in agreement with the results reported for Algerian Mediterranean Sea sediments (5.3-48.7 µgg1 ) (Alomoray and Belhadj, 2007)(120) and lower than the surface marine sediments of Sfax coast, Tunisia (39-117µgg-1) reported by Gargouri et al. (2010)(480), the Pasajes harbour, Spain (447-1390µgg-1) reported by Legorburu and Canton (1991)(479), Taranto Gulf, Italy (86.8129µgg-1) reported by Buccolieri et al. (2006)(160), Nables harbour (41-1196µgg-1), Italy (Adamo et al., 2005)(184), Themaikos Gulf (84-537µgg-1), Greece (Violontzis, 2009)(481), Mediterranean sea (29.4-509.3µgg-1), France (Fernex et al., 2001)(486) and Sardina, Italy (1983239µgg-1) reported by Caredda et al. (1999)(487) and higher than reported by Sabhi et al. (2000)(488) (9.2-37.7µgg-1) for the Moroccan Mediterranean coast (Table 15). Total Lead (TPb) Data obtained at Figure 24 showed that the average Pb levels (µgg-1 dry weight) measured for the three regions were in the following sequence: (western region; 18.93±13.73) > (Middle region; 6.70±1.37) > (Eastern region; 5.01±2.35). The maximum concentration of lead (53.67µgg-1) reported at station 5 (El-Mex; western region). The elevated concentrations of Pb observed in EL-Mex Bay may be related to the release of Pb through the previous discharge from the Chlor-Alkali plant, discharge of freshwater from EL-Umum Drain carrying industrial, agricultural and sewage effluents and atmospheric deposition, where Pb is released from the combustion of gasoline from motor vehicles (Masoud et al., 2007)(294). Abdel-Moati, (2001)(489) pointed out that 44 % of the TPb enters EL-Mex Bay from industrial wastes, 33 % from agricultural wastes discharged via EL-Umum Drain by the EL-Mex pumping station and 23 % from sewage effluents. Lead enters the bay either in the dissolved or particulate form (Saad et al., 2001)(490). An important source of lead in EL-Mex Bay is from the Portland Cement Factory (in Wadi EL-Kamar). Lead content was generally high in -152- the surface of the western harbor. There is a relationship between dispersed oil from ships and lead enrichment (Saad et al., 2004)(91). Table 15 showed that stations 5, 6, 7, 8 at El-Mex Bay, Western harbour, NIOF and Eastern harbor respectively, in the western region are considered as polluted with Pb when compared to upper crust (20µgg-1) (Taylor and Mclennan,1995)(472), average shale (20 µgg-1) (Turekian and Wedepohl, 1961)(469) and the Mean sediment (19µgg-1) (Salomons and Forstner, 1984)(181). The level of Pb in sediments of the Middle and the Eastern region were agreed with the levels which indicate its normal concentrations and reflects the background value concentrations in sediments. Sadiq et al. (2003)(491) reported that low concentrations of lead still might pose a threat to life in a marine environment in comparison with other heavy metals. Table 15 showed that the values obtained in this study are in agreement with the results of Alomary and Belhadj for the coast of Algeria (2007)(120) and lower than the results obtained by Gargouri et al. (2010)(480) for the coast of Sfax, (Caredda et al. (1999)(487) for Sardina, Italy, Fernex et al. (2001)(486) for Mediterranean Sea, France, Feldstein et al. (2003)(492) and higher than the results reported by Sabhi et al. (2000)(488) for the Moroccan Mediterranean coast. Total Cupper (TCu) Anthropogenic sources of copper are primarily related to textile production, marine antifouling agents, pipes and copper based fungicides or pesticides (PIO, 2005)(493). The average concentration of Cu (µgg-1 dry weight) for the three regions were as follows: the Middle region (9.86±4.47)> the Western region (7.93±7.36) > the Eastern region (6.48±6.94) as represented in Figure 25. Cupper values ranged from 0.46 to 26.26µgg-1 with an average of 8.46µgg-1. Table 14 showed that the concentration of Cu in the study area was below the crustal average reported by Taylor (1964)(470) and the mean crust (50µgg-1) (Bowen, 1979)(471) and the average shale (45µgg-1) (Turekian and Wedepohl, 1961)(469) and the mean sediment (33µgg-1) (Salomons and Forstner, 1984)(181) at all stations. On the other hand, Cu concentrations is lower than the upper curst and the average continental crust (25µgg-1) reported by Taylor and Mclennan (1995)(472) and (Wedepohl, 1995)(473) respectively, at all stations except at station 7 (NIOF) in the western regon (26.26µgg-1). Therefore, the investigated samples are considered unpolluted with Cu. These results are in agreement with that obtained by Alomary and Elhadj (2007)(120) for the Algerian Mediterranean Sediments and the results of Gargouri et al. (2010)(480) for Safx coast and Feldsterin (2003)(492) and lower than the results obtained by Benamar et al. (1999)(494) for Algiers Bay, Algeria and higher than that reported for the Moroccan Mediterranean coast (Sabhi et al., 2000)(488) (Table 15). Total Cobalt (TCo) As shown from data in Figure 25, the average Co concentration (µgg-1 dry weight) measured for the three regions were in the following sequence: the middle region (16.96±6.91)> the eastern region (9.50±10.71)> the western region (2.46±1.89). The highest value (26.39µgg-1) found at station 16 (Ras El-Barr) and the lowest value (0.43µgg-1) found at station 2 (Baghoush; western region) when compared to the Co background concentrations (Table 14), the studied surface sediments were found not to be contaminated by Co. However, slight contamination is to be considered in station 16 in Ras El-Barr. These results are in agreement with the results of Adamo et al. (2005)(184) for Nables harbour, Italy and lower than that results obtained by Khairy (2008)(226) for Abu Qir Bay, Egypt (Table 15). -153- Total Cadmium (TCd) Cadmium is presented relatively rare in the earth with the average concentration of 0.2µgg-1 in earth's crust (Mason and Moore, 1991)(495). In present study, the concentration of Cd was in the range of 0.04-0.47 µgg-1 (dry weight), the lowest concentration (0.04µgg-1) observed at station 15 (New Damietta; Middle region) and station 19 (Port Said; Eastern region) and the highest concentration (0.47µgg-1) observed at station 6 (Western harbour; western region). Mostafa et al. (2004)(298) stated that the presence of high concentrations of Cd in the sediments of the western harbour appears to be directly related to urban and industrial runoff discharged from the El-Mahmoudiya Canal. The mean Cd concentrations for the three regions can be arranged in the following sequence: the western region (0.29±0.15 µgg-1) > the Middle region (0.12±0.07µgg-1) > the eastern region (0.11±0.10µgg-1). In former studies of Cd concentration in marine sediments, the concentration of Cd in unpolluted areas were within the range of 1.56-8.0 µgg-1 (Buykx et al., 2000; Santamaria-Fernandez et al. 2005; Svete et al. 2001)(475-477). The concentrations of Cd in the Mediterranean Sea sediments ranged between 0.1 and 2.3 µgg-1 dry weight (UNEP, 1978)(496). Donazzolo et al. (1984)(497) reported probable background cadmium concentrations, as calculated from core samples, of 1.2 µgg-1 dry weight. A probable background cadmium concentration should be in the range of 0.1 to 2.5 µgg-1 dry weight (Sabhi et al., 2000)(488). Frignani and Giordani (1983)(498) quote a value of 0.4 µgg-1 dry weight for Aegean Sea sediments. Thus the investigated sediments are considered unpolluted by Cd. When compared with former studies on the other Mediterranean regions (Table 15), the concentration of Cd of the present study was lower than reported by Caredda et al. (1999)(487), Jdid et al. (1999)(499), Fernex et al. (2001)(486), Feldstein et al. (2003)(492) and are in the range reported by Sabhi et al. (2000)(488). -154- 30000 Fe in µgg-1 25000 20000 15000 10000 5000 0 Western Middle Eastern 600 Mn in µgg-1 500 400 300 200 100 0 Western Middle Eastern Western Middle Eastern 200 Cr in µgg-1 150 100 50 0 Figure 23: The average of total Fe, Mn and Cr levels in µgg-1 dry weight at the studied regions -155- 50 Ni in µgg-1 40 30 20 10 0 Western Middle Eastern Western Middle Eastern Western Middle Eastern 25 Zn inµgg-1 20 15 10 5 0 20 Pb in µgg-1 15 10 5 0 Figure 24: The average of total Ni, Zn and Pb levels in µgg-1 dry weight at the studied regions -156- 10 Cu in µgg-1 8 6 4 2 0 Western Middle Eastern Western Middle Eastern Co in µgg-1 20 15 10 5 0 0.3 Cd in µgg-1 0.25 0.2 0.15 0.1 0.05 0 Western Middle Eastern Figure 25: The average of total Cu, Co and Cd levels in µgg-1 dry weight at the studied regions -157- Table 14. Average concentrations (µgg-1) of total trace metals in sediments along the Egyptian Mediterranean coastal area compared with noncontaminated sediments Fe Mn Zn Cu Ni Cr Co Pb Cd Present study 243.48 17.25 2.05 0.46 1.65 4.08 0.43 3.34 0.04 Min. conc. 38045.05 1085.72 62.21 26.26 60.25 297.95 26.39 53.67 0.47 Max. conc. 13255.69 380.71 22.19 8.46 25.93 82.74 8.24 13.17 0.22 Average conc. 12911.36 305.38 15.84 6.22 20.96 90.18 8.40 11.90 0.15 SD (N=20) a 56300 950 70 55 75 100 25 12.5 0.2 Crustal average 35000 600 71 25 20 35 10 20 0.098 Upper crustb 41000 950 75 50 100 14 0.11 Mean crustc 47000 850 95 45 68 90 19 20 0.3 Average shaled e 41000 770 95 33 52 72 14 19 0.17 Mean sediment 43200 65 25 56 35 14.8 0.1 Average Continental crustf a Taylor (1964)(470) b Taylor and Mclennan (1995)(472) c Bowen (1979)(471) d Turekian and Wedepohl (1961)(469) e Salomons and Forstner (1984)(181, 473) f Wedepohl (1995)(473) -158- Table 15. Concentrations of trace metals (µgg-1) determined in sediments of the present study compared to other parts along the Mediterranean coast. Location Cd Cu Cr Co Fe Mn Ni Zn Pb The present study 0.04-0.47 0.46-26.3 4.1-297.95 0.43-26.39 243.5-38045.1 17.3-1086 1.7-60.25 2.05-62.21 3.34-53.67 Western harbour, Egypt(298) Western harbour, Egypt(500) Pasajes harbour, Spain(479) Coast of Safax(480) Taranto Gulf, Italy(160) Nables Harbour, Italy(184) El-Mex Bay, Egypt(292) Algeciras Bay, Spain(463) Mediterranean Sea, Algeria(120) Mediterranean Sea, France(486) Sardina, Italy(487) 0.61-2.44 39.207 33-649 NA 8819-36140 139-317 13-53 58.5-382 38-1070 0.07-0.64 0.3-19 NA NA 5000-29000 15-40 NA 0.23-4.74 NA 1.2-6.64 25-3726 NA NA 3830-35500 64-365 17-99 477-1390 45-346 5.5-7 13-29 41-82 NA 41011-50163 NA 7-55 39-117 18-88 NA 42.4-52.3 75.2-102.8 NA 26313-36098 552-2826 47.9-60.7 86.8-129 44.7-74.8 0.2-2.5 40-415 10.3-161.8 1.9-7.2 NA 95-535 NA 41-1196 37-314 4.3-11.9 11.5-52.2 27.6-114.9 NA 709-3063 132-592.3 NA 89.3-592.3 NA 0.1-22 5-25 30-251 5-22 18285-42756 235-967 19-144 33-117 12-39 0.1-2.3 1.1-10.4 2.6-18.9 NA NA NA 0.8-54.9 5.3-45.7 1.3-11.5 0.15-3.4 14.82.6 NA NA NA NA NA 29.4-509.3 20.1-393.6 0.21-13.4 2.77-51.3 NA NA NA NA 0.9-51.3 198-3239 74-772 Abu Qir bay, Egypt(226) Themaikos Gulf, Greece(481) Moroccan Med. Coast(488) NA: Not available 0.08-3.54 0.95-127 4.66-186 0.727-22.8 1120-37100 58.6-582 2.05-40.5 5.77-717 2.71-129 0.3-8.4 32-130 21-470 NA NA 590-890 63-130 84-537 38-190 0.03-0.25 1.2-6.7 NA NA NA NA NA 9.2-37.7 0.175-0.25 -159- 6.2.1.1. Assessment of sediment quality Sediment quality guidelines (SQG) Pollution of the natural environment by trace metals is a worldwide problem. Trace metals from natural and anthropogenic sources continously enter the aquatic ecosystem where they pose a serious threat because of their toxicity, long time persistence and bioaccumulaiton (Chon et al., 2010)(501). Sediment is more conservative than water, as it accumulates historical data on processes within water bodies and the effect of anthropogenic factors on these processes. For these reasons, sediment quality parameters have been used as environmental indicators and their ability to trace and monitor contamination sources is largely recognized. Sediment show a high capacity to accumulate and eventually integrate the low concentrations of trace metals usually found in water (Vallejuelo et al., 2010)(502). Sediments can act as both a source and a sink for potential toxic compounds. In order to predict adverse biological effects in contaminated sediments, numerous Sediment Quality Guidelines (SQGs) have been developed over the past decade (McCready et al., 2006; MacDonald et al., 2000)(201, 503), in order to protect aquatic organisms living in or near the sediments from the toxic effects associated with sediment-bound contaminats. They include sediment quality criteria, sediment quality objectives and sediment quality standards. These guidelines are useful for the evaluation of spatial variations of sediment contamination, the classification of the contamination state of the sediments, the design of monitioring programs, interpretation of historical data, and for environmental assessments for future remedial actions (MacDonald et al., 2000)(503). Numerous sediment quality guidelines are used to protect aquatic biota from the harmful and toxic effects related with sediment bound contaminants (McCready et al., 2006)(201). These guidelines evaluate the degree to which the sediment-associated chemical status might adversely affect aquatic organisms and are designed for the interpretation of sediment quality. They are also used to rank and prioritize contaminated areas for further investigation (Diaz-de Alba et al., 2011)(463). SQGs are developed using a variety of approaches, such as effect-rang approach, effect-level approach and apparent effect-threshold approach. The selection of the most appropriate SQGs is not trivial; each derived numerical value may differ significantly based on the derivation procedure, the objective of the calculation and the ability of the Guidelines to match the selected geological background of the specific area (MacDonald et al., 2000)(503). Based on the SQGs proposed by USEPA (Perin et al., 1997)(504), sediments were categorized into three classes; nonpolluted, moderately polluted and heavily polluted. The chemical contamination in the sediments was evaluated by comparison with the sediment quality guidelines proposed by USEPA. These criteria are shown in Table 16. According to US EPA, the concentration of Cd at all stations under investigation was belonged to unpolluted sediments. Figure 26 showed that the concentration of Fe at stations (17 and 18) in El-Gamil west and east was moderately polluted while stations (13, 14, 15, 16 and 19) in Rashid east, Burullus, New Damietta, Ras El-Barr and Port Said respectively were highly polluted. Figure 26 also showed that the concentration of Cr at stations (1, 7, 10, 11 and 20) in El-Salloum, NIOF, Electric power station, Maadia and Rafah, respectively was moderately polluted. Stations (9, 12, 13, 14, 15, 16, 17, 18 and 19) in Abu Qir Bay, Rashid west, Rashid east, Burullus, New Damietta, Ras El-Barr, El-Gamil west, El-Gamil east and Port Said respectively were heavily polluted. The concentration of Mn at stations (9, 10, 11, 17 and 18) in Abu Qir Bay, Electric power station, Maadia, El-Gamil west and east respectively was moderately polluted while at stations (13, 14, 15, 16 and 19) in Rashid east, Burullus, New -160- Damietta, Ras El-Barr and Port Said was heavily polluted. Finally from the obtained data in Figure 27, it was observed that the concentration of Zn at all stations was belonged to unpolluted sediments. Sediment at all stations was classified as not toxic with cupper except station 7 in NIOF which was moderately polluted with Cu. While, Pb at all stations was belonged to unpolluted except for station 5 in El-Mex which was moderately polluted. It was noted that the concentration of Ni at stations (12, 14, 15, 18, 19 and 20) in Rashid west, Burullus, New Damietta, El-Gamil east, Port Said and Rafah, respectively was belonged to moderately polluted sediments. Also Figure 27 showed that Ni at stations (13, 16 and 17) in Rashid east, Ras El-Barr and El-Gamil west, respectively was belonged to heavily polluted. Another method used in this study to assess the impacts of trace metals in the Egyptian Mediterranean coastal area was the Soil and Aquatic Sediment Guidelines and Standards issued by the New York State Department of Environmental Conservation (NYSDEC) (1999)(505). The total trace metal concentrations are compared with the two benchmarks of lowest effect level (LEL) and severe effect level (SEL), which signifies chronic, long term impacts of contamination to benthic organisms (Table 16). Macro benthic communities are considered good indicators of ecosystem health as benthos shows the real effects of pollution on the communities, being an integrator of the recent pollution history in the sediment and of different kinds of pollutants, which can be synergistic (OcchipintiAmbrogi and Forni, 2004)(506). If trace metal concentration in the sediment is lower than LEL, it would be tolerated by the majority of benthic organisms. If the concentration is more than the LEL but lower than the SEL concentration, the sediments is considered to be contaminated, but with moderate impacts on benthic life. If SEL, is exceed; this indicates a clear disturbance to the sediment-dwelling benthic communities and would be detrimental to the majority of them. If all the heavy metal concentrations are higher than SEL it could severely impact health of this biota (Graney and Erisen, 2004)(507). From the obtained data at table 5, it was observed that Cd was less than the LEL at all stations of the present study, which mean that the sediments would be tolerated by the majority of benthic organisms. The concentration of Cr at stations (1, 9, 10, 11, 15, 16 and 20) in El-Salloum, Abu Qir Bay, Electric power station, Maadia, New Damietta, Ras El-Barr and Rafah, respectively was higher than the LEL but lower than the SEL which mean that the sediment is considered to be contaminated, but with moderate impacts on benthic life. While, the concentration of Cr at stations (13, 14, 17, 18 and 19) in Rashid east, Busullus, El-Gamil West and El-Gamil east and Port Said, respectively exceeded the SEL concentration, this indicates a clear disturbance to the sediment-dwelling benthic communities and would be detrimental to the majority of them The concentration of Cu at most of the stations under investigation was lower than LEL which means that it would be tolerated by the majority of benthic organisms. While, the concentration of Cu at station 7 in NIOF and station 16 in Ras El-Barr were higher than the LEL and lower than the SEL which mean that the sediment was considered to be contaminated, but with moderate impacts on benthic life. Results showed that the concentration of Pb at all stations of the Middle and the eastern region were lower than the LEL which means that it would tolerated by the majority of benthic organisms. While, the concentration of Pb at station 5 in El-mex Bay was higher than the LEL and lower than the SEL which mean that the sediment was considered to be contaminated, but with moderate impacts on benthic life. Stations (1, 6, 7 and 8) in El-Salloum, Western harbour, NIOF and Eastern harbour was higher than the LEL but lower than which means that the sediment was -161- considered to be contaminated, but with moderate impacts on benthic life. It was observed that Zn concentration was less than the LEL at all stations of the present study, which mean that the sediments would be tolerated by the majority of benthic organisms. SQGs are developed using a variety of approaches, such as effect rang approach, effect –level approach and apparent effect threshold approach. The selection of the most appropriate SQGs is based on the derivation procedure, the objective of the calculation and the ability of the Guidelines to match the selected geological background of the specific area (Macdonald et al., 2000)(503). The most widely used SQGs for marine sediment samples, have been developed by the U.S National Oceanic and Atmospheric Administration (NOAA) and they include sets of effect-range guidelines derived from a large series of chemical and biological data collected from North American coastal regions that incorporate field and laboratory data from many different methodologies, chemical and biological species (McCready et al., 2006)(201). The data set was compared with the sediment quality guidelines suggested by Long et al. (1995)(199) on the basis of the potential to induce toxic effects in marine organisms. The guidelines define two values ERL (effects range low) and ERM (effects range median). ERL values indicate concentrations below which adverse effects rarely occur, and ERM values represent concentrations above which effects frequently occur. Chemical concentrations corresponding to the 10th and 50th percentiles of adverse biological effects were called the Effects-rang-low (ERL) and Effects-range-median (ERM) respectively. The NOAA guidelines provide two values for each chemical, classifying the sediment either rarely (<ERL), occasionally (≥ERL and <ERM) or frequently associated with adverse biological effects (Macdonald et al., 2000)(503). Comparing results of the present study with ERL and ERM values (Figure 28 and 29), it was observed that Cd, Cu, and Zn at all stations are below the ERL value (1.2, 34, and 150 µgg-1), respectively which indicate that these metals in sediments at all stations of the study area are not likely to have adverse effects on animals that live in sediment. Only one station (El-Mex) which had a Pb concentration > ERL, indicated that Pb at El-Mex will likely to has effects on animals that live in this sediment. On the other hand, all the rest of the studied station had a concentration of Pb below the ERL value which indicates that Pb in the study area is not likely to have adverse effects on animals that live in sediments except station 5 in El-Mex. On the other hand, Ni at stations 12, 14, 15, 18, 19, and 20 in (Rashid west, Burullus, New Damietta, El-Gamil east, Port Said and Rafah) had a value over the ERL value (36.384, 43.545, 44.305, 48.93, 47.415, and 27.79), respectively. This reflects that the adverse effects on animals live at these stations are frequently occured. Stations 13, 16, and 17 in (Rashid east, Ras El-Barr and El-Gamil west), respectively had concentration of Ni above the ERM value (56.536, 56.413, and 60.246) which means that Ni probably has adverse effects on animals live in this sediment. Concentrations of (Zn, Cu, Ni, Pb and Cd) were evaluated in a screening level ecological risk assessment, by comparing to numerical SQGs such as TEL and PEL. It is interpreted that TEL as the concentrations, bellow which adverse biological effects rarely occur. Hence, it is considered to provide a high level of protection for aquatic organisms. Similarly, PEL interpreted as the concentrations above which adverse biological effects frequently occur. Hence, it is considered to provide a lower level of protection for aquatic organisms. When compared to the TEL-PEL SQGs, the concentrations of Cd and Zn are lower than the TEL value at 100% of the sampling stations, while Pb and Cu showed values -162- lower than the TEL at 95% of the sampling stations. On the other hand, in case of Ni, 20% of samples fall in the range between TEL and PEL at Abu Qir, Electric power station, Rashid west and Rafah indicated that associated adverse biological effects may occasionally occur. About 35% of samples are higher than PEL values at Rashid east, Ras El-Barr, New Damietta, Burrllus, El-Gamil east and west and Port Said. To assess metal concentration in sediments, Numerical Sediment Quality Guidelines (SQG) were applied. SQG include a threshold effect concentration (TEC) and a probable effect concentration (PEC). The values of consensus-based TECs and consensus-based PECs (MacDonald et al., 2000)(503) are shown in Table 16. If the metals in sediments are below the TEC, harmful effects are unlikely to be observed. If the metals are above the PEC, harmful effects are likely to be observed. Most of the TECs provide an accurate basis for predicting the absence of sediment toxicity (MacDonald et al., 2000)(503). The concentrations of Cd and Cu at all sediment samples are lower than the proposed TECs indicated that there are no harmful effects from these metals. On the other hand, the concentrations of Ni exceed TECs at stations (12, 13, 14, 15, 19 and 20) in Rashid west, Rashid east, Burullus, New Damietta, Port Said and Rafah respectively, while stations (16 and 17) in Ras El-Barr and El-Gamil west are above the PECs. At stations (9, 12, 15, 16 and 20) in Abu Qir Bay, Rashid west, New damietta, Ras El-barr and Rafah, respectively the concentrations of Cr are above the TECs and at stations (13, 14, 17, 18, 19) in Rashid east, Burullus, El-Gamil west, El-Gamil east and Port Said, respectively the concentration of Cr exceeded the PECs. Station 5 in El-Mex Bay showed concentration of Pb exceeded the PECs. This indicated that these stations were in potential risk. In order to obtain a more realistic measure of predicted toxicity that simply summing the numbers of ERMs/PELs exceeded, mean ERM or PEL quotients (ERMQ PELQ) were calculated as follows: ERMQ or PELQ = [Ci/(ERMi or PELi)] / n Where Ci is the concentration of element i in sediments, ERMi, PELi the guidelines values for the element i and n is the number of metals. Mean quotients are considered as useful tools for reducing a large amount of contaminants into a single number. By calculating mean quotients it is assumed that adverse effects to marine organisms caused by individual chemicals are additional limitation is that this approach does not consider all the chemicals present in sediments but only those include in the SQG list (Anders et al., 2005)(508). Mean quotients can be used to identify, delineate and prioritize areas of potential concern with respect to quality of sediments (Chapman and Mann, 1999)(509). ERMQ values of <0.1, 0.11-0.5, 0.51.5 and >1.5 related to 12%, 30%, 46% and 74% likehood, respectively, that sediments present toxicity in amphipod survival bioassays. Similarly, PELQ values of <0.1, 0.11-1.5, 1.51-2.3 and >2.3 coincide with 10%, 25.5, 50% and 76% likehood of toxicity, respectively (Long et al., 1995)(199). Consequently, four relative levels of priority (highly toxic, medium toxic, slightly toxic and non toxic) have been proposed. The mean ERM and PEL quotients calculated for the sampling sites (based on metals Cd, Cr, Cu, Ni, Pb and Zn) are shown in Figure 30 and 31 and Table 17, only two stations (station 7; NIOF and station 9; Abu Qir Bay) in the western region have ERLQ (0.11-1.5) and are categorized as slightly toxic and the rest of the stations in this region are categorized as not toxic. While, all stations of the middle and the eastern region are categorized as slightly toxic. Stations (2, 3 and 6) in Baghous, ElNobarreya and Western harbour, respectively in the western region have PELQ< 0.1 and are categorized as not toxic while the other stations have PELq (0.11-1.5) and categorized as slightly toxic. -163- Table 16: Comparison of the surfacial sediments from the Egyptian Mediterranean coast with Sediment quality guidelines U S NOAA's NYSDEC US DOE USEPA guidlines Metal TEL PEL ERL ERM LAL HAL LEL SEL TEC PEC Present work Not Moderately Heavily polluted polluted polluted 0.68 4.21 1.2 9.6 0.04 9.6 1.2 9.6 0.99 4.98 NA NA >6 0.04-0.47 Cd NA NA NA NA 0.5 120 NA NA NA NA NA NA NA 0.43-26.39 Co 52.3 160 81 370 4 370 26 110 43.4 111 <25 25-75 >75 4.08-297.95 Cr 18.7 108 34 270 2 270 16 110 31.6 149 <25 25-50 >50 0.46-26.26 Cu NA NA NA NA NA NA NA NA NA NA <17000 17000-25000 >25000 243.48-38045.05 Fe NA NA NA NA NA NA NA NA NA NA <300 300-500 >500 17.25-1085.72 Mn 15.9 42.8 21 52 3 50 NA NA NA NA <20 20-50 >50 1.65-60.25 Ni 30.2 112 47 220 2 218 16 50 35.8 128 <40 40-60 >60 3.34-53.67 Pb 124 271 150 410 5 410 120 270 121 459 <90 90-200 >200 2.05-62.21 Zn (505) Lowest effect level (LEL) Severe effect level (SEL)(505) Effects rang low (ERL)(199) Effects range median (ERM)(199) Threshold effect concentration (TEC)(510) Probable effect concentration (PEC)(510) Low alert level (LAL)(511) High Alert Level (HAL)(512) Threshold effect level (TEL)(510) Probable effect level (PEL)(510) -164- 40000 35000 Fe (µgg-1) 30000 Heavily polluted 25000 20000 Moderately polluted 15000 10000 Not polluted 5000 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 1200 Mn (µgg1-) 1000 800 Highly polluted 600 Moderately polluted 400 200 Not polluted 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 350 Cr (µgg1-) 300 250 200 150 Highly polluted 100 50 Moderately polluted Not polluted 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 Stations Figure 26: Concentration of Fe, Mn and Cr, in sediments along the Egyptian Mediterranean coastal area comparable to US SQG. -165- 70 60 Highly polluted Ni (µgg1-) 50 40 Moderately polluted 30 20 Not polluted 10 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 60 Heavily polluted Pb (µgg1-) 50 40 Moderately polluted 30 20 Not polluted 10 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 Heavily polluted 60 Cu (µgg-1) 50 40 Moderately polluted 30 20 Not polluted 10 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 Stations Figure 27: Concentration of Ni, Pb and Cu, in sediments along the Egyptian Mediterranean coastal area comparable to US SQG. -166- Cr (µgg1-) 400 350 300 250 200 150 100 50 0 > ERM ERM ERL 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 70 60 > ERM Ni (µgg1-) 50 ERM 40 30 20 ERL 10 0 Zn (µgg1-) 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 450 400 350 300 250 200 150 100 50 0 > ERM ERM ERL 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 Stations Figure 28: Concentration of Cr, Ni and Zn, in sediments along the Egyptian Mediterranean coastal area comparable to US NOAA's. -167- > ERM 250 Pb (µgg1-) 200 ERM 150 100 50 ERL 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 300 > ERM Cu (µgg-1) 250 200 150 ERM 100 50 > ERM 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 Stations Figure 29: Concentration of Pb and Cu in sediments along the Egyptian Mediterranean coastal area comparable to US NOAA's. -168- Highly toxic 1.6 1.4 ERMq 1.2 1 Moderate toxic 0.8 0.6 0.4 Slightly toxic 0.2 Non toxic 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 S tation Figure 30: Estimated mean ERMq of surface sediments along the Egyptian Mediterranean coast Highly toxic 2.5 PELq 2 Moderate toxic 1.5 1 Slightly toxic 0.5 Non toxic 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 S tation Figure 31: Estimated mean PELq of surface sediments along the Egyptian Mediterranean coast -169- Table 17: Estimated mean ERMq and PELq of surface sediments along the Egyptian Mediterranean coastal area Region Western region Middle region Eastern region Station 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 ERMq 0.08 0.01 0.05 0.07 0.10 0.04 0.11 0.05 0.12 0.09 0.07 0.17 0.34 0.21 0.20 0.26 0.32 0.23 0.31 0.13 PELq 0.13 0.02 0.08 0.12 0.18 0.09 0.21 0.11 0.14 0.14 0.11 0.20 0.31 0.26 0.27 0.33 0.33 0.29 0.28 0.15 The National Standard of China (NSC) GB18668-2002 (SEPA, 2002)(513) has defined three grades of marine sediment, in which the content of some heavy metals is regarded as parameters used to classify marine sediments quality (Table 18). According to this criterion, the first class quality is suitable for mariculture, nature reserves, and endangered species reserves, and leisure activities such as swimming; the second class quality can be used for industry and tourism sites; and the third class can only be used for harbors. The contents of Cd, Cu, Pb and Zn at all samples are lower than the upper limit of the first class criteria of NSC GB 18668-2002. In Hong Kong, a stricter criterion has been to distinguished sediment quality (Lau et al., 1993)(514). The contents of Cd at station 6, 7 and 11 in the western harbour, NIOF and Maadia, respectively at the western region to some extent, higher than the value which regarded as the upper limit of the desired quality for fairly clean sediments but, lower than the threshold values which are used to indicate moderately contaminated sediments (Table 18). Also, the content of Cu in station 7 in NIOF at the western region and the content of total Ni at station 20 in Rafah at the eastern region considered to some extent, higher than the value which regarded as the upper limit of the desired quality for fairly clean sediments that is close to background levels. The content of Ni in station 12 in Rashid west (middle region) considered to some extent higher than the value which indicated that the sediment is moderately contaminated but, lower than the threshold values which are used to indicate heavily contaminated sediments, while stations 13, 14, 15, 16, 17, and 18 in Rashied east, Burrullus, New Damietta, Ras El-Burr, El-Gamil west and El-Gamil east (middle region) and station 20 in Rafah (eastern region) considered to higher than value which indicated heavily polluted sediment. The content of Pb at station 5 in El-Mex (western harbour) considered to some extent, higher than the value which regarded as the upper limit of the desired quality for fairly clean sediments that is close to background levels but, lower than the threshold values -170- which are used to indicate moderately contaminated sediments. The contents of Zn in all samples are lower than the values which are regarded as the upper limit of the desired quality for fairly clean sediments. That is close to background levels. Comparing the sediment of the present study with classification system from Hong Kong environmental Protection Department (EPD) Classification system. The value of the Mean Cupper, Zinc, and Lead concentrations showed to be calssified as uncontaminated sediment (Class A). Wherease, Nickel and Cadmium represented (Class B) contaminations. Sediments were considered as seriously contaminated (Class D) when comparing the mean concentration of Chromium with the classification system adopted by the Hong Kong Government (EPD,1992)(515) (Table 19). Table 18: The metal threshold values of some different criteria used to distinguish marine sediment quality (µgg1-) Class I Class II Class III Target Trigger Action Cd 0.5 1.5 5 Cu 35 100 200 0.4 1.0 1.5 0.22 20 55 65 8.46 Ni Pb 60 130 250 Zn 150 350 600 20 35 75 35 65 150 40 75 200 25.93 13.17 22.19 Reference (SEPA, 2002)(513) (SEPA, 2002)(513) (SEPA, 2002)(513) (Lau et al., 1993)(514) (Lau et al., 1993)(514) (Lau et al., 1993)(514) The present study Class I; suitable for mariculture, nature reserves, endangered species reserves and leisure activities like swimming. Class II; quality can be used for indursty and tourism activities Class III; can only be used for harbours Target; fairly clean sediment that is closed to background Trigger; moderately contaminated sediment Action; heavily polluted sediment Table 19: Classification of sediments according to the background and classification system from the Hong Kong environmental Protection Department (EPD, 1992) Class A B C D Degree of contamintion Uncontaminated Slightly contaminated Moderately contaminated Seriously contaminated The present study Cu <10 10-41 55-64 >64 8.46 Zn <70 70-150 150-200 >200 22.19 -171- Cr <25 25-50 50-80 >80 82.74 Ni <15 15-35 35-40 >1.5 25.93 Cd <0.1 0.1-1.0 1.0-1.5 >1.5 0.22 Pb <25 25-65 65-75 >75 13.17 6.2.1.2. Estimation of Pollution impact A number of calculation methods have been put forward for quantifying the degree of metal enrichment in sediments. Various authors (e.g. Muller, 1969; Hakanson, 1980)(516, 517) have proposed pollution impact scales (or ranges) to convert the calculated numerical results into broad descriptive bands of pollution ranging from low to high intensity (Abrahim and packer, 2008)(518). Five methods are discussed in the following sections along with proposed modifications. 6.2.1.2.1. Enrichment factor (EF) Natural weathering and human activities are known as metals sources for coastal environment. However, the relative influence of natural and anthropogenic sources on the geochemistry of marine sediments is not always clear, especially in the areas where the local minerals contain high natural concentrations (Valdes et al., 2005)(519). Therefore, for a better assessment of contamination process in the marine coastal environment, it is important to be able to distinguish between natural and human related metal enrichments in sediments. Thus, for a meaningful comparison of metals from different stations, normalizing procedures for metals concentrations needed to be used. The normalization is often done based on a conservative component in which the levels are unaffected by contaminant inputs (Alomary and Belhadj, 2007)(120). A common approach for estimating the anthropogenic impact on sediments is to calculate a normalized enrichment factor (EF) for metal concentrations above uncontaminated background levels (Salomons and Forstner, 1984; Dickinson et al., 1996)(181, 520). The EF calculation seeks to reduce the metal variability associated with variations in mud/sand ratios, and is a convenient tool for plotting geochemical trends across large geographic areas (Abrahim and Parker, 2008)(518). To evaluate the magnitude of contaminants in the environment, the enrichment factors were computed relative to the abundance of species in source material to that found in the Earth's curst (Atgin et al., 2000)(7) . Deely and Fergusson (1994)(521) proposed Fe as an acceptable normalization element factor since they considered the Fe distribution was not related to other heavy metals. Fe usually has a relatively high natural concentration, and is therefore not expected to be substantially enriched from anthropogenic sources in estuarine sediments (Niencheski et al., 1994)(522). According to Forstner and Wittman (1983)(427), in case of Fe, particularly the redox sensitive iron hydroxide and oxide under oxidation condition constitute significant sink of trace metals in aquatic system. Even a low percentage of Fe(OH)3, in aquatic system, has a controlling influence on trace metal distribution (Rath, 2005)(523). Therefore, Iron is taken as a normalization element in determining enrichment factor (Chakravarty and Patgiri, 2009)(524). EF represents the actual contamination level in the sediment and is a good tool to differentiate the metal source between anthropogenic and naturally occurring (Valdes et al., 2005)(519). According to Zhao et al. (2007)(525), Fe was used for the following reasons: (1) Fe is associated with fine solid surfaces; (2) its geochemistry is similar to that of many trace metals; and (3) its natural sediment concentration tends to be uniform. A reference element is often the one characterized by low occurrence variability, such as the most commonly used elements: Al, Fe, Ti, Si, Sr, K, etc., (Duzgoren-Aydin, 2007)(526). The EF calculation is expressed below as the follwoing: -172- EF = [Cx/Cref]sample /[Cx/Cref]background where, Cx is the concentration of the element of interest, Cref is the concentration of reference element for normalization. In the present study, the background values were adopted from Salomons and Forstner (1984) , there values in µgg-1: 41000 for Fe, 0.17 for Cd, 19 for Co, 72 for Cr, 33 for Cu, 850 for Mn, 68 for Ni, 20 for Pb, 95 for Zn and the geochemical normalization was obtained using Fe as the reference element. (181) EF values less than 5 are not considered significant, because such small enrichments may arise from differences in the composition of local soil material and reference soil used in EF calculations (Sezgin et al., 2003)(527). However, there is no accepted pollution ranking system or categorization of degree of pollution on the enrichment ratio and/or factor methodology. EF values were interpreted as suggested by Chen et al. (2007)(528) who interpreted the value of EF into seven classes. EF<1 indicates no enrichment, EF< 3 is minor enrichment, EF = 3-5 is moderate enrichment, EF = 5-10 is moderately severe enrichment, EF= 10-25 is severe enrichment, EF= 25-50 is very severe enrichment and EF>50 is extremely severe enrichment. The computed metal EFs in the surface sediments of the Egyptian Mediterranean coastal area represented in Table 20 showed that the EF of Cd ranges from 0.22 to 74.03, the EF of Co ranged from 0.61 to 10.50, the EF of Cr ranged from 1.18 to 28.99, the EF of Cu ranged from 0.32 to 6.78, the EF of Mn ranged from 0.86 to 8.04, the EF of Ni ranged from 0.62 to 26.99, the EF of Pb ranged from 0.40 to 114.22, the EF of Zn ranged from 0.29 to 14.77. The calculated EFs were found to fall in the following sequence: Cd>Pb>Cr>Ni>Mn>Zn>Co>Cu. As shown in Figure 32 Cadmium showed EFs ranging from minor enrichment (average: 1.49; Middle region) to sever enrichment (average: 18.34; Eastern region) and very sever enrichment (average: 29.57; western region) indicating significant participation of anthropogenic sources. On the other hand, lead showed EFs ranging from no enrichment (average: 0.63; Middle region), minor enrichment (average: 2.74; eastern region) to sever enrichment (average: 24.05; western region). The EFs values of Cr were (average: 3.81; middle region), (average: 4.13; Middle region) indicationg moderate enrichment, (average: 16.88; eastern region) indicating sever enrichment. Nickel showed EFs ranged from minor enrichment (average: 1.77; middle region) to moderate enrichment (average: 4.06; western region) and (average: 8.25; eastern region). Manganese showed EFs ranged from minor enrichment at the middle region (average: 1.29) and the eastern region (average: 1.88) and moderate enrichment at the western region (average: 3.11). The EFs of Zinc were viewed to be with no enrichment at the middle region (average: 0.39) and the eastern region (average: 0.59) to moderate enrichment at the western region (average: 3.74). The EFs for Co were of minor pollution at all the studied regions in the following order: middle reigon<eastern region<western region with an average 1.47, 2.01 and 2.22 respectively. Cupper showed EFs with no enrichment at the middle region (average: 0.48) and the eastern region (average: 0.89) and minor enrichment at the western region (average: 2.75). Despite the high EF in the sediments of the western region at stations (2, 3, 4, 5, 6, 7 and 8) in Baghoush, Nobarreya, El-Dikhaila, El-Mex, Western harbour, NIOF and Eastern harbour, respectively and station 20 in Rafah at the eastern region. There seems to be an overestimation of pollution of metals in these sediments. This may results from the low concentration of Fe in these sediments (243.48, 277.34, 3946.02, 3565.22, 1527.85, 4813.8, 3440.82 and 1422.39), respectively which may lead to higher EF of trace metals at these stations. These results are in agreement with the results of Karabassi et al. (2008)(529) who -173- found that applying EFs for metals pollution detection may leads to incorrect results due to naturally lower concentration of Al and Fe or higher concentration of trace metals in sediments. Table 20: Enrichment factor (EF) in the Mediterranean coastal area Region Station Pb Zn Ni 4.93 2.33 0.83 1 39.08 3.63 5.33 2 114.22 14.77 26.99 3 8.72 2.51 1.75 4 32.64 5.99 1.26 5 Western 28.70 1.78 1.90 6 region 13.41 5.58 1.43 7 15.34 2.51 0.62 8 1.78 0.60 1.33 9 3.93 0.66 2.13 10 1.86 0.79 1.12 11 Average 24.05 3.74 4.06 1.03 0.47 2.97 12 0.51 0.40 1.65 13 0.50 0.29 1.36 14 Middle 0.50 0.30 0.92 15 region 0.40 0.34 1.19 16 0.76 0.43 2.60 17 0.74 0.50 1.67 18 Average 0.63 0.39 1.77 0.42 0.38 1.10 19 Eastern 5.06 0.79 15.40 20 region Average 2.74 0.59 8.25 All region Average 13.73 2.25 3.68 surface sediments of the Egyptian Cd 9.66 73.30 55.65 21.15 10.89 74.03 22.09 26.85 3.99 14.24 13.43 29.57 3.55 0.82 2.22 0.22 0.32 1.97 1.32 1.49 0.31 30.69 15.50 18.34 Cu 2.40 2.33 3.85 3.05 2.56 3.36 6.78 3.95 0.62 0.56 0.77 2.75 0.44 0.32 0.49 0.39 0.57 0.50 0.65 0.48 0.42 1.37 0.89 1.77 Mn 0.86 5.71 3.31 2.37 1.56 8.04 1.98 2.11 2.44 3.32 2.45 3.11 1.42 1.61 1.14 1.15 1.03 1.48 1.18 1.29 1.70 2.05 1.88 2.35 Cr 2.51 9.55 10.79 2.36 3.70 2.64 3.01 1.56 4.24 2.91 2.17 4.13 4.96 6.27 2.65 1.18 1.56 7.28 2.77 3.81 4.77 28.99 16.88 5.29 Co 0.61 3.82 10.50 0.94 0.81 1.95 0.84 0.84 0.87 1.40 1.78 2.22 1.77 1.19 1.06 1.41 1.52 1.48 1.85 1.47 1.08 2.93 2.01 1.93 35.00 30.00 25.00 EF 20.00 15.00 10.00 5.00 0.00 Pb Zn Ni western region Cd Cu Middle region Mn Cr Co Eastern region Figure 32: Mean Enrichment factor for surface sediments along the Egyptian Mediterranean coastal area -174- 6.2.1.2.2. Geoaccumulation Index (Igeo) Another commonly tool used to evaluate the trace metal pollution in sediments of the present study is the geoaccumulation index (Igeo). The geoaccumulation index (Igeo) originally introduced by Müller (1969)(516), determine and define metal contamination in sediments. The geoaccumulation index (Igeo) is defined by the following equation: Igeo = log2 (Cn/1.5*Bn) where Cn is the measured concentration of the examined metal (n) in the sediment and Bn is the geochemical background concentration of the metal (n). The factor 1.5 is the background matrix correction factor due to lithological variability. The background values of the metals here are the same as those recorded in the enrichment factor calculation. Similar to metal enrichment factor, geoaccumulation index can be used as a reference to estimate the extent of metal pollution (Zhang et al., 2009)(530). Müller has distinguished seven classes of the geoaccumulation index from Class 0 (Igeo=0) to Class 6 (Igeo>5). The Igeo is associated with a qualitative scale of pollution intensity, samples may be classified as unpolluted (Igeo≤0), unpolluted to moderately polluted (0≤Igeo≤1), moderately polluted (1≤Igeo≤2), moderate to strongly polluted (2≤Igeo≤3), strongly polluted (3≤Igeo≤4), strongly to extremely polluted (4≤Igeo≤5), and extremely polluted (Igeo≥5). The highest class (Class6) reflects at least 100fold enrichment above the background values (Table 21). Table 21: Geoaccumulation Index Igeo Igeo Value ≤0 0-1 1-2 2-3 3-4 4-5 >5 Igeo class 0 1 2 3 4 5 6 Pollution level Unpolluted Unpolluted to moderately polluted Moderately polluted Moderately polluted to highly polluted Highly polluted Highly polluted to very highly polluted Very highly polluted This classification is a methodological approach based on the geochemical data that makes possible to map the study area and discriminate various sub-areas according to their pollution degree. In addition it is possible to obtain a proper comparison between various marine areas in terms of their heavy metal quality (Christophoridis et al., 2009)(531). The calculated Igeo values are presented in Table 22 and the variations are shown graphically in Figure 33. It is evident from the figure that the Igeo values for Zn, Mn, Ni, Fe, Cu and Co fall in class "0" (unpolluted) at all the sampling locations indicating that there is no pollution from these metals. The Igeo value for Pb fall in class "0" (unpolluted) at almost all the sampling location except station 5 at El-Mex Bay and station 7 at NIOF which fall in class "1" (unpolluted to moderately polluted). The Igeo value for Cd fall in class "0" (unpolluted) at almost all locations except El-Salloum, El-Dikhaila, Western harbour, NIOF, Eastern harbour, Electrical power stations and Maadia falls in class "1" (unpolluted to moderately polluted). The Igeo value for Cr fall in class "0" (unpolluted) at all stations of the western region, while stations 13 and 17 in (Rashid east, El-Gamil east) at the middle region and station 19 in Port Said at the eastern region were classified as "moderately polluted" . -175- Table 22: Igeo values of trace metals in the surface marine sediments along the Egyptian Mediterranean coastal area Region Western region Middle region Eastern region All region Stations 1 2 3 4 5 6 7 8 9 10 11 Average 12 13 14 15 16 17 18 Average 19 20 Average Average Pb -0.88 -2.77 -1.03 -0.91 0.85 -0.56 0.00 -0.29 -1.67 -1.31 -2.12 -0.97 -2.70 -2.23 -2.37 -1.76 -2.11 -2.22 -1.93 -2.19 -2.17 -3.17 -2.67 -1.57 Zn -1.88 -6.12 -3.91 -2.64 -1.53 -4.50 -1.20 -2.83 -3.16 -3.83 -3.28 -3.17 -3.76 -2.52 -3.07 -2.44 -2.26 -2.95 -2.43 -2.78 -2.25 -5.77 -4.01 -3.12 Ni -3.75 -5.95 -3.43 -3.55 -4.16 -4.79 -3.55 -5.23 -2.40 -2.51 -3.16 -3.86 -1.49 -0.85 -1.23 -1.20 -0.85 -0.76 -1.06 -1.06 -1.11 -1.88 -1.49 -2.65 Cd 0.17 -1.78 -1.99 0.44 -0.66 0.88 0.79 0.59 -0.42 0.62 0.81 -0.05 -0.84 -1.47 -0.14 -2.87 -2.35 -0.78 -1.02 -1.35 -2.57 -0.49 -1.53 -0.65 -176- Cu -1.84 -6.76 -5.85 -2.35 -2.75 -3.58 -0.91 -2.18 -3.12 -4.05 -3.32 -3.34 -3.85 -2.81 -2.32 -2.04 -1.52 -2.76 -2.04 -2.48 -2.12 -4.98 -3.55 -3.06 Mn -3.45 -5.61 -6.21 -2.86 -3.61 -2.47 -2.83 -3.23 -1.28 -1.63 -1.79 -3.18 -2.31 -0.64 -1.24 -0.63 -0.82 -1.33 -1.32 -1.18 -0.23 -4.54 -2.39 -2.40 Fe -3.10 -7.98 -7.79 -3.96 -4.11 -5.33 -3.68 -4.16 -2.42 -3.22 -2.94 -4.43 -2.67 -1.19 -1.29 -0.69 -0.72 -1.75 -1.42 -1.39 -0.86 -5.43 -3.15 -3.24 Co -3.81 -6.05 -4.40 -4.04 -4.41 -4.37 -3.93 -4.41 -2.62 -2.73 -2.10 -3.90 -1.84 -0.94 -1.21 -0.19 -0.11 -1.19 -0.53 -0.86 -0.74 -3.88 -2.31 -2.68 Cr -1.77 -4.73 -4.36 -2.72 -2.22 -3.93 -2.09 -3.51 -0.34 -1.67 -1.82 -2.65 -0.36 1.46 0.11 -0.45 -0.08 1.11 0.05 0.26 1.40 -0.58 0.41 -1.32 Figure 33: Igeo values distribution of trace metals in the surface marine sediments along the Egyptian Mediterranean coastal area -177- 6.2.1.2.3. Contamination factor (Cf) and Degree of contamination (Cd) Hakanson (1980)(517) proposed an overall indicator of contamination based on integrating data for a series of seven specific heavy metals and the organic pollutant PCB. This method is based on the calculation for each pollutant of a contamination factor (Cf). Surfacial sediment samples are compared to a baseline pristine reference level, according to the following equation: Cf = Mx/Mb Where, Mx and Mb respectively, refer to the concentration of a pollutant in the contaminated sediments and the pre-industrial "baseline" sediments. According to Hakanson (1980)(517) classification the contamination factor was classified into four groups: Cf< 1 low contamination factor; 1 ≤ Cf < 3 moderate contamination factors; 3≤ Cf <6 considerable contamination factors; Cf ≥ 6 very high contamination factor. Data at Table 24 showed that the contamination factors values are low for Zn, Cu and Fe at all sampling sites. They are between low and moderate for Ni, Cd, Mn and Co and between low and considerable contamination for Cr. The study by Hakanson (1980)(517) analysed seven specific heavy metals (As. Cd, Cu, Cr, Hg, Pb, Zn) and the organic pollutants PCB and thus considers eight possible measures of contamination. Hakanson's study also propsed that the numeric sum of the eight specific contamination factors expressed the overall degree (Hakanson, 1980)(517) of sediment contamination (Cd) using the following formula: 8 Cd = Cif i=1 The calculated Cd is therefore defined as the sum of the Cf for the eight pollutant species specified by Hakanson (1980)(517). The Hakanson (1980)(517) classification terminology and calculation formula is based on and is restricted to the seven metals plus PCB specified in Hakanson's study. Furthermore all eight species must be analysed in order to calculate the correct Cd for the range of classes defined by Hakanson (1980)(517). 6.2.1.2.4. Modified degree of contamination (mCd) As a result of the above limitations Abrahim (2005)(532) presented a modified and generalized form of the Hakanson (1980)(517) equation for the calculation of the overall degree of contamination at a given sampling site as follows: i n mCd c i 1 i f n where, n = number of analyzed elements and i = the element (or pollutant) and Cf = contamination factor. Using this generalized formula to calculate the mCd allows the incorporation of as many metals as the study may analyze with no upper limit. For the classification and description of the modified degree of contamination (mCd) in estuarine sediments the follwong gradation are proposed: -178- Table 23: The classification and description of the modified degree of contamination (mCd) mCd < 1.5 1.5 < mCd < 2 2 < mCd < 4 4 < mCd < 8 8 < mCd < 16 16 < mCd < 32 mCd ≥ 32 Nil to very low degree of contamination Low degree of contamination Moderate degree of contamination High degree of contamination Very high degree of contamination Extremely high degree of contamination Ultra high degree of contamination In the Egyptian Mediterranean coastal sediments the revised Hakanson equation was used to calculate the modified degree of contamination (mCd) for the nine analyzed elemetns (Cd, Cu, Cr, Co, Fe, Mn, Pb, Zn and Ni). The results for each sampling site are presented in Table 24 and illustrated in Figure 34. The calculated Cfs were found to fall in the following sequence: Cd>Cr>Pb>Co>Ni>Mn>Fe>Cu>Zn. The Egyptian Mediterranean mCd are less than 1.5 indicating zero to very low degree of contamination. mCd values are calculated based only on the separate contamination factors, which don't consider the normalizing factor of Fe, therefore it gives values not reproducible to every environment with the same degree of contamination and not easily compared to other areas studied in the past with different geological backgrounds (Christophoridis et al., 2009)(531). 6.2.1.2.5. Pollution Load Index The extent of pollution by trace metals has been assessed by employing the method based on Pollution load index (PLI) developed by Tomlinson et al. (1980)(533) as the following equation: Where CF = contamination factor and n= number of metals PLI provides a simple, comparative means for assessing a site or estuarine quality: a value of zero indicates perfection, a value of one indicates only baseline levels of pollutants present and values above one would indicate progressive deterioration of the site and estuarine quality (Tomlinson et al., 1980)(533). PLI calculated for total metals in surface sediments of the Egyptian Mediterranean Sea from El-Salloum to Rafah are presented in Table 24. PLI values of the analyzed samples ranged from 0.04 at station 2 (Baghoush; western region) and 0.72 at station 19 (Port Said; eastern region) with an average 0.41. Figure 35, shows the variation of PLI at different stations. In general, there is an increase of PLI toward the eastern region. However, results of PLI were less than 1 at all the studied locations indicating only baseline levels of pollutants present. The PLI can provide some understanding to the public of the area about the quality of a component of their environment, and indicates the trend spatially and temporarily. In addition, it also provides valuable information to the decision makers on the pollution level of the area (Harikumar et al., 2010)(534). -179- Table 24: Modified degree of contamination (mCd) and contamination factors (Cf) for the surfacial sediments along the Egyptian Mediterranean coastal area Region Station Cf Pb Cf Zn Cf Ni Cf Cd Cf Cu Cf Mn Cf Fe Cf Co Cf Cr Sum Cif mCd 0.86 0.41 0.15 1.69 0.42 0.15 0.17 0.14 0.44 4.43 0.49 1 0.23 0.02 0.03 0.44 0.01 0.03 0.01 0.03 0.06 0.86 0.10 2 0.77 0.10 0.18 0.38 0.03 0.02 0.01 0.10 0.07 1.66 0.18 3 0.84 0.24 0.17 2.04 0.29 0.23 0.10 0.12 0.23 4.25 0.47 4 2.84 0.58 0.11 0.95 0.22 0.14 0.09 0.10 0.32 5.34 0.59 5 Western region 1.07 0.07 0.07 2.76 0.13 0.30 0.04 0.10 0.10 4.62 0.51 6 1.57 0.65 0.17 2.59 0.80 0.23 0.12 0.13 0.35 6.62 0.74 7 1.29 0.21 0.05 2.25 0.33 0.18 0.08 0.10 0.13 4.62 0.51 8 0.50 0.17 0.37 1.12 0.17 0.68 0.28 0.33 1.19 4.81 0.53 9 0.63 0.11 0.34 2.30 0.09 0.54 0.16 0.31 0.47 4.95 0.55 10 0.36 0.15 0.22 2.63 0.15 0.48 0.20 0.47 0.42 5.09 0.57 11 0.24 0.11 0.70 0.84 0.10 0.33 0.24 0.57 1.17 4.30 0.48 12 0.34 0.26 1.09 0.54 0.21 1.06 0.66 1.06 4.14 9.36 1.04 13 Middle region 0.31 0.18 0.84 1.36 0.30 0.70 0.61 0.88 1.62 6.80 0.76 14 0.46 0.28 0.85 0.21 0.36 1.07 0.93 1.78 1.10 7.04 0.78 15 0.37 0.31 1.08 0.29 0.52 0.94 0.91 1.88 1.42 7.73 0.86 16 0.34 0.19 1.16 0.88 0.22 0.66 0.45 0.90 3.25 8.04 0.89 17 0.41 0.28 0.94 0.74 0.36 0.67 0.56 1.41 1.55 6.93 0.77 18 0.35 0.32 0.91 0.25 0.35 1.41 0.83 1.22 3.95 9.58 1.06 Eastern region 19 0.18 0.03 0.53 1.06 0.05 0.07 0.03 0.14 1.01 3.10 0.34 20 All region Average 0.70 0.23 0.50 1.27 0.26 0.49 0.32 0.59 1.15 5.51 0.61 -180- PLI 0.34 0.04 0.08 0.29 0.29 0.18 0.43 0.23 0.43 0.34 0.36 0.35 0.69 0.61 0.63 0.71 0.62 0.66 0.72 0.15 0.41 2 mCd 1.5 1 0.5 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 Stations Figure 34: modified degree of contamination (mCd) for sediments along the Egyptian Mediterranean coast Pollution Load Index 1.50 1.00 0.50 0.00 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 Stations Figure 35: Pollution load index distribution at different stations along the Egyptian Mediterranean coastal sediments. -181- 6.2.2. Leachable metals Sediments are the important component of ecosystem in which toxic compounds accumulate through complex physical and chemical adsorption mechanisms depending on the properties of the adsorbed compounds and the nature of the sediment matrix (Leivouri, 1998)(134). In order to avoid the pollution of trace metals in marine environment, it is necessary to establish the data and understand the mechanisms influencing the distribution of trace metals in marine environment (Raj and Jayaprakash, 2008)(535). The mobiltiy and bioavailabiltiy of heavy metals in the environment are predominanted by their existing fractions. There are two methods to extract the active fraction of heavy metals in sediments. One is to adopt the total content of the nonresidual fractions using multiple sequential extraction procedure. The other is to choose a certain selective reagent to extract the active fraction directly, named single step extraction procedure. The selective reagents generally include dilute acids, chelating agents, neutral salts, buffer reagents, and so on. The extraction procedure using dilute hydrochloric acid is one of the most widely used methods in single reagent extraction, and it is considered to be a rapid, effective means to assess the mobility of heavy metals in sediment and to evaluate whether the sediment has been polluted by anthropogenic activities (Jayaprakash et al., 2008)(467). After a series of environmental evolution, the acid leachable heavy metals in sediment are easy to release into water column and bring "secondary pollution" (Ayyamperumal et al., 2006)(536). The leaching of metals provides an accurate measure of the bioavailable metals in any aquatic environment which are often readily available to organisms affecting them directly. Hence assessment of trace metal enrichment in sediments on the acid leachable (non-residual) elements is of prime interest, as it often yields more data on the extent of trace metal enrichment than the total sediments, which include the residual or non-residual fraction, and so may mark the relationships sought (Sarkar and Bhattacharya, 2010)(482). The leachable metal fraction is defined as the anthropogenic fraction of metals involved with the sediment particles. The assessment of trace metals on the acid leachable elements is of great interest as the results are more informative than total sediments, which include the residual or non residual or non polluted fraction (Janki-Raman et al., 2007)(537). The acid leachable fraction extracts almost the whole degree of elements as it is absorbed by sediments depicting the contamination of an area (Janaki-Raman et al., 2007)(537). It is now widely accepted that the use of total element concentrations in environmental impact assessments does not represent an optimal approach (Sahuquilloet et al., 2003)(538). The leachable metals fraction defined as that including exchangeable, carbonate bound, iron and manganese oxide bound and organically bound fractions (Nriagu, 1990)(539). Analysis of the leachable (labile) metal fraction of the sediment may be more useful, in terms of discovering its biological significance and the new inputs, than analysis of the total metal fraction (Lacerda et al., 1992)(540). However, sediment analysis is more indicative than water analysis for evaluating the degree of contamination in the aquatic medium. Concentrations of toxic elements are usually higher in sediments with less possibility of contamination of samples during handling and processing, and the analytical methods are simpler (El-Nemr et al., 2006)(437). The importance of leaching studies has gained significant attention in recent decade due to the assessment of metals present in different fractions in the sediment. The leaching of metals provides an accurate data base of the bioavailable metals in any aquatic environment which are often readily available to organisms affecting them directly. This bioavailable -182- fraction is thus defined as the amount of metal that can be exchanged with biological organisms and be incorporated into their structure (Vangronveld and Cunnihgham, 1998)(541). The identification of the main binding sites of trace metals helps in the understanding of geochemical processes and allows the prediction of potential remobilisation, along with the determination of bioavailability and possibly the discrimination of sources (Hall et al., 1996)(542). Leachability of metals from soils and sediments depends on several factors, sediment characteristics, including pH, CaCO3 content, organic matter content (Sahuquilloet al., 2003)(538). The ratio of the trace metal concentrations in the labile fraction to the total concentration of metals in the sediment is expressed as a percentage, known as the percentage of extractability. The labile fraction is usually defined as exchangeable, carbonate bound, iron and manganese oxide bound and organically bound fractions. The ratio between labile and total trace metals may be referring to the anthropogenic input or the new input percentage (Masoud et al., 2007)(294). For investigating the bioavailability of metals, a one step extraction procedure was applied. 1N HCl attack was selected because the extraction procedure is simple and its replication is reliable. Many terms have been given to the leachable fraction (acid soluble, labile, non-residual and non detrital). They are the unstable fraction of metals that with a slight change in the environmental conditions (pH, Eh), may be released to the upper water column thus named non-residual or labile. It is important to asses the availabily of heavy metals in sediments because of their persistence, subsequent bioaccumulation and toxification to biota (Tanner and Leong, 1999)(422). This one-step extraction process yields metals bound as hydroxides, carbonates, sulfides, oxides and weakly bound to organic matter. The concentrations of the selected nine trace metals of labile fractions in the surfacial sediments of the Egyptian Mediterranean coastline are shown in Table 6. The surface layer was chosen for this study, where this layer controls the exchange of metals between sediments and water as well as constitutes a reserve of metals to which benthic organisms are exposed (El-Nemr et al., 2006)(437). Visual inspection of Figures 36, 37 and 38 represented the variations of trace metal content in labile fractions of the studied sediments. From the obtained data, it is observed that the concentration of trace metals in labile fraction decreasing in the order Fe>Mn>Pb>Zn>Ni>Cr>Co>Cu>Cd. The percentage of extractability which is the ratio of leachable to total heavy metal concentrations were expressed in Table 25. This has been used as a theoretical estimation of the relative importance of metals of anthropogenic origin (Carrel et al., 1994)(543) and refers to the new input percentage (NIP) of heavy metals. The NIP showed the following decreasing order: Mn>Pb>Cd>Zn>Cu>C>Fe>Cr>Ni. Leachable Iron (LFe) Iron is one of the most abundant metals in sediments because it is the common element in the earth's crust (Wei et al., 2007)(13). In the western region of the present study, the total Iron concentrations ranged from 243.48 to 11478.38µgg-1 and from 106.63 to 2100.42µgg-1 for labile fraction. While in the middle region, the total Iron concentration ranged from 9653.67 to 38045.05µgg-1 and from 1494.21 to 6831.61µgg-1 for labile fraction. Finally in the eastern region, the total Iron concentration ranged from 1422.39 to 33971.50µgg-1 and from 94.98 to 3667.31µgg-1 for labile fraction (Figure 36). % of LFe for Fe fluctuated between 6.68% at station 20 in Rafah to 69.46% in station 2 in Baghoush. The maximum % of LFe (69.46%) was found at station 2 (Baghoush) in the western region and the minimum percentage (6.68%) of LFe was found at station 20 (Rafah) in the -183- eastern region. It was also noted that Fe has a relatively low percentage of LFe in almost all stations except some stations 2, 3, 4, 6, 7, and 8 in Baghoush, Nobareya, Dekhaila, El-Mex, NIOF and the Eastern harbour, respectively in the western region which exceed (30%). Results showed that there was a significant increase in the residual Fe from station 9 in Abu Qir at the western region to station 20 in Rafah at the eastern region. The low percentage of LFe in most cases (average: 22.83%) was agreeable with the findings of (Dassenakis et al., 2003)(180) who found that the low percentage (<20%) of weakly bound iron may be due to the increased contribution of the lattice-held fraction of the metal. Leachable Manganese (LMn) Manganese is the 11th element in terms of abundance in the earth crust (Anschutz et al., 2005)(113). Mn in Earth's crust is 1600 µgg-1; in soils it is 61-1060 µgg-1. The common aqueous species found in water is predominantly M2+ and M4+. Mangansese is essential for plants and animal (WHO, 2004)(73). Natural levels of manganese in soil ranged from 40 to 900 µgg-1, with an estimated mean of 330 µgg-1 (Rope et al., 1988)(116). Accumulation of manganese in soil usually occurs in the subsoil and not on the soil surface (WHO, 1981)(117). From the obtained data at Figure 36 it was observed that, the concentration of manganese ranged between 17.25 and 526.53 for total and from 10.83 to 261.85µgg-1 for labile fractions at the western region. In the middle region, the total manganese concentrations ranged between 257.30 and 822.60 µgg-1; and from 29.99 to 307.27µgg-1 for labile fraction. While, in the esatern region, the total manganese concentration ranged between 54.76 and 1085.72µgg-1 and from 30.20 to 171.53µgg-1 for labile fraction. The % of LMn ranged between 19.94 to 91.67% at the western region, 3.66 to 46.21% at the middle region and 15.80 to 55.15% at the eastern region. These results were in agreement with the data reported by Dassenakis et al. (1995)(544), who found that high percentage of weakly bound Mn (>50%) are probably due to the elevated association of Mn with carbonates that are dissolved by the dilute HCl (Dassenakis et al., 1995)(544). Leachable Lead (LPb) Lead forms stable organic compounds. Tetraethyllead and tetramethyllead are used extensively as fuel additives. Both are volatile and poorly soluble in water. Trialkyllead compounds are formed in the environment by the breakdown of tetraalkyllead. These trialkyl compounds are less volatile and more readily soluble in water. Lead is mined, most usually as the sulfide, "galena". Lead is a non essential element for living organisms and is an accumulative poison (Schulz and Zabel, 2000)(79). The average abundance in Earth's crust is 13 µgg-1; in natural soils background level ranges from 2.6-25 µgg-1; the common aqueous species are hydroxides and carbonates of Pb2+ (Sharma and Pervez, 2003)(93). Lead is reported to be in the range 15 to 50 µgg-1 for coastal and estuarine sediments around the world (Denton et al., 1997)(48) with < 25 µgg-1 in clean coastal sediments. Hence, entry into the aquatic environment occurs through releases (directly or through atmospheric deposition) from the smelting and refining of lead, the burning of petroleum fuels containing lead additives and, to a lesser extent, the smelting of other metals and the burning of coal and oil. Metallic lead deriving from shotgun cartridges or used as fishing weights is lost in the environment and often remains available to organisms (Schulz and Zabel, 2000)(79). Total and labile fractions of the surfacial sediments along the Egyptian Mediterranen coast represented Pb content fluctuated between 4.41 and 53.67 and from 1.78 to 51.35µgg-1 respectively, for the western region. It ranged from 4.61 to 8.83 in total fraction and from 0.77 to 3.98µgg-1 in labile fraction for the middle region. Finally in the eastern region, lead concentrations ranged between 3.34 and 6.67 µgg-1 in total fraction, and from 0.54 to 1.56 -184- µgg-1 for labile fraction (Figure 36), which indicate a new input of lead to the western region of the Egyptian Mediterranean coast. Table 25 showed that Lead exhibited a high % of LPb in the western region ranged between 25.72 and 95.68% (average: 60.95%). The high extractability percentage of Pb reported at station 5 (El-Mex Bay) indicated a new input in El-Mex Bay, which was probably due to the domestic, industrial effluents and the atmospheric deposition; many reported studies have also indicated elevated levels of heavy metals in aquatic systems receiving effluents from urban areas, domestic, and untreated sewage (El-Nemr, 2003)(545). Leachable Zinc (LZn) Sediments are known as major sinks for zinc in the aquatic environment, and residues in excess of 3000 µgg-1 have been reported close to mines and smelters (Denton et al., 2001)(66). The highest sedimentary zinc levels are found to be from enclosed harbors reaching as high as 5700 µgg-1. This is mainly due to restricted water circulation and also particularly prone to zinc contamination from a variety of localized sources including brass and galvanized fittings on boats, wharves and piers; zinc-based anti-corrosion and anti-fouling paints (Denton et al., 1997)(48). The average zinc content of the lithosphere is approximately 80 µgg-1 (Callender, 2003)(65) and depending on the local geology, sediments from uncontaminated waters typically contain zinc concentration in the order of 5-50 µgg-1. However, levels normally encountered in carbonate sediments from pristine reef waters, away from coastal developments are usually less than 1 µgg-1 (Denton et al., 2001)(66). Results at Figure 37 showed that, the total concentration of zinc ranged between 2.05 and 62.21 and from 0.11 to 49.48µgg-1 labile fractions at the western region. In the middle region, the total zinc concentrations ranged between 10.49 and 29.82 µgg-1 and from 1.49 to 6.54µgg-1 for labile fraction. While, in the esatern region, the total zinc concentrations ranged between 2.61 and 30.05 µgg-1 and from 0.15 to 3.63µgg-1 for labile fraction. Table 25 showed that the % of LZn ranged between 1.16 and 89.27% (average: 43.35%) at the western region, and from 8.11 to 24.85% (average: 15.46%) at the middle region, and from 5.83 to 12.07% (average: 8.95%) at the eastern region, indication that about 45% of Zn detected in the western region was a new input. Leachable Nickel (LNi) Nickel is a relatively mobile heavy metal. In natural waters, nickel is transported in both particulate and dissolved forms. The pH, oxidation –reduction potential, ionic strength, type, and concentration of organic and inorganic ligands (in particular, humic and fulvic acids), and the presence of solid surfaces for adsorption (in particular, hydrous iron and manganese oxides) can all affect the transport, fate, and biological availability of nickel in fresh water and seawater (Snodgrass, 1980)(100). In some sediments under reducing conditions and in the presence of sulphur, relatively insoluble nickel sulphide is formed (Ankley et al., 1991)(228). Under aerobic conditions and pH less than 9, nickel forms compounds with hydroxide, carbonate and sulphate. Naturally occurring organic ligands are sufficiently soluble to maintain aqueous Ni2+ concentrations above 60 µg/L (Callahan et al., 1979)(546). Most of the nickel in sediments and suspended solids is distributed among organic materials, precipitated and co-precipitated as particle coatings, and crystalline particles (CEPA, 1994)(547). Typically, nickel residues in sediments can be up to 100 µgg-1 or higher but may fall below 1 µgg-1 in some clean coastal waters (Denton et al., 1997)(48) with the average concentration of nickel in the lithosphere of 55 µgg-1 (Callender, 2003)(65). From the obtained data at Figure 37, it was observed that, the concentration of nickel ranged between 1.65 and 19.36 and from 0.27 to 3.29µgg-1 for total and labile fractions espectively, at the western region. In the middle region, total concentrations ranged between 36.38 and.60.25 -185- µgg-1 and from 2.70 to 11.16µgg-1 for labile fraction. While, in the eastern region, total nickel concentration ranged between 27.79 and 47.42 µgg-1 and from 0.15 to 6.72 µgg-1 for labile fraction. The % of LNi ranged between 2.86 and 28.83% (average: 15.61%) at the western region, from 4.49 to 25.20% (average: 12.07%) at the middle region and from 0.55 to 14.17% (average: 7.36%) at the eastern region (Table 25), which indicates that stations along the western region have a relatively low input of Ni. This indicates that this element is tightly bound to the sediment minerals. Leachable Chromium (LCr) Chromium is the 21st most abundant element in Earth's crust with an average concentration of 100µgg-1. Chromium compounds are found in the environment, due to erosion of chromium containing rocks and can be distributed by volcanic eruptions. The concentrations range in soil is between 1 and 3000 µgg-1, in sea water 5 to 800 µg/L, and in rivers and lakes from 26µgL-1 to 5.2mgL-1. Chromium like zinc is one of the most abundant heavy metals in the lithosphere with an average concentration of about 69µgg-1 (Callender, 2003)(65). Levels of chromium in marine sediments range from 2.4 at unpolluted sites to 749 µgg-1 at grossly contaminated sites. Under the US EPA sediment quality classification, sediments with chromium levels of less than 25 µgg-1 are considered as non-polluted whereas sediments with 25-75 µgg-1 and >75 µgg-1 are considered to be moderately polluted and heavily polluted respectively (Denton et al., 1997)(48). Calcareous sediments of biogenic origin, such as those found in coral reefs, are often lower and normally contain 3-5 µgg-1 (Denton et al., 2001)(66). From the obtained data in Table 25, the % of LCr ranged between 1.58 and 61.35% (average: 23.60%) at the western region, and from 0.42 to 3.56 % (average: 1.51%) at the middle region, and from 0.96 to 1.04 (average: 1.00%) at the eastern region, indicating that this element is tightly bound to the sediment minerals. Leachable Cobalt (LCo) The average cobalt abundance in earth's crust is 29µgg-1; in soils it is 1.0-14 µgg-1. (WHO, 2004)(73). Data at Figure 38 showed that cobalt content in total and labile fractions of the surfacial sediments along the Egyptian Mediterranen coast were in the range (0.43 to 6.63 and 0.10 to 2.85 µgg-1, respectively) for the western region, and from 7.94 to 26.39µgg-1 for total fraction and from 1.88 to 8.77 µgg-1 for the labile fraction in the middle region. Finally in the eastern region, the total cobalt concentrations ranged between 1.93 and 17.07 µgg-1 and from 0.34 to 7.87 µgg-1 for labile fraction, which indicate a new input of cobalt to the the Egyptian Mediterranean coast. In Table 25 the % of LCo rangrd between 5.34 and 43.01% (average: 24.96%) in the western region, and from 16.94 to 35.22% (average: 24.92%) in the middle region, and from 17.69 to 45.93% (average: 31.81%) in the eastern region. Results showed that relatively low % of LCo were found at most of the stations of the study area not exceeding 30%. This indicates that this element is tightly bound to the sediment minerals. Leachable Copper (LCu) Copper is a moderately abundant heavy metal with mean concentration in the lithosphere of about 39µgg-1. It is an essential trace element for the growth of most aquatic organisms. However it becomes toxic to aquatic organisms at levels as low as 10 µgg-1 (Callender, 2003)(65). Heavily polluted sediments have been reported to exceed 200 µgg-1 (Denton et al., 1997)(48). Its mean concentration in soil is 18 µgg-1 (Shacklette, 1970)(548) and from 4 to 28 µgg-1 in forage plants (Engel et al., 1964)(549). Uses of copper include electrical wiring and electroplating, the production of alloys, copper piping, photography, antifouling paints and pesticide formulations. Major industrial sources include mining, smelting, refining and coal-burning industries. Certain of these anthropogenic sources may -186- led to significant concentrations entering the aquatic environment (either directly via sewage or industrial discharges or through atmospheric deposition) but copper will also enter the aquatic environment through natural sources, e.g. from the weathering or the solution of copper minerals (CCREM,1987)(103). From the data obtained in Figure 38, the total cupper concentrations in the western region, ranged between 0.46 and 26.26 µgg-1 and from 0.23 to 8.20 µgg-1 for labile fraction. While, in the middle region, the total cupper concentration ranged between 3.44 and 17.27 µgg-1 and from 0.56 to 2.08 µgg-1 for labile fraction. Finally in the eastern region, the total cupper concentrations ranged between 1.57 and 11.39 µgg-1 and from 0.27 to 1.79µgg-1 for labile fraction, which indicate a new input of cupper to the Egyptian Mediterranean coastal area. The % of LCu ranged between 8.92 and 86.46% (average: 41.45%) at the western region, from 10.58 to 17.34% (average: 13.48%) at the middle region, from 15.71 to 17.46% (average: 16.59%) at the eastern region. The maximum % of LCu (86.46%) observed at station 5 in El-Mex Bay. The antifouling paints used for ships and boats are regarded as one of the important sources, which increased the level of copper in El-Mex Bay (Masoud et al., 2007)(294). From the obtained data at Figure 38, it was observed that the relatively high % of LCu (> 30%) was observed at stations 2, 3, 4, 5, 6, 7, 8, 10 (Baghoush, Nobarreya, Dekhaila, El-Mex, Western harbor, NIOF, Eastern harbor and Power station). Cu, although a micronutrient, can cause a toxic response in bacteria at certain concentrations. Dissolved copper may exist as free cupric ions (Cu2+), inorganic complexes, and complexes with various organic ligands (e.g. humic substances, phytoplankton metabolites, proteins, etc.) (Wei et al., 2007)(13). Anthropogenic sources of cupper are primarily related to textile production, marine anti-fouling agents, pipes and copper based fungicides or pesticides (PIO, 2005)(550). Leachable Cadmium (LCd) The average concentration of cadmium in the lithosphere is ~0.1µgg-1 and it is strongly chalcophilic (Callender, 2003)(65). Concentrations in pristine areas are <0.2 µgg-1 with levels exceeding 100 µgg-1 at severely contaminated sites (Naidu and Morrison, 1994)(551). Cadmium is widely distributed in the Earth's crust at an average concentration of about 0.2 µgg-1 and is commonly found in association with zinc. Higher levels are present in sedimentary rocks: marine phosphates often contain about 15µgg-1. Weathering and erosion result in the transport by rivers of large quantities of cadmium to the world's oceans and this represents a major flux of the global cadmium cycle; an annual gross input of 15,000 tonnes has been estimated (Bryan,1971)(552). The results at Table 25 showed that the % of LCd in the western region ranged between 11.63 and 79.44% (average: 31.94%) and from 12.5 to 86.0% (average: 45.39%) for the middle region and from 13.26 to 62.79% (average: 38.03%) for the eastern region, which suggested a new input of Cd to the most of locations. Cd is contained in some phosphate based fertilizers and petroleum. Such sources could constitute a major source of Cd that may reach humans. In additions, sewage sludge from wastewater treatment may contain significant quantities of Cd (El-Nemr et al., 2006)(437). These results are in agreement with El-Nemr et al. (2007a)(61). -187- Table 25: The relative percentage of leachable Metals from total metals in the sediments of the Egyptian Mediterranean coastal area Region Station 1 2 3 4 5 6 Western 7 region 8 9 10 11 Min Max Average 12 13 14 15 Middle 16 Region 17 18 Min Max average 19 Eastern 20 region Min Max Average Min All Max region Average %LZn 13.53 25.59 1.16 49.88 89.27 67.93 28.00 73.50 25.08 52.99 49.89 1.16 89.27 43.35 15.77 8.74 15.34 24.85 21.47 8.11 13.92 8.11 24.85 15.46 12.07 5.83 5.83 12.07 8.95 1.159 89.272 30.145 %LCu %LPb %LCd %LCr %LCo %LNi 14.14 47.33 79.44 8.47 14.96 9.79 49.56 71.43 43.24 61.35 22.30 20.38 37.09 36.80 40.63 24.02 21.34 2.86 46.77 65.18 21.10 19.36 33.23 15.19 86.46 95.68 39.13 35.42 31.38 21.50 31.11 61.51 20.26 25.25 13.08 21.51 31.23 66.76 21.09 29.12 32.59 19.96 56.72 94.47 25.07 42.77 26.78 17.67 8.92 45.26 31.05 1.58 30.56 7.95 76.59 60.30 18.67 4.76 5.34 6.11 17.36 25.72 11.63 7.53 43.01 28.83 8.92 25.72 11.63 1.58 5.34 2.86 86.46 95.68 79.44 61.35 43.01 28.83 41.45 60.95 31.94 23.60 24.96 15.61 16.35 28.90 40.85 0.66 23.72 7.42 14.36 14.67 36.96 0.92 16.94 6.88 10.58 21.99 12.50 0.67 24.87 8.65 17.34 45.03 62.86 3.56 35.22 25.20 11.20 23.92 86.00 2.91 29.92 17.73 11.99 12.01 43.62 0.42 19.02 4.49 12.54 47.95 34.92 1.41 24.71 14.11 10.58 12.01 12.50 0.42 16.94 4.49 17.34 47.95 86.00 3.56 35.22 25.20 13.48 27.78 45.39 1.51 24.92 12.07 15.71 23.45 62.79 0.96 45.93 14.17 17.46 16.28 13.26 1.04 17.69 0.55 15.71 16.28 13.26 0.96 17.69 0.55 17.46 23.45 62.79 1.04 45.93 14.17 16.59 19.87 38.03 1.00 31.81 7.36 8.915 12.01 11.63 0.42 5.34 0.55 86.464 95.68 86.00 61.35 45.93 28.83 29.174 45.23 37.25 13.61 25.63 13.55 -188- %LFe %LMn 14.78 47.38 69.46 74.98 38.45 62.80 39.69 85.02 26.56 91.67 40.97 70.48 32.59 52.81 41.20 84.33 9.08 49.73 9.88 19.94 26.17 55.74 9.08 19.94 69.46 91.67 31.71 63.17 15.48 46.21 7.49 3.66 8.85 20.49 17.96 37.35 14.66 33.26 9.08 25.73 16.83 28.02 7.49 3.66 17.96 46.21 12.91 27.82 10.80 15.80 6.68 55.15 6.68 15.80 10.80 55.15 8.74 35.47 6.68 3.66 69.46 91.67 22.83 48.03 40000 Fe µgg-1 30000 20000 10000 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 1200 Mn µgg-1 1000 800 600 400 200 0 Pb µgg-1 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 60 50 40 30 20 10 0 T Pb LPb 1 2 3 4 5 6 7 8 9 10 11 12 1314 15 16 17 18 19 20 Stations Figure 36: Distribution of total trace metals concentrations (Fe, Mn and Pb) and leachable fractions in sediments along the Egyptian Mediterranean coast -189- Zn µgg-1 70 60 50 40 30 20 10 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 70 60 Ni µgg-1 50 40 30 20 10 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 T Cr 350 L Cr Cr µgg-1 300 250 200 150 100 50 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 Stations Figure 37: Distribution of total trace metals concentrations (Zn, Ni and Cr) and leachable fractions in sediments along the Egyptian Mediterranean coast -190- 30 Coµgg-1 25 20 15 10 5 0 Cu µgg-1 1 2 3 4 5 6 7 8 9 10 11 12 1314 15 16 17 18 19 20 30 25 20 15 10 5 0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 0.5 TCd 0.4 Cd µgg-1 LCd 0.3 0.2 0.1 0 1 2 3 4 5 6 7 8 9 10 11 1213 14 15 1617 18 19 20 Stations Figure 38: Distribution of total trace metals concentrations (Co, Cu and Cd) and leachable fractions in sediments along the Egyptian Mediterranean coast -191- 6.2.3. Fractionation of trace metals Measurements of total metal content are a poor indicator of metal bioavailability, mobility or toxicity, when these properties basically depend on the chemical association of the different components of the sample (Tuzen et al., 2004)(553). Aquatic sediments consist of several different geochemical phases that act as reservoirs of trace metals. These phases include carbonates, sulfides, organic matter, iron and manganese oxides, and clays, all of which may occur in a variety of structural forms (Gao et al., 2010)(250). According to Quevauviller (1998)(554) the determination of specific chemical forms, or the nature of binding, is much more valuable than the determination of the total metal content, since the toxic effects and the geochemical pathways of elements are determined mainly by their mobile species. Fractionation of heavy metal contents may give indications of the source of the metals. According to Tack and Verloo (1995)(555), exchangeable, carbonate, reducible and oxidizable fractions are considered the fractions that are more available to aquatic biota where the bioavailability decreases in the order of exchangeable > carbonate > reducible > oxidizable. Trace metals speciation studies are important because slight changes in metal availability and in environmental conditions can cause these elements to be toxic to animals and plants (Ure et al., 1993)(16). The sequential extraction procedure allowed determination of the distribution of the trace metals between the different geochemical fractions, reflecting the relative proportions of each metal transported by different chemical mechanisms (Passos et al., 2011)(263). In the present work, fractionation of Cr, Fe, Mn, Ni, Pb and Zn into the different chemical forms has been conducted in order to demonstrate in which forms these metals are chemically chelated, as well as to differentiate between the residual metals (natural background) and non-residual ones (man-made sources of pollution). Iron (Fe) Figure 39 and 40 showed that the examined Fe fractions are represented in the following sequence: Residual> Fe-Mn oxides> organic form > carbonate> exchangeable. This sequence corresponding to average percentages of 80.27% for residual, 12.24% for oxides, 7.42 for organic, 0.07% for carbonate and 0.009% for exchangeable Fe. The exchangeable fraction and the carbonate fraction represented only minor portions from the total concentration (less than 1%) which considered very low, limiting its potential toxicity as pollutant. These results are in agreement with the result of Wei et al. (2007)(13) who found that a negligible amount of Fe was found in nonstable phase compared to the total concentration, suggesting relatively low mobility of this element. Residual fraction dominated the different phase of Fe in all the studied sites. The high average pecentage of residual iron fraction (80.27%) reflects the natural background of iron in the investigated area. The residual fraction corresponding to the metal fraction in the mineral crystalline matrix is strongly retained and would not normally be released into solution under natural environmental conditions (Morillo et al., 2007)(163). This indicates that iron is tightly bound to the sediment minerals and it is not easily released to the environment. The high content of both total Fe (13255.685 µgg-1 on average) and residual Fe (10388.84 µgg-1 on average) may emphasize the strong influence of water discharge and sediment influx from the river Nile into the Mediterranean Sea (Nasr et al., 1990)(325). The high percentage of Fe in the residual fraction indicates that most of the iron exists as crystalline iron oxides (goethite, limonite, magnetite, etc). Large amounts of Fe accumulate in the residual fraction, probably because this is an element basically of natural origin (it is one of the most common elements in the earth's crust) (Morillo et al., 2007)(163). These results were also in agreement with the results of Usero et al. (1998)(169). The metal present in the residual fraction can be used as a baseline data for the assessment of the degree of contamination of the system. The association -192- between metals and the residual fraction of uncontaminated soils is so strong that metal association with non-residual fraction has been used as an indicator of anthropogenic enrichment (Sutherland et al., 2000)(556). Table 7 showed that the association of Fe with different fractions in the studied regions was in order: western region, residual (3892.37µgg-1, 72.68%)> Fe-Mn oxides (525.47µgg-1, 19.08%)> organic form (357.10µgg-1, 8.12%)> carbonate (2.0 µgg-1, 0.11%)> exchangeable (0.20 µgg-1, 0.012%), the middle region, residual (19967.46 µgg-1, 90.41%)> orgnic form (1294.69 µgg-1, 5.85%)> Fe-Mn oxides 825.74 µgg-1, 3.73%) > carbonate (2.16 µgg-1, 0.01%)> exchangeable (0.43µgg-1, 0.002%), the eastern region, residual (12594.33 µgg-1, 86.50%)> organic form (631.85µgg-1, 9.02%) > Fe-Mn oxides (475.78µgg-1, 4.39%) > carbonate (3.39µgg-1, 0.07%) > exchangeable (0.27µgg-1, 0.01%). Manganese (Mn) Figure 41 showed that the examined Mn fractions are represented in the following sequence: Residual > Fe-Mn oxides > carbonat > organic form > exchangeable. This sequence corresponds to the average percentage of 44.22%, 43.08%, 8.83, 3.75%, and 0.12%, respectively (Figure 42). Table 8 showed that the association of Mn with different fractions in the studied regions was in the order: western region, Fe-Mn oxides (95.04 µgg-1, 65.01%)> residual (53.53 µgg-1, 23.06%)>, carbonate (17.46 µgg-1, 7.54%)> organic form (6.46 µgg-1, 4.31%)> exchangeable (0.15µgg-1, 0.08%), middle region, residual (337.35µgg-1, 71.64%)> Fe-Mn oxide (77.32µgg-1, 15.90%) > carbonate (43.58µgg-1, 8.99%) > organic form (16.00µgg-1, 3.29%) > exchangeable (0.73 µgg-1, 0.17%), eastern region, residual (309.97µgg-1, 64.55%), > Fe-Mn oxides (30.96 µgg-1, 17.60%)> carbonates (54.24µgg-1, 15.43%) > organic form (13.02µgg-1, 2.26%)> exchangeable (0.56µgg-1, 0.16%). The data revealed that Mn fractionation was similar in the exchangeable fraction for all the three regions (<1%). The concentration of Mn associated with carbonate was relatively high in the sediments of the eastern region (15.43% on the average), may be due to anthropogenic origin. Caplat et al. (2005)(557) found that manganese is bound to the nonresidaul and the residual fractions of the sediments. Mn is mainly present in the acid soluble fraction (carbonate form) and significant affinity for the residual fraction (up to 50%). Also, it is noted from the results that the relatively high % of Mn in the western region (65.01%) were found in the Fe-Mn oxides form. Relatively higher concentration of Mn associated with the Fe–Mn oxides may caused by the adsorption of this metal by the Fe-Mn colloids (Purushothaman and Chakranpani, 2007)(273). These results were in agreement with the results of Faragallah and Khalil (2009)(326) they found that manganese is principally present as amorphous oxides rather than carbonate. This indicated that Mn comes from anthropogenic sources, which increases potential Mn mobility and bioavailability. In general, Mn can be present as oxides, hydroxides or in association with iron oxides and hydroxides. Mn ions can be adsorbed and / or partially ion exchanged on the surface of MnO2 and they can be environmentally mobile in certain conditions (Weisz et al., 2000)(558). Relatively low percentage of Mn was found to bind to organic matter and sulfides (4.31, 3.29, and 2.26% for the western, the middle, and the eastern region respectively). This indicates that organic matter is not the primary factor impacting the behavior of Mn in the study area. Large amounts of Mn accumulate in the residual fraction in the sediments of the middle and the eastern region of the Egyptian Mediterranean coastal area (71.64 and 64.55%, -193- respectively). The dominance of the residual fraction for Mn in the sediments may be attributed to most of Mn comes from the parent material of geologic origin. Zinc (Zn) The different fraction species and the total Zn content extracted from the surfacial sediments along the Egyptian Mediterranean coastal area are shown in Figure 43. This Figure showed that the examined Zn fractions are represented in the following sequence: Residual > Fe-Mn oxides > organic > carbonate form > exchangeable. Figure 44 showed that this sequence corresponding to average percentages of 71.70% for residual, 18.24% for Fe-Mn oxides, 5.79% for organic, 3.79% for carbonate and 0.47% for exchangeable Zn. The association of Zn with different fractions in the studied regions was observed at Table 9, in the order: western region, residual (11.44µgg-1, 59.20%)> Fe-Mn oxides (4.93 µgg-1, 27.75%), carbonate (1.02 µgg-1, 6.22%)> organic forms (1.42 µgg-1, 6.19%)>exchangeable (0.06µgg-1, 0.63%), middle region, residual (14.68µgg-1, 87.25%)> organic form (1.10µgg-1, 6.14%)> Fe-Mn oxides (1.05 µgg-1, 6.12%)>carbonates (0.06µgg-1, 0.40%)>exchangeable (0.01 µgg-1, 0.10%), eastern region, residual (10.62µgg-1, 86.03%), > Fe-Mn oxides (0.62µgg-1, 8.34%)> organic form (0.51µgg-1, 2.41%) > carbonate (0.08µgg-1, 2.33%)> exchangeable (0.03µgg-1, 0.89%). The data revealed that the fractionation of Zn was similar in the exchangeable fraction for all the three regions (<1%) except station 2 in Baghoush (3.84%; western region) and station 20 in Rafah (1.61%; eastern region). The carbonate fraction was relatively low (less than 10%) except at station 6 in the western region (14.89%). Zinc showed relatively high percentage in the reducible (Fe-Mn oxides) fraction (27.72%) in the western region. The relatively high percentage of Zn in this fraction is in agreement with the known ability of amorphous Fe-Mn oxides to scavenge Zn from solution (Ramos et al., 1999)(559). This relatively high percentage of Zn in the reducible fraction of the western region are a hazard for the aquatic environment because Fe and Mn species can be reduced into the porewater during early diagenesis, microbially mediated redox reactions (Canfield, 1989)(560). Dissolution will also release the Zn associated with oxide phases to the porewater, possibly to the overlying water column (Petersen et al., 1995) and to the benthic biota (Jones and Turki, 1997)(561). Abdallah (2007a)(292) stated that zinc mostly partitioning in the Fe-Mn oxides reducible and in the residual fractions, wherease in the carbonate and organic matter fractions slightly decreased with increasing concentrations in the sediments. Residual fraction is the first most important fraction of Zinc in the western region with percent concentration (average: 59.20%). While in the middle and the western regions, the residual form was the predominant for Zn (87.25 and 86.03% respectively). Relatively low percentage of Zn was found to bind to organic matter and sulfides (6.19, 6.14, and 2.41% for the western, the middle, and the eastern region respectively). This indicates that organic matter is not the primary factor impacting the behavior of Zinc in the study area. Nickel (Ni) The different fraction species and the total Ni content extracted from the surfacial sediments along the Egyptian Mediterranean coastal area are shown in Figure 45. This Figure showed that the examined Ni fractions are represented in the following sequence: Residual > Fe-Mn oxides > organic form > exchangeable > carbonate. Figure 46 illlustrated that this sequence corresponding to average percentages follows: 80.05% for residual, 10.32% for FeMn oxides, 6.91% for organic form, 1.91% for exchangeable and 0.81% for carbonate bound Ni. -194- The association of Ni with different fractions in the studied regions was listed at Table 10 in the following order: western region, residual (5.64 µgg-1, 76.96%)> Fe-Mn oxides (0.59 µgg-1, 11.91%), organic form (0.45 µgg-1, 6.61%)> exchangeable (0.12 µgg-1, 3.19%)> carbonate (0.07µgg-1, 1.35%), middle region, residual (30.85µgg-1, 81.75%)> Fe-Mn oxides (3.45µgg-1, 9.47%) > organic form (3.00µgg-1, 8.26%) > exchangeable (0.14µgg-1, 0.36%) > carbonates (0.06 µgg-1, 0.16%), eastern region, residual (26.05µgg-1, 91.12%), > Fe-Mn oxides (1.46µgg-1, 4.56%)> organic form (1.30µgg-1, 3.87%) > exchangeable (0.11µgg-1, 0.34%)> carbonate (0.04µgg-1, 0.12%). From the obtained data, relatively low percentage of Ni was found to bind to exchangeable and carbonate forms for the western, the middle, and the eastern region. While the bound to Fe-Mn oxides form showed relatively moderate percentage of Ni in the western and the middle region (average: 11.91 and 9.47%, respectively). The high average pecentage of residual Ni fraction (91.12%, eastern region; 81.75, middle region and 76.96, western region) reflects the natural background of Nickel in the investigated area. These results were inagreement with someother studies (e.g. Martin et al., 1998; Yuan et al., 2004)(562, 563). Silicate and residual fraction of metals are generally much less toxic for organisms in aquatic environment because this fraction is chemically stable and biologically inactive (Zakir and Shikazono, 2011)(264). Francois (1988)(483) showed that Ni distribution was primarily controlled by the mineralogical sediments more than its association with organic matter accumulation. These results were in agreement with the results of Verlimirovic et al. (2010)(564) who mentioned that the dominant proportions of nickel (59.1%) were found in the residual fraction, which indicates low availabilty. The residual fraction of metals is most strongly associated to the crystalline structures of the minerals, presenting small risk to the environment, and this holds for Ni. This is in accordance with literature data (Kartal et al., 2006)(565). Chromium (Cr) The different fraction species and the total Chromium content extracted from the study area are represented in Figure 47. Results showed that the examined Cr fractions are represented in the following sequence: Residual > Fe-Mn oxides > organic form > carbonate > exchangeable. As shown in Figure 48 Cr percentages were: 86.17% for residual, 8.14% for Fe-Mn oxides, 3.61% for organic form, 1.75% for carbonate and 0.33% for exchangeable Cr. The average values and its relative percentage of the five fractions in the studied regions (Table 11) can be arranged as the following: western region, residual (17.63 µgg-1, 76.63%)> Fe-Mn oxides (1.48 µgg-1, 14.34%), organic form (0.74 µgg-1, 5.37%)> carbonates (0.23 µgg-1, 3.1%)> exchangeable (0.05µgg-1, 0.56%), middle region, residual (117.34µgg-1, 97.72%)> organic form (1.54µgg-1, 1.63%) > Fe-Mn oxides (0.52µgg-1, 0.52%) > carbonate (0.10µgg-1, 0.09%) > exchangeable (0.04 µgg-1, 0.04%), eastern region, residual (125.73µgg-1, 98.19%), > organic form (1.07µgg-1, 0.90%)> Fe-Mn oxides (0.63µgg-1, 0.74%) > carbonates (0.07µgg-1, 0.09%)> exchangeable (0.051µgg-1, 0.08%). The obtained data revealed that the fractionation of Cr was similar in the exchangeable fraction for all the three regions (<1%) except station 2 and 3 in (Baghoush; 2.79% and ElNobarreya, 1.04%, respectively) in the western region, which considered very low, limiting its potential toxicity as pollutant, despite the total concentration for this metal being higher than the background value at most to the studied stations. Relatively low percentage of Cr was found to bind to carbonate (less than 1%) at the middle and the eastern region indicating its low mobility. On the other hand station 8 in the western region showed relatively moderate percentage of Cr bound to carbonate (12.17%). There was a relatively moderate -195- percentage (14.34%) of Cr found in the Fe-Mn oxides in the western region, while the middle and the eastern region showed low percentage of Cr bounded to the Fe-Mn oxides (0.52 and 0.74% respectively). Relatively low percentage of Cr was found to bind to organic matter and sulfides (5.37, 1.63, and 0.90% for the western, the middle, and the eastern region respectively). This indicates that organic matter is not the primary factor impacting the behavior of chromium in the study area. The high average pecentage of residual Cr fraction (98.19%, eastern region; 97.72, middle region and 76.63, western region) reflects the natural background of chromium in the investigated area. This indicates that this element is tightly bound to the sediment minerals and that it is not easily released to the environment. Lead (Pb) Lead is highly toxic to the environment. In the areas influenced by extensive human activities, a considerable proportion of Pb in the environment is of anthropogenic origin, because it is an important additive that has been widely used in many products (Gao et al., 2010)(250). The different fraction species and the total lead content extracted from the present study are presented in Figure 49. The examined Pb fractions are represented in the following sequence: Residual >Fe-Mn oxides > carbonate > organic form > exchangeable. This sequence corresponding to average percentages of 48.7% for residual, 26.05% for Fe-Mn oxides, 13.89% for carbonates, 8.44% for organic and 2.92% for exchangeable Pb as shown in Figure 50. The association of Pb with different fractions in the following order: western region, residual (4.45 µgg-1, 35.21%)> Fe-Mn oxides (5.84 µgg-1, 33.80%), carbonate (4.72 µgg-1, 21.36%)> organic form (1.18 µgg-1, 7.79%)> exchangeable (0.22µgg-1, 4.72%), middle region, residual (5.16µgg-1, 67.47%)> Fe-Mn oxides (1.07µgg-1, 15.18%) > organic form (0.74 µgg-1, 9.47%) > exchangeable (0.30µgg-1, 4.12%) > carbonate (0.29 µgg-1, 3.76%), eastern region, residual form (3.42µgg-1, 57.17%), > Fe-Mn oxides (1.18µgg-1, 21.47%)> organic form (0.38µgg-1, 8.83%) > carbonates (0.42µgg-1, 8.28%)> exchangeable (0.29µgg-1, 4.70%). From the obtained data, it is observed that the content of Pb measured in the exchangeable fraction were (4.72, 4.12, and 4.70%) on the average for the western, middle and the eastern region respectively. Lead showed appreciable concentration in the carbonate fraction, with a relative abundance value of 21.36 % in the western region. Similar results were reported for Pb in carbonate in surface sediment samples from Naha port, Japan (Noah and Oomari, 2006)(566). Zhang et al. (1988)(567) attributed the high carbonate bounded lead in Huanghe estuarine sediments to the similarity of its ionic radii to that of calcium, which allows lead to substitute calcium in the carbonate crystal lattice to form a mixed carbonate phase. Carbonate fraction is also termed to be the most bioavailable fraction to the aquatic organisms since the elements are loosly bound to the sediments and can be released back to the environment (Tack and Verloo, 1995)(555). A major portion of Pb is bound to the Fe/Mn oxides with comparable amounts associated with the carbonate fraction. The fact that Pb can form stable complexes with Fe and Mn dioxide (Ramos et al., 1994)(568) may be the reason why reducible Pb is more abundant than other tow non-residual fractions of Pb (Gao et al., 2010)(250). Lead was dominant in the reducible fraction, which has been proved to be sensitive to anthropgenic inputs (Modak et al., 1992)(569), and it represented 33.80, 15.18, and 21.47% of the total Pb for the western, middle and eastern region respectively. Amorphous Fe oxyhydroxide phase is well recognized for its scavenging properties of metals in the environment (Zakir and Shikazono, 2011)(264). This phase accumulated metals from the aqueous system by the mechanism of adsorption and co-precipitation (Bordas and Bourg, 2001)(570). Fe and Mn hydrous oxides are important scavengers of Pb in sediments (Wong et -196- al., 2007)(571). Lead species are strongly sorbed to Fe/Mn oxides, which are reported to be more important than association with clays and organic materials (Fergusson, 1990)(3). The sorption of lead onto Fe/Mn oxides is not affected by aging, but does decrease with an increase in Cl¯ ion concentration, due to the formation of lead chloride complexes. As a result, lead is immobile in the aquatic environment and tends to accumulate in sediments close to its point of entry (Morrison, 1996)(68). The metal in this fraction may be released if the sediments is subjected to more reducing conditions (Singh et al., 2005)(266). -197- Concentration (µgg-1) 12000 10000 8000 6000 4000 2000 0 F1 F2 F3 F4 F5 Figure 39: The average concentration of Fe speciation µgg-1 in surfacial sediments from the Egyptian Mediterranean coast 0.01% 0.07% 12.24% 7.42% 80.27% F1 F2 F3 F4 F5 Figure 40: The relative percentage of Fe species in surfacial sediments from the Egyptian Mediterranean coast -198- Concentration (µgg-1) 200 150 100 50 0 F1 F2 F3 F4 F5 Figure 41: The average concentration of Mn speciation µgg-1 in surfacial sediments from the Egyptian Mediterranean coast 8.83% 0.12% 44.22% 43.08% 3.75% F1 F2 F3 F4 F5 Figure 42: The relative percentage of Mn species in surfacial sediments from the Egyptian Mediterranean coast -199- Concentration (µgg-1) 14 12 10 8 6 4 2 0 F1 F2 F3 F4 F5 Figure 43: The average concentration of Zn speciation µgg-1 in surfacial sediments from the Egyptian Mediterranean coast 0.47% 3.79% 18.24% 5.79% 71.70% F1 F2 F3 F4 F5 Figure 44: The relative percentage of Zn species in surfacial sediments from the Egyptian Mediterranean coast -200- Concentration (µgg-1) 20 15 10 5 0 F1 F2 F3 F4 F5 Figure 45: The average concentration of Ni speciation µgg-1 in surfacial sediments from the Egyptian Mediterranean coast 1.91% 0.81% 10.32% 6.91% 80.05% F1 F2 F3 F4 F5 Figure 46: The relative percentage of Ni species in surfacial sediments from the Egyptian Mediterranean coast -201- Concentration(µgg-1) 70 60 50 40 30 20 10 0 F1 F2 F3 F4 F5 Figure 47: The average concentration of Cr speciation µgg-1 in surfacial sediments from the Egyptian Mediterranean coast 0.33% 1.75% 8.14% 3.61% 86.17% F1 F2 F3 F4 F5 Figure 48: The relative percentage of Cr species in surfacial sediments from the Egyptian Mediterranean coast -202- Concentration (µgg-1) 5 4 3 2 1 0 F1 F2 F3 F4 F5 Figure 49: The average concentration of Pb speciation µgg-1 in surfacial sediments from the Egyptian Mediterranean coast 2.92% 13.90% 48.70% 26.05% 8.44% F1 F2 F3 F4 F5 Figure 50: The relative percentage of Pb species in surfacial sediments from the Egyptian Mediterranean coast -203- 6.2.3.1. Risk assessment code (RAC) The distribution of metal speciation associated with different geochemical fraction is a critical parameter to assess the potential mobility and biovailability of heavy metals in sediments (Wang et al., 2010)(258). The RAC considers the different binding strengths of the metals in the various sediments fractions. It assesses the availability of metals in solution by applying a scale to the percentage of metals in the exchangeable and carbonate sediment fractions. This classification is considered by Perin et al. (1985)(572). The RAC classification defines risk levels as zero, low, medium, high and very high, depending on the percentage value (Jain, 2004)(275). Risk assessment code has been used to assess environmental risks and estimate possible damage to benthic organisms caused by contaminated sediments (Passos et al., 2011)(263). Accordingly, if this value is < 1% there is no risk for the aquatic system, 1-10% indicates low risk, 11-30 % medium risk, 31-50% high risk, and > 50% very high risk (Table 26) (Passos et al., 2011)(263). This classification scheme is presented as the following: Table 26: Classification of Risk assessment code (RAC) RAC No risk Low risk Medium risk High risk Very high risk Criterion (%) <1 1-10 11-30 31-50 >50 The risk assessment code of (Fe, Mn, Zn, Cr, Ni and Pb) was evaluated in the sediments of the Egyptian Mediterranean coastal area. From the present results (Table 27), it can be seen that the sum of the exchangeable and carbonate-bound fraction of Cr, Fe, Mn, Ni, Pb, and Zn was 0.04-12.58 (average: 2.08%), 0.01-0.34 (average: 0.06%), 0.87-18.96 (average: 8.95%), 0.14-10.88 (average: 2.72%), 4.32-55.43 (average: 16.82%), and 0.2615.27 (average: 4.26%), respectively. This suggests that Fe has no risk to local environment, Cr, Mn, Ni, and Zn have posed low risk to local environment, Pb was at Medium risk level. The percentage of bioavailable forms (exchangeable and carbonate fractions) in sediments of the Egyptian Mediterranean coastal area were lower than (10%) except for Pb reached to 16.82% on average. The potential bioavailable form (Fe/Mn oxide and organic matter and sulfide fractions) were higher than 10%, the highest value reached to 46.83% for Mn. When the environmental conditions are changed, the potential bioavailable form can dissolve or degrade and release the metal. The potential ecological risk presented by this case can not be neglected. Elevated levels of metals in the Fe/Mn oxide and organic matter and sulfide fractions can reflect the pollution extent caused by human activities (Liu et al., 2009)(573). -204- Table 27: Risk assessment code (RAC) (%) and risk rank for trace metals in the sediments of the Egyptian Mediterranean coastal area Station 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 Average Cr RAC 1.45 12.43 3.30 2.28 0.80 3.50 1.80 12.58 0.39 0.79 0.93 0.27 0.10 0.07 0.23 0.10 0.05 0.10 0.04 0.30 2.08 Rank Low risk Medium risk Low risk Low risk No risk Low risk Low risk Medium risk No risk No risk No risk No risk No risk No risk No risk No risk No risk No risk No risk No risk Low risk Fe RAC 0.032 0.256 0.342 0.029 0.038 0.119 0.017 0.063 0.035 0.069 0.035 0.027 0.015 0.007 0.005 0.008 0.025 0.011 0.021 0.148 0.068 Mn Rank No risk No risk No risk No risk No risk No risk No risk No risk No risk No risk No risk No risk No risk No risk No risk No risk No risk No risk No risk No risk No risk RAC 4.41 3.58 4.45 8.71 6.14 6.62 6.34 2.79 16.93 4.82 18.96 6.23 0.87 4.39 12.04 11.55 13.72 15.35 13.17 17.99 8.95 Rank Low risk Low risk Low risk Low risk Low risk Low risk Low risk Low risk Medium risk Low risk Medium risk Low risk No risk Low risk Medium risk Medium risk Medium risk Medium risk Medium risk Medium risk Low risk Ni RAC 3.28 9.40 3.48 2.53 6.41 7.18 3.29 10.88 1.07 0.80 1.46 0.51 0.46 0.54 0.55 0.81 0.18 0.56 0.76 0.14 2.72 -205- Rank Low risk Low risk Low risk Low risk Low risk Low risk Low risk Low risk Low risk No risk Low risk No risk No risk No risk No risk No risk No risk No risk No risk No risk Low risk Pb RAC 14.95 19.84 47.94 9.86 55.20 55.43 24.05 6.65 5.96 8.12 7.19 6.48 8.45 13.92 8.11 8.15 5.71 4.32 11.61 14.35 16.82 Rank Medium risk Medium risk High risk Low risk High risk High risk Medium risk Low risk Low risk Low risk Low risk Low risk Low risk Medium risk Low risk Low risk Low risk Low risk Medium risk Medium risk Medium risk Zn RAC 2.72 11.10 1.62 5.54 6.50 15.27 4.52 9.01 4.77 9.58 4.77 0.93 0.54 0.46 0.31 0.35 0.60 0.26 0.48 5.95 4.26 Rank Low risk Medium risk Medium risk Low risk Low risk Medium risk Low risk Low risk Low risk Low risk Low risk No risk No risk No risk No risk No risk No risk No risk No risk Low risk Low risk 6.2.4. Toxicity assessment of trace metals in sediments based on AVS, SEM models Acid volatile sulfide (AVS) is one of the major chemical components that control the activities and availability of metals in the interstitial waters of sediments. Sulfide reacts with several divalent transition metal cations (cadmium, copper, nickel, lead, and zinc) to form highly insoluble compounds that are not bioavailable (USEPA, 2004)(444). Metal bioavailability refers to the ability of metals to be accumulated by animals and plants, which is subjected to the ingestion habits of animals, e.g., through water (pore water and overlying water) and/or through sediments (Chapman et al., 2002)(574). Although metals bound to AVS cann't be released from sediment into water, they may be ingested by animals. The AVS procedure extracts metals not only from the target sulfide phase, but also from other nonsulfide phases that may be bioavailable (Feng et al., 2005)(575). The parameters that determine the bioavailability/toxicity of trace metals (results of SEM and AVS analysis) in sediment samples from the Egyptian Mediterranean Coast are presented in Table 28. From the obtained data, it was observed that the concentrations of AVS ranged from 0.015 µmoleg-1 dry weight at station 2 in Baghoush to 31.326 µmoleg-1 dry weight at station 7 in NIOF (western region) (average: 1.847 µmoleg-1dry weight). This is in agreement with literature values reported from marine and fresh water sediments in the US and Canada, which were found to range from 0.1 to 75 µmoleg-1dry weight (Di Toro et al., 1990; Ankley et al., 1991; Ankley et al., 1993; Casas and Crecelius, 1994; Carlson et al., 1993; Allen et al., 1993)(22, 228, 424, 576-578). Relatively small AVS levels (<2µmoleg-1) have been found at almost all the studied locations. Station 1 in salloum has AVS concentration (3.51µmoleg-1) and station 7 in NIOF has an AVS level of more than 10 µmoleg-1 (31.326 µmoleg-1). Hence, according to Van den Hoop et al. (1997)(579) the sediment in station 7 in NIOF are able to bind heavy metals in large quantities. The range and average concentrations of SEM were 0.0001-0.0011 µmole/g (mean: 0.0003 µmole/g) for Cd, 0.002-0.046 µmole/g (average: 0.0169 µmole/g) for Cu, 0.002-0.059 µmole/g (average: 0.0186 µmole/g) for Ni, 0.004-0.033 (average: 0.0118 µmole/g) for Pb and 0.002-0.174 (average: 0.0549 µmole/g) for Zn. The use of different relationships between AVS and SEM to establish mechanical models such as the ratio of SEM and AVS (SEM/AVS), the difference between SEM and AVS (SEM-AVS) or the organic carbon normalized difference between SEM and AVS (SEM-AVS)/ foc to assess metal toxicity has been widely applied (Di Roro et al., 1990; Burton et al., 2005;Yin et al., 2008)(22, 246, 247). The AVS-SEM models are generally based on the hypothesis that when there are enough sulfides in the sediment, metals will react with the sulfide to form insoluble compounds that are not bioavailable to benthic biota; however, if the levels of sulfide are too low, the metals will be toxic toward the benthic biota (Yin et al., 2010)(580). It has been verified (Di Toro et al., 1990)(22) that divalent transition metals do not begin to cause toxicity in sediment until the reservoir of sulfide is used up (i.e. until the molar concentration of metals exceeds the molar concentration of sulfide), typically at relatively high dry weight metal concentrations. This observation has led to a laboratory measurement technique for calculating the differences between SEM concentration and AVS concentration in field samples, to determine potential toxicity. To evaluate the potential effects of metals on benthic species, the molar concentration of AVS ([AVS], µmole g-1) is compared to the sum of SEM molar concentrations ([SEMi], µmole g-1) for five metals: cadmium, copper, nickel, lead, and zinc; when [SEMi]/[AVS]<1, acute toxicity due to heavy metals is not probable. -206- On the other hand, the sediment may be considered potentially toxic when this ratio is >1 (Di Toro et al., 1990)(22). From the obtained data at Table 28 and according to Di Toro et al. (1990)(22) the sediment may be considered potentially toxic at stations 2, 6, 8, 10, 11, 12, 13, 14, 15, 16, 18, and 19 in Baghoush, Western Harbour, power station, Maadia, Rashid West, Rashid East, Burullus, New Damietta, Ras El-Barr, El-Gamil East, and Port Said respectively. Acute toxicity due to heavy metals is not probable at stations 3, 4, 5, 7, 9, 17, and 20 in Nobarreya, Dekhaila, El-Mex, NIOF, AbuQir, El-Gamil west, and Rafah respectively. Di Toro et al. (1990)(22) proposed that a SEM/AVS>1 indicated toxicity, then on the contrary, the pore water concentrations would be low and no toxicity to sediment dwelling organisms would be observed under these conditions. However, this prediction was not always accurate when the molar sum of the SEM was greater than that of the AVS, which could be due to the different sensitivities of the benthic biota in the sediment to metals (Hare et al., 1994)(581). Burton et al. (2005)(246) conducted a long period field toxicity experiment and concluded that sediments with a SEM to AVS ratio of 8.32 or greater would result in high macroinvertebrate toxicity, the ratios between 2 and 8.32 are occasionally toxic, and the ratio less than 2 are not toxic. Table 28 showed that according to Burton et al. (2005)(55) the sediments at stations 6, 8, 16, 18, and 19 (Western Harbour, Eastern Harbour, Ras El-Burr, El-Gamil East, and Port said), respectively are occasionally toxic while the other stations are not toxic. SEM/AVS has been endorsed as the best technology for assessing the bioavailability of five important toxic metals (Pb, Zn, Cu, Cd, and Ni) (Allen et al., 1993)(424). Other relationships between SEM and AVS can be expressed as the molar difference between SEM and AVS (SEM-AVS). According to USEPA (2004)(444), the assessment of metal toxicity is based on the difference between the corresponding SEM and AVS molar concentrations. In this approach each sample falls into one of three categories (tiers): associated adverse effects on aquatic life are probable (Tier 1); associated adverse effects on aquatic life are possible (Tier 2); or no indication of associated adverse effects (Tiers 3). According to the USEPA evaluation, when [SEM]–[AVS] is greater than 5, the sampling site is classified as Tier 1. If [SEM] – [AVS] is between zero and 5, the sampling site is classified as Tier 2. If [SEM]–[AVS] less than zero, the sampling site is classified as Tier 3. From this point of view, Table 29 Shows that the values of [SEM]-[AVS] calculated at sites 2, 6, 8, 10, 11, 12, 13, 14, 15, 16, 18, and 19 in Baghoush, Western Harbour, Eastern Harbour, Power station, Maadia, Rashid west, Rashid East, Burullus, New Damietta, Ras El-Burr, ElGamil East, and Port Said are positive and less than 5 means associated adverse effects on aquatic life are possible (tier 2). Whereas, (SEM-AVS) calculated at sites 1, 3, 4, 5, 7, 9, 17, and 20 (El-Salloum, Nobarreya, Dekhaila, El-Mex, NIOF, El-Gamil West, and Rafah) respectively, are negative reflecting no indication of associated adverse effects at these sampling sites (tier 3). This result is consistent with the findings of SEM /AVS. The obtained data concluded that the remobility and bioavailabilty of trace metals contained in sediments of the Egyptian Mediterranean coastal area are low. TOC and AVS are significant parameters for the evaluation of toxicity of sediments since they play an important role in controlling the availability of inorganic and organic contamination and the toxicity of sediments (McGrath et al., 2002)(245). EPA has developed a recommended approach, Equilibrium Partitioning Sediment Benchmarks (ESBs) for estimating metal toxicity based on the bioavailable metal fraction, which can be measured in -207- pore water and /or predicted based on the relative sediment concentrations of AVS, SEM and organic carbon (TOC). Both AVS and TOC are capable of sequestering and immobilizing a range of metals in sediments (USEPA, 2005)(582). The benchmarks application document advises that: (i) any sediment in which [SEM-AVS]/foc < 130 μmol/g OC should pose a low risk of adverse biological effects due to cadmium, copper, lead, nickel and zinc (ii) any sediment in which 130 μmol/gOC < [SEM-AVS]/foc < 3000 μmol/g OC may have adverse biological effects due to cadmium, copper, lead, nickel and zinc (iii) in any sediment in which [SEM-AVS]/foc >3000 μmol/g OC adverse effects due to cadmium, copper, lead, nickel and zinc may be expected (iv) any sediment in which [AVS] > 0.1 μmol/g OC will not cause adverse biological effects due to chromium or silver. The results as shown in Table 30 revealed that [SEM-AVS]/foc < 130 μmol/g at all sampling sites. This sediments should pose a low risk of adverse biological effects due to cadmium, copper, lead, nickel and zinc at all stations according to (USEPA, 2005)(582). The models (SEM/AVS, SEM-AVS, SEM-AVS/foc) are useful tools for the assessment of sediment quality (Yin et al., 2010)(580). The concentration of AVS in sediment is a product of the equilibrium between AVS generation and the loss due to oxidation or diffusion. Consequently, the AVS contents in sediments may vary with those factors affecting the supply of organic matter, the rate of SO42- reduction, and the redox status of the sediments (Oehm et al., 1997)(583). Low positive correlation (r2= 0.39) between AVS and OC as shown in Figure 51. Therefore, organic matter may not be the major controlling factor for AVS content in the sediments because of the lower TOC concentrations in comparison with freshwater sediments (Song and Muller, 1999)(236). High concentrations of SO42- (20-30 mM) in marine sediments, compared with 0.2 mM in freshwater sediments, can be responsible for most of the anoxic oxidation process (Blazer, 1989)(584). Thus, SO42- reduction is probably more important for AVS formation than the supply of organic matter in marine sediments (Fang et al., 2005)(26). OC 0.012 0.01 R2 = 0.3919 0.008 0.006 0.004 0.002 0 0 10 20 30 40 AVS Figure 51: The relationship between OC and AVS Although this method can be used for the detection of pollution problems in the polluted sediments, sediment classification on the basis of these analyses should not be final. Relation SEM/AVS>1 is not showing the actual bioavailability and toxicity, because there are bound metals in sediment in different forms with iron and manganese (Ankely et al., 1996)(23). When SEM/AVS>1, other binding forms for metals in sediments should be considered to assess the bioavailability of metals. The sequential extraction procedure must be used as an additional tool for assessing the potential bioavailability and toxicity of metals -208- in sediment. Although the role of AVS is to transforms the metals from biologically available chemical species into insoluble sulfides, the sedimentary sulfide system is of highly dynamic nature, metals that are associated with AVS may be released within sediments through storms, dredging ativities, oxidation, etc. and may have adverse environmental impact (Feng et al., 2005)(575). To have better understanding of SEM and metals associated with particular geochemical phases, sequential extraction procedure was conducted. -209- Table 28: The concentrations of AVS, SEM (µmoleg-1), and the ratio of SEM and AVS in surface sediments of the Egyptian Mediterranean coastal area. Station AVS 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 3.505 0.015 0.036 0.26 0.335 0.032 31.326 0.058 0.576 0.123 0.116 0.049 0.052 0.044 0.11 0.043 0.071 0.038 0.029 0.119 SEM SEM/AVS 0.1513 0.0159 0.0162 0.1465 0.2408 0.0661 0.2014 0.2063 0.0892 0.1401 0.1342 0.0501 0.0640 0.0485 0.1329 0.1220 0.0448 0.0874 0.0792 0.0122 0.043 1.060 0.449 0.563 0.719 2.065 0.006 3.557 0.155 1.139 1.157 1.023 1.231 1.102 1.208 2.836 0.630 2.300 2.731 0.102 Toxicity according to Di Toro et al. (1990)(22) acute toxicity due to heavy metals is not probable the sediment may be considered potentially toxic acute toxicity due to heavy metals is not probable acute toxicity due to heavy metals is not probable acute toxicity due to heavy metals is not probable the sediment may be considered potentially toxic acute toxicity due to heavy metals is not probable the sediment may be considered potentially toxic acute toxicity due to heavy metals is not probable the sediment may be considered potentially toxic the sediment may be considered potentially toxic the sediment may be considered potentially toxic the sediment may be considered potentially toxic the sediment may be considered potentially toxic the sediment may be considered potentially toxic the sediment may be considered potentially toxic acute toxicity due to heavy metals is not probable the sediment may be considered potentially toxic the sediment may be considered potentially toxic acute toxicity due to heavy metals is not probable -210- Toxicity according to Burton et al. (2005)(55) Not toxic Not toxic Not toxic Not toxic Not toxic Occasionally toxic Not toxic Occasionally toxic Not toxic Not toxic Not toxic Not toxic Not toxic Not toxic Not toxic Occasionally toxic Not toxic Occasionally toxic Occasionally toxic Not toxic Table 29: The concentrations of AVS, SEM (µmole/g), and the SEM-AVS in surface sediments of the Egyptian Mediterranean coastal area. Sample AVS 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 3.505 0.015 0.036 0.26 0.335 0.032 31.326 0.058 0.576 0.123 0.116 0.049 0.052 0.044 0.11 0.043 0.071 0.038 0.029 0.119 SEM SEM-AVS 0.1513 0.0159 0.0162 0.1465 0.2408 0.0661 0.2014 0.2063 0.0892 0.1401 0.1342 0.0501 0.0640 0.0485 0.1329 0.1220 0.0448 0.0874 0.0792 0.0122 -3.354 0.001 -0.020 -0.114 -0.094 0.034 -31.125 0.148 -0.487 0.017 0.018 0.001 0.012 0.004 0.023 0.079 -0.026 0.049 0.050 -0.107 Toxicity according to USEPA (2004)(444) Tier 3 Tier 2 Tier 3 Tier 3 Tier 3 Tier 2 Tier 3 Tier 2 Tier 3 Tier 2 Tier 2 Tier 2 Tier 2 Tier 2 Tier 2 Tier 2 Tier 3 Tier 2 Tier 2 Tier 3 Tier 2; associated adverse effects on aquatic life are possible Tier 3; no indication of associated adverse effects Table 30: The concentrations of AVS, SEM (µmole/g), and the SEM-AVS/fOC in surface sediments of the Egyptian Mediterranean coastal area. Station AVS SEM OC/g (SEM-AVS)/foc 3.505 0.1513 0.0027 -1242.113 1 0.015 0.0159 0.0032 0.282 2 0.036 0.0162 0.0072 -2.753 3 0.26 0.1465 0.0034 -33.385 4 0.335 0.2408 0.0031 -30.380 5 0.032 0.0661 0.0038 8.964 6 31.326 0.2014 0.01 -3112.458 7 0.058 0.2063 0.0056 26.482 8 0.576 0.0892 0.0022 -221.267 9 0.123 0.1401 0.0079 2.160 10 0.116 0.1342 0.0028 6.508 11 0.049 0.0501 0.0005 2.265 12 0.052 0.0640 0.0011 10.921 13 0.044 0.0485 0.0018 2.498 14 0.11 0.1329 0.0029 7.898 15 0.043 0.1220 0.0014 56.398 16 0.071 0.0448 0.0019 -13.812 17 0.038 0.0874 0.002 24.709 18 0.029 0.0792 0.0014 35.858 19 0.119 0.0122 0.002 -53.401 20 -211- 6.3. Ecological risk assessment The ecological risk assessment (REA) approach provides an adequate framework for estimating the effects associated to the occurrence of contaminants in sediments. ERA is a process for evaluating the likelihood that adverse ecological effects may occur or are occurring as a result of organism exposure to one or more environmental stressors (USEPA, 1998)(330). A screening ERA is typically the initial phase of the process, aiming at identifying stressors and receptors that pose potentially unacceptable risks and those which can be ruled out (Duke and Taggart, 2000)(585). Accordingly, the effects in the evaluation phase are often estimated by the application of the appropriate quality benchmarks, namely the suitable environmental quality criteria. The term criteria refers to a definitive value, refined over time based on region-specific effects and contaminant information, but unfortunately, these values are not always available (Chapmand et al., 1999)(586). In these circumistances, values that are more generic are selected in the screening ERA, generally adopted from other regions. In the case of sediment contamination, several sets of sediment toxicity benchmarks, the sediment quality guidelines (SQGs), are usually adopted (Chapman and Mann, 1999)(509). The basic approach used to derive the risk assessment in the Egyptian Mediterranen coast was shown in Chapter II (review; section 2.4). The ecological risk assessment is generally conducted in a three step process: problem formulation, Analysis step and risk characterization phase. The proceeding sections will discuss in details the formulation of the ERA in the Egyptian Mediterranean Sea. 6.3.1. Problem formulation In the problem fromulation, the purpose of the assessment is defined and a plane for analyzing and characterizing the risks is determined, generating a conceptual model and defining the endpoints (Gomez-Gutierrez et al., 2007)(587). In this study the conceptual model is based on the hypothesis that industrial, urban and agricultural land based sources of contamination have contributed to the release of trace metals into the Egyptian Mediterranean coast, which may find their ultimate fate in the sediments. Thus, the assessment will consist on the recognition of possible adverse effects of trace metals towards the marine ecosystem, and particularly the benthic community, which is to be the most susceptible to the sediment bound contaminants. A full description of the Egyptian Mediterranean Sea is given in Chapter III (Socioeconomic and environmental aspects). Selected assessment and measurement endpoints in the present study are given in Table 31. The assessment will consist on the recognition of possible generic adverse effects of the investigated chemicals (trace metals) towards the marine ecosystem, and particularly the benthic community, which is to be the most susceptible to the sediment bound contaminants (Jones et al., 1999)(588). In the present study, measurement endpoints depended on measuring the chemical concentrations of the target pollutants in the sediments. For toxicity to occur, a contaminant must be present, a receptor must be present, and there must be a complete exposure pathway by which the receptor is exposed to the contaminant. The conceptual site model indentifies where contaminant interactions with biota can occur. A conceptual model describes the fate and transport of site contaminants through the physical system (sediment of the Egyptian Meditrranean coast) and key receptor exposure pathways. The conceptual site model used in the Ecological risk assessment of the Egyptian Mediterranean Sea is presented in Figure 52. As shown in Figure 52, the selected exposure media was the Sea sediments. The ecological receptors included in this risk assessment were the benthic organisms, although they were not -212- investigated directly. The selected exposture route was the direct contact of the benthic organisms with the bay sediments. Table 31: Assessment and measurement endpoints for the SERA of the Egyptian Mediterranean coast. Receptor Assessment endponts Receptor Measurement endpoint type - Trace metals concentrations (site) Sediments Sediment quality Abiotic - Sediment quality guidelines for protection of aquatic life (collected from literature) 6.3.2. Analysis setup The analysis part is designed to characterize the exposure, determining how likely is to occur and, given this exposure, the potential and type of ecological effects that can be expected (Gomez-Gutierrez et al., 2007)(587). 6.3.2.1. Exposure characterization The assessment of the exposure was based on the concentrations of trace metals found in the Egyptian Mediterranean sediments. Concentrations were reported in µgg-1 dry weight. Only trace metals with available guidelines were evaluated in the SERA. The concentrations of trace metals in sediment samples are given in Chapter V (Results; Table 5). The range and average ± SD concentrations (µgg-1) were: 2.05-62.21 (22.19 ±15.84) for Zn, 0.46-26.26 (8.46 ±6.22) for Cu, 1.65-60.25 (25.93 ±20.96) for Ni, 4.08-297.95 (82.74 ±90.18) for Cr, 3.34-53.67 (13.17 ±11.90) for Pb, 0.04-0.47 (0.22 ±0.15) for Cd. The maximum concentration for each trace metal was used in the SERA as a conservative assumption. The maximum concentrations were: (62.21µgg-1) for Zn, -1 (26.26µgg ) for Cu, (60.25µgg-1) for Ni, (297.95µgg-1) for Cr, (53.67µgg-1) for Pb and (0.47µgg-1) for Cd 6.3.2.2. Effect characterization The effect characterization was based on several sets of sediment quality guidelines (SQGs) reported in literature. These SQGs have been calculated using different theoretical and empirical approaches, such as the equilibrium partitioning (EqP) method (Di Toro et al., 1991; USEPA, 1994)(589, 590), the screening level concentration approach (Neff et al., 1988)(591), the effects range approach including the effect range low (ERL) and the effect range medium (ERM) (Long et al., 1995)(199), the effects level approach (ELA) including the threshold (AET) approach including the apparent effect threshold low (AET-L) and the apparent effects threshold high (AET-H) (Barrick et al., 1988)(592) and the logistic regression models including T20, which represents the probability of occurrence of adverse ecological effects in 20% of the investigated samples, T50 and T80 (USEPA/NOAA, 2005)(593). In most of the developed sediment quality guidelines, more than one value is available, one representing the low level of adverse ecological effects (ERL, ETL and T20) and the other representing higher level of adverse ecological effects (ERM, PEL, T50 and AET-L). For some sediment quality guidelines, values representing higher level of adverse ecological effects are available (T80 and AET-H), where extreme adverse ecological effects could be expected. -213- A full assessment of the impacts of trace metals in the Egyptian Mediterranean coastal area using the different methods of SQGs were previously discussed in this chapter (section 6.3). As a result of the different approaches mentioned above, SQGs reported for different pollutants exhibit a great variability, so that some authors have developed the consensus based approach trying to harmonize the existing values (MacDonald et al., 2000)(503), which was used in the present study for the risk calculations and for pointing out the presence of any hot spots in the Egyptian Mediterranean Coast. Consensus based sediment quality values developed for the investigated pollutants in the Egyptian Mediterranean coast sediments, together with the sediment quality guidelines used in their calculation are given in table 30. Because consensus based marine SQGs were not available for all the target metals, values were calculated for all the target metals in the present study following the methodology described by MacDonald et al. (2000)(503). In the consensus approach (CA), consensus-based SQGs are derived from the existing SQGs that have been established for the protection of sediment-dwelling organisms. Derivation of numerical sediment quality guidelines using the CA involves several steps. First, the SQGs for the protection of sediment-dwelling organisms are grouped into two categories according to their original narrative intent, including threshold effect concentrations (TECs) and probable effect concentrations (PECs). TEC group included ERL (Long and Morgan, 1991; Ingersoll et al. 1996a, b)(594-596), TEL (Smith et al. 1996; Ingersoll et al. 1996 a, b)(595-597) and T20 (USEPA/NOAA, 2005)(593). The TECs are intended to identify concentrations below which harmful effects on sediment-dwelling organisms are unlikely to be observed. The PECs are intended to identify concentrations above which harmful effects on sediment-dwelling organisms are likely to be frequently or always observed (MacDonald et al. 1996; Swartz, 1999)(510, 598). PEC group included PEL (Smith et al., 1996; Ingersoll et al., 1996a, b)(595-597), ERM (Long and Morgan, 1991; Ingersoll et al., 1996a)(594, 595), T50 (USEPA/NOAA, 2005)(593) and AET-L (Barrick et al., 1988)(592). Following classification of the existing SQGs, consensus-based TECs were calculated by determining the geometric mean of the SQGs that are included in this category. Likewise, consensus-based PECs were calculated by determining the geometric mean of the PEC-type values. The geometric mean, rather than the arithmetic mean, was calculated because it provides an estimate of central tendency that is not unduly affected by outliers and because the SQGs may not be normally distributed. Consensus-based TECs or PECs are calculated only if three or more published SQGs are available for a chemical substance or group of substances (MacDonald et al., 2000)(503). Recent evaluations based on combining several sets of guidelines into one to yield "consensus-based" guidelines have shown that such guidelines can substantially increase the reliability, predictive ability, and level of confidence in using and applying the guidelines (MacDonald et al., 2000; Ingersoll et al., 2000)(503, 599). The agreement of guidelines derived from a variety of theoretical and empirical approaches helps to establish the validity of the consensus-based values. Use of values from multiple guidelines that are similar for a contaminant provides a weight-of evidence for relating to actual biological effects. A series of papers were produced (Swartz, 1999; MacDonald et al., 2000)(503, 598) that addressed some of the difficulties associated with the assessment of sediment quality conditions using various numerical sediment quality guidelines. The results of these investigations demonstrated that combining and integrating the effect levels from several sets of guidelines to result in consensus based sediment quality guidelines provide a unifying synthesis of the existing guidelines, reflect causal rather than correlative effects, and can account for the effects of contaminant mixtures in sediment (Swartz, 1999)(598). -214- Aquatic receptors Point source 1- Nobarreya drain 2- Abu Qir Drain (ElAmiaa) 2- Lake Mariout (El-Mex outfall) 3- Lake Idku outlet 4- Burullus outlet 5- Lake Manzala outlet (El-Gamil outlet) 6- Rosetta (River Nile Estuary) 7- Damietta (River Nile Estuary) Exposure Media fish h Benthic s Ingestion Industrial, domestic and agricultural effluents Local residents I Water Direct contact X Ingestion Industrial effluents discharged directly into the sea Sediments Direct contact I X I Amosheric input Non Point source Aquatic food items fish & benthics Shipping activities Ingestion X = Pathway is complete I = Pathway is insignificant Figure 52: Conceptual site model for the SLERA in the Egyptian Mediterranean Coast -215- X Additionally, MacDonald et al. (2000)(503) have evaluated the consensus based effect levels for reliability in predicting toxicity in sediments by using matching sediment chemistry and toxicity data from field studies conducted throughout the United States. The results of their evaluation showed that most of the consensus-based threshold effect concentrations (TEC -lower effect level) and probable effect concentrations (PEC - upper effect level) for individual contaminants provide an accurate basis for predicting the absence or presence, respectively, of sediment toxicity. The consensus-based SQGs as developed only involve effects to benthic macroinvertebrate species. The guidelines do not consider the potential for bioaccumulation in aquatic organisms and subsequent food chain transfers to humans or wildlife. Where bioaccumulative compounds are involved, the consensus-based SQGs need to be used in conjunction with other tools, such as bioaccumulation-based guidelines, bioaccumulation studies, food chain modelling, and tissue residue guidelines to evaluate the direct toxicity and upper food chain effects of these compounds. 6.3.3. Risk characterization The risk characterization integrates the exposure and effect characterization to assess whether chemical concentrations are sufficiently high to pose unacceptable risks to ecolocigal receptors. It should be emphasized that this SLERA, where possible, incorporated conservatism where uncertainities were apparent, which is typical for a screening analysis (i.e. risks are likely to be overestimated rather than underestimated). This allows for chemicals posing negligible risk to be confidently removed from further evaluations. The chemicals indentified as being of potential concern (COPCs) have to be evaluated further in more detailed site-specific assessement to further characterize the risks they pose (Khairy, 2008)(226). In the present study, risk was characterized by compring the maximum concentration of each metal with its corresponding sediment quality guidelines (Table 32). The selected approach was the hazard quotient (HQ). The detailed approach used to evaluate the investigated contaminants in the SLERA is shown in Figure 53. Two HQs were calculated for each pollutant; TEC HQ, which was calculated by dividing the maximum concentration of each pollutant by the calculated consensus-based TEC (CBSQGTEC) and the PEC HQ, which was calculated by dividing the maximum concentration of each pollutant by the calculated consensus-based PEC (CBSQGPEC) (Figure 53). When TEC HQ < 1 for a given pollutant, rare adverse ecological effects are expected to occur with respect to this pollutant, when PEC HQ > 1, frequent adverse ecological effects are expected to occur and when TEC HQ > 1 > PEC HQ, adverse ecological effects are possible but less frequent than the previous level (Figure 53). -216- Table 32: Summary of the effect concentration levels from different SQGs applied in the SERA of the Egyptian Mediterranean coast Extreme effect Threshold effect concentration Probable effect concentration Trace Max. conc. concentrations metal present study ERL TEL T20 TECذ ERM PEL AET-L T50 PECa AET-H T80 EECa Cd 0.47 1.20 0.680 0.380 0.700 9.60 4.21 2.70 1.40 3.50 14.0 4.90 8.30 Cr 297.95 81.0 52.3 49.0 59.2 370 160 97.0 140 168 1101 410 672 Cu 26.26 34.0 18.7 32.0 27.3 270 108 390 94.0 181 1300 280 603 Pb 53.67 46.7 30.2 30.0 34.8 218 112 430 94.0 177 1200 300 600 Ni 60.25 20.9 15.9 15.0 17.1 51.6 42.8 110 47.0 58.1 371 150 236 Zn 62.21 150 124 94.0 121 410 271 460 240 333 3800 640 1560 a: Calculated consensus based SQGs for each group calculated according to MacDonald et al. (2000)(503) ERL, ERM (Long et al., 1995)(199) TEL, PEL (MacDonald et al., 1996)(510) T20, T50 and T80 (USEPA/NOAA, 2005)(593) AET-L, AET-H (Barrick et al., 1988)(592) -217- TEC HQ = concentration of the pollutant CBSQGTEC PEC HQ = concentration of the pollutant CBSQGPEC TEC HQ <1 TEC HQ >1> PEC HQ Possible but less frequent effects Rare effects PEC HQ >1 Frequent effects Use labile fraction Stop TEC HQ <1 Stop TEC HQ >1> PEC HQ Contaminants of potential concern (less concern) PEC HQ >1 Contaminants of potential concern (max. concern) Figure 53: SLERA approach applied in the Egyptian Mediterranean coast -218- Trace metals were further evaluated by calculating both HQs (TEC HQ and PEC HQ) based on the concentration of the labile fraction (the sum of the first 4 fractions obtained from the sequential extraction scheme). Calculated HQs for the investigated trace metals in the study area are shown in Figure 54. TEC HQ based on the total metal concentrations for Cd, Cu and Zn was less than 1 indicating rare effects. While, TEC HQ for Cr, Pb and Ni were higher than 1 based the total metals concentrations; indicating frequent adverse ecological effects are expected to occur. At the same time, the TEC HQ for Pb based on the labile fraction was in the range (TEC HQ > 1 > PEC HQ) indicating that adverse ecological effects are possible but less frequent with respect to Pb. While the TEC HQ for Ni and Cr based on the labile fraction concentration was TEC HQ < 1 indicating rare effects (Stop). Based on the calculated values of PEC HQ (Figure 54), it can be recognized that the calculated PEC value for Pb was (TEC HQ>1>PEC HQ). Thus it can be concluded that Pb considered as contaminant of less potential concern. Trace metals (TEC HQ) 6 5 4 Total Labile 3 2 1 0 Cd Cr Cu Pb Ni Zn Trace metals (PEC HQ) 2 1.5 Total Labile 1 0.5 0 Cd Cr Cu Pb Ni Zn Figure 54: TEC HQ and PEC HQ for trace metals in the Egyptian Mediterranean coastal sediments Evaluation of the adverse ecological risk usually includes the calculated HQ based on the maximum concentrations in the first stage, followed by determining the number of samples exceeding the used quality guidelines to determine contaminants of potential concern in a given area. Maximum detected TEC HQ and PEC HQ, together with the percentage of samples exceeding TEC and PEC level are given in Table 33. The maximum calculated PEC HQ for Cr and Ni was represented about 15% of the total samples. -219- 6.3.4. Area of special concern based on the conducted SLERA One of the principle goals of conducting this screening level ERA was the identification of sites of special concern in the study area due to the occurrence of the different investigated pollutants. The application of the HQ methodology is appropriate for the screening level assessment and may provide a good visualization tool or risk indicator for sites. The HQ was estimated by means of the two approaches considered in the present study (TEC HQ and PEC HQ). Calculated values of PEC HQ for each pollutant in the investigated sediment samples are shown in Table 34. It can be observed that the highest risk for adverse ecological effects (PEC HQ>1) from sediments was located at Rashid east, El-Gamil west and Port Said for Chromium. Also, the results revealed highest risk for adverse ecological effects due to Ni was found at Rashid east, Ras El-Barr and El-Gamil west. -220- Table 33: Summary of the information obtained from the risk characterization process for pollutants in sediments of the Egyptian Mediterranean Coast. Trace metal Cd Cu Cr Zn Ni Pb Metal type Total Labile Total Labile Total Labile Total Labile Total Labile Total Labile Max. PEC HQ 297.95 1.87 60.25 4.75 - Location of the max. PEC HQ Rashid east El-Gamil west - % of exceedance of PEC HQ 0% 0% 0% 0% 15% 0% 0% 0% 15% 0% 0% 0% -221- Max. TEC HQ Location of the max. TEC HQ 297.95 1.87 60.25 4.75 53.67 44.29 Rashid east El-Gamil west El-Mex Bay % of exceedance of TEC HQ 0% 0% 0% 0% 50% 0% 0% 0% 55% 0% 5% 5% Table 34: The calculated PEC HQ of the Egyptian Mediterranean Coastal sediments. Region Western region Middle region Eastern region Station 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 Cd 0.08 0.02 0.02 0.10 0.05 0.13 0.13 0.11 0.05 0.11 0.13 0.04 0.03 0.07 0.01 0.01 0.04 0.04 0.01 0.05 Cu 0.08 0.00 0.00 0.05 0.04 0.02 0.15 0.06 0.03 0.02 0.03 0.02 0.04 0.05 0.07 0.10 0.04 0.07 0.06 0.01 Cr 0.19 0.02 0.03 0.10 0.14 0.04 0.15 0.06 0.51 0.20 0.18 0.50 1.77 0.70 0.47 0.61 1.39 0.67 1.69 0.43 Zn 0.12 0.01 0.03 0.07 0.17 0.02 0.19 0.06 0.05 0.03 0.04 0.03 0.07 0.05 0.08 0.09 0.06 0.08 0.09 0.01 Ni 0.13 0.03 0.16 0.15 0.10 0.06 0.15 0.05 0.33 0.31 0.20 0.63 0.97 0.75 0.76 0.97 1.04 0.84 0.82 0.48 Pb 0.09 0.02 0.08 0.09 0.30 0.11 0.17 0.14 0.05 0.07 0.04 0.03 0.04 0.03 0.05 0.04 0.04 0.04 0.04 0.02 6.3.5. The Potential Ecological Risk Index method Potential Ecological Risk Index Method is simple, relative shortcut and precise (Hong et al., 2004)(600), not only reflects the single impact of heavy metals to ecological environment but also takes into accounts the different background values of the geography (Xin et al., 2008)(601) and combines environmental chemistry with biological toxicology and ecology (Guo et al., 2010)(602). In the present study, Hakanson's ecological risk method was used to evaluate the potential ecological risk of metal contaminants in sediments. In 1980, Lars Hakanson's reported an ecological risk index for aquatic pollution control; therefore, Hakanson's method has been often used in ecological risk assessment as a diagnostic tool to penetrate one of many possible avenues towards a potential ecological risk. The method is based on the hypothesis that a sediment ecological risk index for toxic substances should account for the following requirements: (1) the potential ecological risk index (RI) increases with the metal pollution increase in sediments; (2) the ecological harms of different heavy metals in sediments have cooperatively, and the potential ecological risk of the cooperative harm is more serious, especially for Cu, Zn, Pb, Cd, and Cr; and (3) toxicity response of each heavy metal is different, and those metals whose biologic toxicity are strong have larger proportion in RI The index is calculated as the following equations: Cif = CiD / CiR ; Efi = Tif x Cif ; CH = Cif RI = Eif -222- In which, Cif is the pollution coefficient of single metal; CiD is the measured concentration of sample; CiR is the background concentration of sediments; CH is the polluted coefficient of many metals; Eif is the potential ecological risk factor of single metal; Tif is the biological toxicity factor of different metals; and RI is the potential ecological risk index of many metals. The highest pre-industrial background concentration of global sediments is selected as the reference concentration in this study, Cd= 1, Cr=90, Cu=50, Pb=70, and Zn=175 µg g-1. The formula reveals the hazards of trace metals on the human and aquatic ecosystem and reflects the level of heavy metal toxicity and ecological sensitivity to the heavy metal pollution. The standardized response coefficient for the toxicity of trace metals, which made by Hakanson (1980)(517), was adopted to be evaluation criterion, the corresponding coefficients based on its toxicity were: Cd=30, Cu= Pb=Ni = 5, Cr=2, Zn=1 (Qinna et al., 2005)(603). According to Hakanson's ecological risk index method, the trace metal polluted elements in the present sediment samples are analyzed and evaluated. Only five polluted elements (Cu, Pb, Zn, Cd, and Cr) are investigated, which are less than eight elements required for Hakanson's method. Therefore, the integrated pollution degree (CH) is defined as following: CH<5, low pollution; 5≤CH<10, middle-pollution; 10≤CH<20, high pollution; CH ≥20, very highe pollution. As shown in Table 34, the results of pollution index and integrated pollution index indicated low pollution for the studied metals (Cd, Cr, Cu, Pb and Zn) in all the sampling sites. Table 35: Pollution index, integrated pollution index and pollution grade in sediments along the Egyptian Mediterranean coastal area Station 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 Cd 0.29 0.07 0.06 0.35 0.16 0.47 0.44 0.38 0.19 0.39 0.45 0.14 0.09 0.23 0.04 0.05 0.15 0.13 0.04 0.18 Pollution index Cif Cr Cu Pb 0.35 0.28 0.23 0.05 0.01 0.06 0.06 0.02 0.21 0.18 0.19 0.23 0.26 0.15 0.77 0.08 0.08 0.29 0.28 0.53 0.43 0.10 0.22 0.35 0.95 0.11 0.14 0.38 0.06 0.17 0.34 0.10 0.10 0.93 0.07 0.07 3.31 0.14 0.09 1.30 0.20 0.08 0.88 0.24 0.13 1.14 0.35 0.10 2.6 0.15 0.09 1.24 0.24 0.11 3.16 0.23 0.10 0.80 0.03 0.05 Zn 0.22 0.01 0.05 0.13 0.28 0.04 0.36 0.11 0.09 0.06 0.08 0.06 0.14 0.10 0.15 0.17 0.11 0.15 0.17 0.01 -223- Integrated pollution Integrated index CH pollution grade GG 1.37 Low pollution 0.20 Low pollution 0.40 Low pollution 1.08 Low pollution 1.62 Low pollution 0.96 Low pollution 2.03 Low pollution 1.17 Low pollution 1.48 Low pollution 1.06 Low pollution 1.07 Low pollution 1.27 Low pollution 3.78 Low pollution 1.91 Low pollution 1.43 Low pollution 1.80 Low pollution 3.09 Low pollution 1.87 Low pollution 3.70 Low pollution 1.08 Low pollution The pollution degree and potential ecological risk are analyzed by the use of potential ecological risk index method (Puente et al., 2008)(604). The evaluated standards for the analyzing potential ecological risk factor (Eif) and potential ecological RI are given in Table 36. Table 36:.Relation between RI and pollution levels Potential ecological risk factor Eif Threshold range of single metal risk factor grade Potential ecological risk index RI Threshold range of five metals RI grade < 30 30-60 60-120 120-240 >240 < 110 110-220 220-440 > 440 I Low II Middle III appreciable IV high V serious A Low B middle C appreciable D High The evaluation of potential risk of trace metal associated within the sediments along the Egyptian Mediterranean coastal area are summarized in Table 37. The potential ecological risk factor (Eif) of Cd, Cr, Cu, Pb, and Zn were lower than 30, which indicated slight potential ecological risk of all five metals in the studied stations. According to the evaluating standards, all the stations of the study area had RI ranged from 2.68 to 18.91 (<110), implicating a low ecological risk levels. Table 37: Evaluation on potential risk of trace metal pollution in sediments along the Egyptian Mediterranean costal area Station 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 Cd 8.61 2.22 1.92 10.38 4.83 14.07 13.23 11.49 5.70 11.73 13.41 4.26 2.76 6.96 1.05 1.50 4.47 3.78 1.29 5.43 Potential ecological risk factor Eif Cr Cu Pb 0.70 1.39 1.17 0.09 0.05 0.32 0.12 0.09 1.05 0.36 0.97 1.14 0.52 0.73 3.85 0.16 0.41 1.45 0.56 2.63 2.14 0.21 1.09 1.75 1.90 0.57 0.68 0.75 0.30 0.86 0.68 0.49 0.49 1.87 0.34 0.33 6.62 0.71 0.46 2.60 0.99 0.41 1.76 1.20 0.63 2.27 1.73 0.50 5.19 0.73 0.46 2.49 1.20 0.56 6.32 1.14 0.48 1.61 0.16 0.24 -224- Zn 0.22 0.01 0.05 0.13 0.28 0.04 0.36 0.11 0.09 0.06 0.08 0.06 0.14 0.10 0.15 0.17 0.11 0.15 0.17 0.01 RI 12.09 2.68 3.23 12.98 10.21 16.13 18.91 14.66 8.94 13.70 15.16 6.86 10.69 11.06 4.79 6.17 10.96 8.18 9.39 7.45 Risk grade Low Low Low Low Low Low Low Low Low Low Low Low Low Low Low Low Low Low Low Low 6.4. Multivariate Statistical analyses To assess the dynamics of trace metals and identify the contributing sources of bioavailable trace metals in the surfacial sediments along the Egyptian Mediterranean coastal area, multivariate statistical analyses such as factor and cluster analyses were carried out. 6.4.1. Application of principle component analysis (PCA) Principal component analysis (PCA), a multivariate statistical technique, is generally employed to reduce the dimensionality of a dataset while attempting to preserve the relationships present in the original data. The PCA enables a reductions in data and description of a given multidimensional system by means of a small number of new variables (Loska and Wiechula, 2003)(605). Principal component analysis is one of the multivariate statistical analytical tools used to assess metal behaviour in sediments (Zhou et al., 2004)(606), and it is applied to detect the hidden structure and association of elements in the data set, in an attempt to explain the influence of latent factors on the data distribution (Simeonov et al., 2000)(607). The Eigenvalues and Eigenvectors were computed for the standardized data using a specialized statistical software package (SPSS for windows version 17). The results of the principal component analysis (PCA) on the data matrix obtained from total trace metals analysis of surfacial sediments along the Egyptian Mediterranean coastal area are shown in Table 38. Three principal components were obtained with Eigen values greater than 1, together explaining more than 80.49% of total variance of the data, and the variances of Factor1, Factor2 and Factor3 are 46.020%, 21.269% and 13.202% respectively. Apparently the result of PCA corresponds well with the correlation coefficients. Factor 1 has strong loadings of Ni, Fe, Co, Mn and Cr; correlation coefficients among this group of elements exceed 0.7 (0.953, 0.920, 0.905, 0.888 and 0.831, respectively). Cobalt, Ni and Cr belong to the siderophile elements, and are main rocks forming elements. It is easy for them to enter into iron magnesium silicate minerals, because of their similar ionic radius. This element association is considered to represent the lithology of the study area, and a natural input, i.e., they are derived from terrigenous detrital material transported by surface runoff. Factor 2 indicated significant loadings in favour of Zn and Cu (0.875 and 0.858 respectively). These metals were believed to have the same sources. The impact of trace metals occurs over a finite period of time, and many have been effectively retained in the sediments near their sources, rather than resuspended and distributed uniformly throughout the study area. Factor 3, is strongly loaded with the textural parameters (sand and Mud), which are inversely related to each other. This factor contributes 13.202% of the total variance and may be termed as "Textural Factor". Principal component analysis was used on the data matrix obtained from leachable trace metals analysis of surfacial sediments along the Egyptian Mediterranean Coastal area to quatify relationships between variables under simultaneous condition of their interactions and the results were reported in Table 39. In this way, the number of variables under investigation was reduced and interelement associations might be assessed in detail (Bakac, 2000)(608). Results showed that two components (with Eigen values >1) were extracted describing approximately 80.655% of the common variance. To interpreat a group of variables to be associated with a particular factor, loadings greater than 0.7 were considered. The first factor describes 46.216% of the common variance and is positively loaded by LPb, although negative loading of LCo, LNi, LFe and LMn is also observed. The second factor, describing -225- 34.439% of the common variance of the data set, is positively loaded by LCr and negatively loaded by LCd. The PCA of the metals in the five binding fractions were applied. In the case of exchangeable fraction (F1), three components have been extracted, they accounted for 75.554% of the variance in the original data. Factor 1 has high negative association of Cr (-0.850) and Zn (-0.758), while Factor 2 were negatively associated with Mn (-0.596) and Factor 3 was positively associated with Ni (0.726) and negatively associated with Fe (-0.304) (Table 40). The principal component analysis of carbonate Fraction (F2) was shown in Table 41. Two components have been extracted, together they accounted for 65.111% of the variability in the original data. The factor 1 was positively associated with Zn (0.831) and Pb (0.774) and negatively associated with Mn (-0.692) and Fe (-0.650), while the Factor 2 was negatively associated with Cr (-0.732). The PCA was applied on the results of trace metals associated with the Fe/Mn oxide fraction (F3). Two components have Eignevalues were greater than 1, accounted for a cumulative variance of 86.143% (Table 42). Factor 1 represent 51.194% of the data variance was associated with Zn (0.986), Cr (0.927) and Pb (0.920). Factor 2 represented 34.949% of the variance was associated with Ni (0.901) and Fe (0.883) and negatively associated with Zn (-0.012), Cr (-0.094) and Pb (-0.226). The plot of loading of the components in the organic fraction (F4) gives a distribution of the metals into two components (Table 43). Factor 1 was associated with Fe (0.970), Ni (0.952), Mn (0.948) and Cr (0.907). Factor 2 of this fraction was positively associated with Pb (0.903) and Zn (0.822) and negatively associated with Fe (-0.082), Ni (-0.194), Mn (-0.025) and Cr (-0.042). The application of PCA on the data of trace metals binding to the residual fraction (F5) (Table 44) explaining only the first two components (82.981% of the variance). The factor 1 of this fraction represented 63.104% of the variance and was positively associated with Mn (0.952), Cr (0.916), Fe (0.914) and Ni (0.873), while factor 2 (19.878% of the variance) was positively associated with Zn (0.719) and negatively associated with Mn, Cr and Ni (-0.121, -0.274, -0.362, respectively). 6.4.2. Cluster analysis Cluster analysis was used in order to clarify the pattern of metal distributions in the sediments of the selected area. Classification was performed using (MINITAB 14 for windows). Cluster analysis can be used in combination with other statistical techniques in order to assess epidemiological relationships between variables and outcomes. Cluster analysis refers to a set of techniques designed to classify observations so that members of the resulting groups are similar to each other and distinct from the other groups. Hierachical clustering, which successively joins the most similar observations, is the most common approach. Because groups are simply based on their similarity to each other, hierarchical cluster analysis can be useful when abundant data are available and clear hydrogeologic models have not yet been developed. While other multivariate techniques, such as factor analysis or principal component analysis, provide more insight into the underlying structure of a data set, the use of these techniques might require further analyses to identify distinct groups. Cluster -226- analysis, on the other hand, may be thought of as a useful way of objectively organizing a large data set into groups on the basis of a given set of characteristics. This can ultimately assist in the recognition of potentially meaningful patterns. The set of characteristics chosen for inclusion in the cluster analysis is assumed to include the important distinguishing characteristics of the entities that are being clustered. It is recommended that the simplest characteristics applicable to the data set be chosen because this is likely to ease interpretation of the final results (Swanson et al., 2001)(609). Cluster analysis provides a number of methods to obtain an insight into data sets, and to extract relevant information from them. This analysis is the most important tool used for interpreting multivariate data containing objects and features, and sometimes also properties. Cluster analysis generically refers to different multivariate methods designed to creat homogeneous sets of objects called cluster (Debska and Wianowska, 2002)(610). The basic principal upon which all clusters analyses are based is very simple. All of them attempt to group samples or objects into groups of similar objects called clusters. Objects are placed into different clusters such that members of any other cluster are more similar to each other in some way than that they are to members of any cluster. The major problem associated with cluster analysis is that the techniques always produce clusters even in circumistances where there are no natural groupings in the data. The analysis actually imposes a cluster structure on the data. The success of the method will depend entirely on knowing whether the clusters produced are real ones or simply artifacts of the method (Hagan and Fellowes, 2003)(611). Figure 55 depicts a dendogram drived by group average methods and Squared Euclidean of twenty sites based on all the parameters (Trace metals: Fe, Mn, Zn, Cu, Pb, Cr, Co, Ni; Organic matter, Carbonate, Mud and Sand) in surfacial sediments along the Egyptian Mediterranean coastal area. The cluster analysis results indicate six clusters: (1) Pb-Zn-Cu; (2) TOM-CaCO3; (3) Cd; (4) Ni-Mn-Fe-Co-Cr; (5) Mud; (6) Sand in terms of similarities. This indicates that Ni, Mn, Fe, Co, and Cr appear to have originated mainly from natural sources. In addition, Pb, Zn and Cu seem to drive partly from sources other than Ni, Mn, Fe, Co and Cr. Cluster analysis allows the grouping of sampling sites on the basis of the similarities of trace metals (Sundaray et al., 2011)(612). This analysis for metals concentrations is rendered as dendogram (Figure 56), where 20 sampling sites of the surfacial sediments along the Egyptian Mediterranean Coastal area are clustered into two groups depending upon the enrichment of metals. The sites in groups have similar characteristics features and anthropogenic/natural background source types. The first major grouping is formed by the most stations from the western region (1, 4, 9, 11, 8, 7, 5, and 10), the Middle region (12, 13, 17, 14, 18, 15, and 16) and station 19 in the eastern region. The most relevant in this study is the second group, formed by the four stations 20, 2, 3, and 6. -227- Table 38: Factor loadings on elements in surfacial sediments samples along the Egyptian Mediterranean coastal area (n=20) Element Factor 1 Factor 2 Factor 3 Ni 0.953 0.036 0.034 Fe 0.920 0.268 0.136 Co 0.905 0.188 0.151 Mn 0.888 0.155 0.181 Cr 0.831 0.059 0.005 CaCO3 -0.824 -0.009 0.267 Cd -0.649 0.114 0.072 TOM -0.625 0.169 0.382 Pb -0.583 0.415 0.436 Zn -0.055 0.875 0.366 Cu 0.114 0.858 0.329 Sand 0.202 -0.675 0.702 Mud -0.202 0.675 -0.702 Eigenvalue 5.983 2.765 1.716 % variance explained 46.020 21.269 13.202 Cumulative % variance 46.020 67.290 80.491 Table 39: Factor loadings on leachable metals in surfacial sediments samples along the Egyptian Mediterranean coastal area (n=20) Element Factor 1 Factor 2 L Pb 0.801 0.522 LCo -0.799 0.557 LNi -0.767 0.609 LFe -0.696 0.684 LZn 0.675 0.661 LCu 0.651 0.636 LCd 0.478 -0.065 LCr 0.641 0.705 LMn -0.537 0.578 Eigenvalue 4.159 3.099 % variance explained 46.216 34.439 Cumulative % variance 46.216 80.655 -228- Table 40: Factor loadings of variable (5 metals) using PCA technique of the data set in the Exchangeable fraction of the surfacial sediments along the Egyptian Mediterranean coastal area. Element Cr Zn Pb Fe Mn Ni Eigenvalue % variance explained Cumulative % variance Factor 1 -0.850 -0.758 0.610 0.468 0.479 0.510 2.377 39.622 39.622 Factor 2 0.193 0.275 0.501 0.640 -0.596 0.103 1.139 18.977 58.598 Factor 3 0.163 0.486 0.239 -0.304 0.277 0.726 1.017 16.955 75.553 Table 41: Factor loadings of variable (5 metals) using PCA technique of the data set in the Carbonate fraction of the surfacial sediments along the Egyptian Mediterranean coastal area. Element Zn Pb Mn Fe Cr Ni Eigenvalue % variance explained Cumulative % variance Factor 1 0.831 0.774 -0.692 -0.650 0.418 0.470 2.587 43.122 43.122 Factor 2 0.03 0.408 0.404 0.108 -0.732 0.664 1.319 21.989 65.112 Table 42: Factor loadings of variable (5 metals) using PCA technique of the data set in the Fe/MN oxides fraction of the surfacial sediments along the Egyptian Mediterranean coastal area. Element Zn Cr Pb Ni Fe Mn Eigenvalue % variance explained Cumulative % variance Factor 1 0.986 0.927 0.920 -0.314 0.360 0.407 2.587 43.122 43.122 -229- Factor 2 -0.012 -0.094 -0.226 0.901 0.883 0.668 1.319 21.989 65.112 Table 43: Factor loadings of variable (5 metals) using PCA technique of the data set in the Organic fraction of the surfacial sediments along the Egyptian Mediterranean coastal area. Element Fe Ni Mn Cr Pb Zn Eigenvalue % variance explained Cumulative % variance Factor 1 0.970 0.952 0.948 0.907 0.023 0.370 3.704 61.740 61.740 Factor 2 -0.082 -0.194 -0.025 -0.042 0.903 0.822 1.538 25.634 87.373 Table 44: Factor loadings of variable (5 metals) using PCA technique of the data set in the Residual fraction of the surfacial sediments along the Egyptian Mediterranean coastal area. Element Mn Cr Fe Ni Zn Pb Eigenvalue % variance explained Cumulative % variance Factor 1 0.952 0.916 0.914 0.873 0.443 0.497 3.786 63.104 63.104 -230- Factor 2 -0.121 -0.274 0.032 -0.362 0.917 0.674 1.193 19.878 82.981 Similarity 59.78 73.19 86.59 100.00 Pb Zn Cu TOM CaCO3 Cd Ni Mn Fe Co Cr Mud Sand Variables Figure 55: Cluster analysis of the selected trace metals in the surfacial sediments along the Egyptian Mediterranean coastal area Similarity 99.94 99.96 99.98 100.00 1 12 13 19 17 14 18 15 16 4 9 11 8 Variables 7 5 10 20 2 3 6 Figure 56: Dendogram showing station groups formed by group averaging cluster analysis of elemental concentrations -231- 6.4.3. Correlation matrix Pearson Correlation (PC) matrix for analysed sediment parameters was calculated to see if some of the parameters were interrelated with each other and the results are presented in Table 45. Examination of the matrix also provides clues about the carrier substances and the chemical association of trace metals in the study area (Forstner and Witlmann, 1983)(613). The correlation matrixes of the metal contents, the sand fraction, calcium carbonate (CaCO3) and organic matter content (OM) in the surface sediments of the study area are given in Table 45. The correlation matrixes show the differences in the inter-relationships between sediment properties in the study area, which may relate to either compositional differences or process variability between the areas. The data presented in Figure 57 showed that strong positive correlation exists between Fe and (Mn, Co, Cr, and Ni) (r = 0.92, 0.96, 0.69, and 0.85 respectively). It means that these metals tend to accumulate together. The significantly positive correlation with Fe indicates that the elements were derived from similar sources and also moving together (Bhuiyan et al., 2009)(614). There is a negative correlation between Fe and Pb (r = -0.3918). This result is in agreement with the results of Sohrabi et al. (2010)(615). This result suggested that Pb was not strongly controlled by natural weathering processing (Zhang et al., 2009)(530). The strong positive correlation exists between Zn and (Cu and Pb) (r = 0.80 and 0.63 respectively) Figures (58 and 59 respectively). Also, Cr shows strong positive correlation with (Ni, Fe, Mn, and Co), where (r = 0.83, 0.69, 0.79 and 0.60, respectively) Figures (62, 57, 60 and 61 respectively). The data show that strong positive correlation exists between Ni and (Fe, Mn, Cr, and Co) (r =0.85, 0.78, 0.83 and 0.86, respectively) Figures (57 and 62). It means that Ni strongly coupled with these metals. On the other hand it shows high negative correlation with TCO3 (r = -0.81) indicating that Ni does not found in carbonate form, and negative correlation with Pb and Cd (r = -0.48 and -0.59). Carbonate gives negative correlation with most of the studied metals except Pb and Cd (r = 0.56 and 0.39) and no correlation with Zn, and cupper (r= 0.10 and 0.007). There were positive correlation between TOM and Cd (r= 0.49) whereas Pb had low association with total organic matter with low positive correlation (r= 0.373). This results are in agreement with Sohrabi et al. (2010)(615). Organic matter shows moderate positive correlation with Cd where (r = 0.49). On the other hand it shows negative correlation with Ni, Fe, Mn, Co, and Cr (r= 0.54, -0.46, -0.40, -0.45 and -0.51). This negative correlation may indicate that these metals are not associated with organic matter. -232- Table 45: Correlation matrix between heavy metals, CaCO3 and OM in sediments (n=20) along the Egyptian Mediterranean coast from Salloum to Rafah (n= 20) Zn Ni Pb Cd Fe Cu Mn Co Cr CaCO3 OM Zn 1 Ni -0.0079 1 Pb 0.6621* -0.5335 1 Cd 0.0620 -0.5954 0.3227 Fe 0.1850 0.8515* -0.3918 -0.5549 0.1710 0.2673 1 Mn 0.1074 0.7839* -0.4026 -0.4166 0.9198* 0.2652 1 Co 0.1159 0.8644* -0.4253 -0.5660 0.9627* 0.3426 0.8414 Cr 0.0580 0.8316* -0.4092 -0.4983 0.6919* 0.0925 0.7892* 0.6011* CaCO3 0.1011 -0.808 0.5666 0.3911 -0.683 0.0067 -0.675 -0.686 -0.647 1 OM 0.2122 -0.537 0.3732 0.4907 -0.455 0.2452 -0.403 -0.446 -0.505 0.5803 Note: * is significant at P< 0.05 -233- 0.1410 1 0.3887 Cu 0.8029* 1 1 1 1 Manganese 1200 1000 800 600 400 200 0 R = 0.9195 Cobalt 0 10000 20000 Iron 30 25 20 15 10 5 0 30000 40000 R = 0.9627 0 10000 20000 Iron 30000 40000 Chromium 400 300 200 100 R = 0.6918 0 0 10000 20000 Iron 30000 40000 40000 Iron 30000 20000 10000 R = 0.8512 0 0 20 40 Nickel 60 80 Figure 57: Relationship between Fe and Mn, Co, Cr, Ni -234- Cupper 30 25 20 15 10 5 0 R = 0.8028 0 20 40 Zinc 60 80 Lead Figure 58: Relationship between Zn and Cu 60 50 40 30 20 10 0 R= 0.6621 0 20 40 Zinc 60 80 1200 1000 800 600 400 200 0 R = 0.7892 0 100 200 Chromium 300 400 Figure 60: Relashionship between Mn and Cr Cobalt Manganese Figure 59: Relationship between Zn and Pb 30 25 20 15 10 5 0 R = 0.6011 0 100 200 300 400 Chromium Figure 61: Relationship between Co and Cr -235- Chromium 400 300 200 100 R = 0.8316 0 Manganese 0 20 40 Nickel 60 1200 1000 800 600 400 200 0 80 R = 0.7839 0 20 40 60 80 Nickel 30 Cobalt 25 20 15 10 5 R = 0.8644 0 0 10 20 30 40 50 60 Nickel Figure 62: Relationship between Ni and Cr, Mn, Co -236- 70 Statistical analyses based on acid leachable elements were effectively utilized for the interpretation of geochemical processes of heavy metals (Jonathan et al., 2004; Selvaraj et al., 2004; Jayaprakash et al., 2008)(467, 616, 617). The correlation coefficients among acid leachable trace metals and sediment properties in the Egyptian Mediterranean coastal area are listed in Table 46. From the obtained results iron showed postitive correlation with Co (r= 0.94), and Ni (r=0.98), indicating that acid leachable Co and Ni are mainly combined with Fe oxyhydroxides but not Mn oxyhydroxides. The acid leachabel contents of Ni, Fe, Mn, and Co are negatively correlated with OM (r= -0.36, -0.29, -0.26, and -0.40, respectively), on the other hand Zn, Pb, Cd, and Cr, showed low positive correlation with OM (r= 0.15, 0.29, 0.18, and 0.37, respectively), which indicates that the organic matter is not the important factors controlling the potential perniciousness of trace metals in the sediment. Acid leachable Ni, Fe, Mn and Co are negatively correlated with CaCO3, (r=-0.56, -0.48, -0.32, and -0.58), which indicates that these metals are hardly combined with carbonates. Acid leachable Zn, Pb, Cd, Cu, and Cr have a relatively low positive correlation with CaCO3 (r=0.33, 0.53, 0.28, 0.49, and 0.46, respectively) indicating that these metals may be combined with CaCO3. The behaviour of the six trace metals (Fe, Mn, Zn, Ni, Cr and Pb) in the sedimentary five fractions could be known by performing correlation matrix (Tables 47-52). As shown in Table 47 high correlation between total Fe and both organic bounded Fe (r=0.861) and residual Fe (r=0.978). Moderate correlation was found between Fe bound to oxides and Total Fe and Organic iron (r=0.611 and 0.750 respectively). It is clear from Table 48 that total Mn correlates significantly with exchangeable Mn fraction (r=0.701), Mn bound to carbonate fraction (r=0.769), and Residual Mn (r=0.936). Significant correlation was obsereved between exchangeable Mn and Mn bound to carbonate (r=0.845) and exchangeable Mn and Mn bound to organic fraction (r=0.799). Mn bound to carbonate was found to be significantly related to Mn bound to organic fraction (r=0.830). The results of correlation coefficient matrix between chemical characteristics and different species of Zn metal (Table 49) showed that significant correlation observed between total Zn and Carbonate Zn (r=0.619), Zn bound to oxides (r= 0.652), Organic Zn (r=0.831) and residual Zn (r=0.915). Zn bound to carbonate fraction was observed to be significantly correlated with Zn bounded to Fe/Mn oxides fraction (r=0.937) and Zn bound to organic fraction (r=0.743). There was significant correlation between Zn bounded to Fe/Mn oxides and Zn bound to organic fraction (r=0.791). Finally Zn bounded to organic was significantly correlated with the residual Zn (r=0.640). Table 50 showed that significant correlation found between Total Ni and Ni bound to Fe/Mn oxides (r=0.757), Ni bounded to organic fraction (r=0.712), and residual Ni (r=0.9680. Also, Ni bounded to Fe-Mn oxides was significantly correlated with Ni bounded to organic fraction (r=0.978). Total Cr was significantly correlated with residual Cr (r=0.993) (Table 51). Finally, Table 52 showed that total Pb was significantly correlated with both carbonate fraction (r=0.891) and Fe/Mn oxides fraction (r=0.963). Pb bounded to Carbonate fraction was significantly correlated with Fe/Mn oxides (r=0.805), while Pb bounded to Fe/Mn was significantly correlated to Pb bounded to organic fraction (r= 0.716). Bird et al. (2005)(618) have suggested that anthropogenically sourced metals preferentially partitioned to the non residual phase of the sediment, and that the residual phase generally reflects background geochemical conditions. -237- Table 46: Correlation matrix between leachable trace metals, CaCO3 and OM in sediments from Salloum to Rafah (n=20) Zn Ni Pb Cd Fe Cu Mn Co Cr CaCO3 Zn 1 Ni -0.1195 1 Pb 0.9535** -0.3022 1 Cd 0.1546 -0.3666 0.2539 1 Fe -0.0521 0.9809** -0.2240 -0.2686 1 Cu 0.7515* -0.1187 0.7717* 0.3065 0.0116 1 Mn 0.0252 0.6682* -0.1123 -0.1466 0.7126* 0.0007 1 Co -0.1699 0.9716** -0.3509 -0.4012 0.9443** -0.1774 0.6623* 1 Cr 0.8659* -0.0448 0.8354* 0.2105 0.0370 0.8764* -0.0248 -0.0975 1 CaCO3 0.3337 -0.568 0.5278 0.2481 -0.487 0.4921 -0.322 -0.586 0.4594 1 OM 0.1529 -0.36 0.2881 0.1867 -0.294 0.5335 -0.26 -0.404 0.3704 0.5803 Note: * is significant at P< 0.05 ** is significant at P< 0.01 -238- OM 1 Table 47: Correlation coefficient matrix between chemical characteristics and different species of Iron T Fe F1. F2 F3 F4 F5 %TOM CaCO3 T Fe 1.000 F1 0.300 1.000 F2 0.308 0.150 1.000 F3 0.611* -0.152 -0.059 1.000 F4 0.861** 0.047 0.176 0.750* 1.000 F5 0.978** 0.304 0.382 0.572 0.870** 1.000 TOM -0.455 -0.326 -0.137 0.086 -0.370 -0.475 1.000 CaCO3 -0.683 -0.370 -0.532 -0.113 -0.579 -0.725 0.580 1.000 Table 48: Correlation coefficient matrix between chemical characteristics and different species of Manganese. T Mn F1 F2 F3 F4 F5 %TOM CaCO3 T Mn 1.000 F1 0.701* 1.000 F2 0.769* 0.845** 1.000 F3 0.203 0.230 0.474 1.000 F4 0.769* 0.799* 0.830** 0.556 1.000 F5 0.936** 0.621 0.585 -0.125 0.575 1.000 TOM -0.403 -0.480 -0.362 0.012 -0.273 -0.413 1.000 CaCO3 -0.675 -0.664 -0.564 0.038 -0.433 -0.702 0.580 1.000 Table 49: Correlation coefficient matrix between chemical characteristics and different species of Zinc. T Zn F1 F2 F3 F4 F5 %TOM CaCO3 T Zn 1.000 F1 0.362 1.000 F2 0.619* 0.245 1.000 F3 0.652* 0.192 0.937** 1.000 F4 0.831** -0.030 0.743* 0.791* 1.000 F5 0.915** 0.396 0.333 0.336 0.640* 1.000 TOM 0.212 0.160 0.555 0.472 0.313 0.157 1.000 CaCO3 0.101 0.212 0.571 0.594 0.254 -0.142 0.580 Note: * is significant at P< 0.05 ** is significant at P< 0.01 -239- 1.000 Table 50: Correlation coefficient matrix between chemical characteristics and different species of Nickel. T Ni F1 F2 F3 F4 F5 %TOM CaCO3 T Ni 1.000 F1 0.165 1.000 F2 -0.181 0.060 1.000 F3 0.757* 0.412 -0.105 1.000 F4 0.712* 0.404 -0.076 0.978** 1.000 F5 0.968** 0.040 -0.204 0.577 0.523 1.000 TOM -0.537 -0.006 0.143 -0.368 -0.374 -0.536 1.000 CaCO3 -0.808 0.113 0.273 -0.569 -0.595 -0.793 0.580 1.000 Table 51: Correlation coefficient matrix between chemical characteristics and different species of Chromium. T Cr F1 F2 F3 F4 F5 %TOM CaCO3 T Cr 1.000 F1 -0.251 1.000 F2 -0.379 -0.001 1.000 F3 -0.350 -0.107 0.558 1.000 F4 0.371 -0.232 -0.331 -0.104 1.000 F5 0.993** -0.264 -0.400 -0.383 0.408 1.000 TOM -0.505 -0.154 0.401 0.557 -0.148 -0.529 1.000 CaCO3 -0.647 0.050 0.538 0.665 -0.574 -0.677 0.580 1.000 Table 52: Correlation coefficient matrix between chemical characteristics and different species of Lead. TPb F1 F2 F3 F4 F5 %TOM CaCO3 TPb 1.000 F1 0.033 1.000 F2 0.891** 0.130 1.000 F3 0.963** -0.011 0.805** 1.000 F4 0.655* -0.220 0.386 0.716* 1.000 F5 -0.052 0.022 -0.326 -0.110 0.173 1.000 TOM 0.373 0.001 0.091 0.444 0.321 0.060 1.000 CaCO3 0.567 -0.259 0.426 0.651 0.371 -0.355 0.580 Note: * is significant at P< 0.05 ** is significant at P< 0.01 -240- 1.000 Chapter VII Summary The coastal zone of Egypt on the Mediterranean Sea extends from Rafah in the eastern region to El-Salloum in the western region for over 1200 km. It hosts a number of important residential and economic centers, like the cities of Alexandria, Matruh, Rosetta, Damietta, Port Said and Al-Arish. It also hosts five large lakes, namely Bardawil, Manzala, Burullus, Edku and Maryut which represents about 25% in area of the total wetland of the Mediterranean. Many activities are known in the coastal areas including fishing, industrial, tourism, trading and agricultural, oil and gas production, and transportation. The main objective was to study the concentration and distribution of some trace metals in the surfacial sediments along the Egyptian Mediterranean coast and to evaluate the contamination degree and the potential ecological risk for the selected metals. To achieve this objective, twenty surfacial sediment samples were collected from selected stations along the coastal area from El-Salloum to Rafah during July 2010. The study area was divided into three regions as follows: western region, located in the western area of the coast represented by 11 stations from El-Salloum to El-Maadia. The middle region, located in the Delta area of the coast represented by 7 stations from Rashid west to ElGamil west and the eastern region, represented by 2 stations from Port Said to Rafah. The samples were collected and placed into sealed polyethylene bags. Separate samples were collected at the same time for the measurement of SEM/AVS. Samples were collected in such a manner that exposure to atmospheric O2 is minimized, or sulfides will be oxidized. Several ecological assessment methods were applied (total and leachable concentration, sequential extraction, and AVS/SEM) to assess the trace metals (Fe, Mn, Cr, Ni, Zn, Pb, Cu, Co and Cd) pollution and potential biotoxicity in sediments from the Egyptian Mediterraean coast. The interrelationship and corresponding relationships of different evaluation methods were also discussed. The obtained results can be summarized as follows: A- Geochemical analysis Grain size analysis was performed on twenty sediment samples collected from the study area. Results showed that fine sand and very fine sand were the dominated fractions of all sediment samples. The range and average of sand were 86.85 to 100% (93.43%). The highest value of sand content (100%) was observed at Nobareya, El-Mex, Western harbour, Rashid west and Rafah. While the lowest value (86.85%) was observed at El-Salloum. The range and average of total organic matter (TOM) in the surface sediments of the study area were found to vary from 0.08 to 1.72 (0.56 ± 0.43%). The highest value was observed at NIOF (western region) and the lowest value was observed at Rashid west (middle region). The Egyptian Mediterranean coast contains a wide variety of sediments. Coastal sediments are mainly composed of two principal types: carbonate and quartze dominant sand. The concentration of total carbonate in the sediment samples of the investigated area ranged between 2.85 to 95.57%, with an average (37.78 ± 39.65%). The study area was divided into three regions, which revealed differences in the distribution of CaCO3. The western region, -241- where sediments at El-Salloum are characterized by relatively medium CaCO3 percentage (34.97%) while sediments from Baghoush to the Eastern harbour (west of Alexandria) are characterized by high percentage of CaCO3 ranged from (67.24%) at El-Mex Bay to a maximum percentage (95.57%) at the western harbour. On the other hand the region east of Alexandria characterized by relatively low % of CaCO3 (14.69, 15.69 and 22.11%) at electrical power station, Maadia and Abu Qir, respectively. There was a relatively low percentage of CaCO3 in the Middle region ranged from 2.85% at Rashid west to 6.08% at New Damietta and the Eastern region 6.33% at Rafah and 7.32% at Port Said. B- Trace metal Distribution I - Total trace metals distribution The distribution of the total trace metals (Fe, Mn, Cr, Ni, Zn, Pb, Cu, Co and Cd) of sediments along the Egyptian Mediterranean coastal area was studied. The range and average ± SD concentrations (µgg-1) were 243.48–38045.05 (13255.69± 12911.36) for Fe, 17.251085.72 (380.71 ±305.38) for Mn, 4.08-297.95 (82.74 ±90.18) for Cr, 1.65-60.25 (25.93 ±20.96) for Ni, 2.05-62.21 (22.19 ±15.84) for Zn, 3.34-53.67 (13.17 ±11.90) for Pb, 0.4626.26 (8.46 ±6.22) for Cu, 0.43-26.39 (8.24 ±8.40) for Co, 0.04-0.47 (0.22 ±0.15) for Cd. The level of trace metals can be arranged as the following: Fe> Mn> Cr> Ni> Zn> Pb> Cu> Co> Cd. The lowest value of Fe, Zn, Cu, Ni, Cr and Co (243.48, 2.05, 0.46, 1.65, 82.74 and 0.43 µgg-1, respectively) observed at Baghoush, while Mn, Pb and Cd showed a minimum concentration value (17.25, 3.34 and 0.04µgg-1) at El-Nobarreya, Rafah and Port Said, respectively. On the other hand, the highest content of Fe, Mn, Ni, Cr, Co, Pb and Cd; 38045, 1085.72, 60.25, 297.95, 26.39, 53.67 and 0.47 µgg-1, respectively observed at New Damietta, Port Said, El-Gamil west, Rashid east, Ras El-Barr, El-Mex and Western harbor, respectively. The concentration of Zn (62.21µgg-1) and Cu (26.26µgg-1) was found to be high at NIOF. The distribution of Fe, Mn, Ni and Co, among the three regions of the study area was similar and arranged as the following: Middle region > Eastern region > Western region. While the distribution of Zn, Pb and Cd are also similar and arranged as the following: Western region > Middle region> Eastern region. Cupper was distributed among the three regions of the study area as the following: Middle region > Western region > Eastern reigon. The distribution of Chromium was different than the other metals and its distribution among the different regions of the study area as the following: Eastern region> Middle region> Western region Assessment of pollution impact 1- Sediment quality guidelines - The magnitude and ecological relevance of metal pollution in the surfacial sediments along the Egyptian Mediterranean coastal area was investigated by applying different sediment quality approaches. - Based on the SQGs proposed by USEPA, sediments were categorized into three classes: unpolluted, moderately polluted and heavily polluted. - Accordingly, the concentration of Cd and Zn at all stations under investigation was belonged to unpolluted sediments. - The concentration of Cr at El-Salloum, NIOF, Electric power station, Maadia and Rafah was moderately polluted, while the stations at Abu Qir, Rashid west, Rashid -242- east, Burullus, New Damietta, Ras El-Barr, El-Gamil west and Port Said were heavily polluted. - Sediment at all stations was classified as unpolluted with cupper except NIOF station which was moderately polluted. - The concentration of Fe at El-Gamil stations was moderately polluted, while Rashid east, Burullus, New Damietta, Ras El-Barr and Port Said were highly polluted. Pb at all stations was belonged to unpolluted except El-Mex Bay which was moderately polluted. - It was noted that the concentration of Ni at Rashid west, Burullus, New Damietta, ElGamil east, Port Said and Rafah was belonged to moderately polluted sediments, while Ni at Rashid east, Ras El-Barr and El-Gamil west was belonged to heavily polluted. - The concentration of Mn at the Eastern harbour, Electric power station, El-Gamil east and El-Gamil west was moderately polluted, while Rashid east, Burullus, New Damietta, Ras El-Barr and Port Said was heavily polluted. 2- Enrichment factor - The computed metal EF range in the surface sediments of the Egyptian Mediterranean coastal area showed that the EF of trace metals (Cd, Co, Cr, Cu, Mn, Ni, Pb, Zn) were: (0.22 to 74.03), (0.61 to 10.50), (1.18 to 28.99), (0.32 to 6.78), (0.86 to 8.04), (0.62 to 26.99), (0.40 to 114.22), and (0.29 to 14.77), respectively. - The calculated EF was found Cd>Pb>Cr>Ni>Mn>Zn>Co>Cu. - Despite the high EF for almost all the studied metals in the sediments of the western region at Baghoush, Nobarreya, El-Dikhaila, El-Mex, Western harbour, NIOF and the Eastern harbour and Rafah Station at the eastern region. There seems to be not even moderate pollution of metals in these sediments. This leads to incorrect results due to the naturally lower concentration of Fe at these stations (243.48, 277.34, 3946.02, 3565.22, 1527.85, 4813.8, 3440.82 and 1422.39 respectively) which may lead to higher EF of trace metals. For this reason we used Igeo index too. to fall in the following sequence: 3- Geoaccumulation load Index Results showed that the Igeo values for Zn, Mn, Ni, Fe, Cu and Co fall in class "zero" (unpolluted) at all the sampling locations indicating that there is no pollution from these metals. The Igeo value for Pb fall in class " zero" (unpolluted) at almost all the sampling location except El-Mex Bay and NIOF which fall in class "1" (unpolluted to moderately polluted). The Igeo value for Cd fall in class "zero" (unpolluted) at almost all locations except El-Salloum, El-Dikhaila, Western harbour, NIOF, Eastern harbour, Electrical power stations and Maadia falls in class "1" (unpolluted to moderately polluted). The Igeo value for Cr fall in class "zero" (unpolluted) at all stations of the western region except stations 13 and 17 in (Rashid east, El-Gamil east) at the middle region and station 19 in Port Said at the eastern region were classified as "moderately polluted". -243- 4- Contamination factor and modified degree of contamination: - The calculated CF was found to fall in the following sequence: Cd (1.27) >Cr (1.15) >Pb (0.70)>Co (0.59) >Ni (0.50)>Mn (0.49)>Fe (0.32) >Cu (0.26)>Zn (0.23). - The contamination factors values are low for Zn, Cu and Fe at all sampling sites and between low and moderate for Ni, Cd, Mn and Co and finally, between low and considerable contamination for Cr. - Modified degree of contamination (mDc) was found to be less than 1.5 indicating sediments along the Egyptian Mediterranean coast classified from zero to very low contamination. 5- Pollution load index - The Results of PLI were less than 1 at all the studied locations indicating only baseline levels of pollutants present. - PLI values of the analyzed samples ranged from 0.04 at Baghoush and 0.72 at Port Said with an average 0.61. In general, there is an increase of PLI toward the eastern region. II- Leachable trace metals The range and average concentrations (µgg-1) were: 94-6831 (1930±1777) for Fe, 10.83-307.27 (126±81) for Mn, 0.55-8.21 (2.61±2.01) for Cr, 0.15-11.16 (3.04±3.23) for Ni, 0.11-49.48 (7.40±10.94) for Zn, 0.54-51.35 (8.13±11.97) for Pb, 0.22-8.20 (2.19±2.29) for Cu, 0.09-8.77 (2.34±2.82) for Co, 0.02-0.23 (0.06±0.05) for Cd. Leachable Iron: Results showed that the % of LFe ranged between (6.68 to 69.46%) with an average (22.83%). The maximum % of LFe (69.46%) was found at Baghoush in the western region which has high % of calcium carbonate (94.45%) and the minimum percentage (6.68%) of LFe was found at Rafah in the eastern region. The low percentage of LFe in most cases (average: 22.832%) may be due to the increased contribution of the lattice-held fraction of the metal. This reflects low bioavailability of Fe. Leachable Manganese: Data showed that the range and average of LMn % was (3.66-91.67; 48.03). The highest % of LMn (91.67%) was observed at El-Mex Bay (western region) while the lowest % of LMn (3.66 %) was observed at Rashid east (Middle region). The high percentage of weakly bound Mn (>50%) observed at almost all stations of the western region are probably due to the elevated association of Mn with carbonate that are dissolved by the dilute HCl. The relatively low % of LMn in the Middle (27.82%) and the eastern region (35.47%) indicated that manganese is tightly bound to the sediment minerals. Leachable Zinc: The % of LZn ranged between 1.159 and 89.27 (average: 30.15%). The lowest value observed at Nobarreya while the highest value observed at El-Mex Bay. There was a relatively high percentage of Zn (43.35%) associated with the non residual fraction (leachable) at the western region. While the Middle and the Eastern region showed relatively low % of leachable Zn (15.46 and 8.95%, respectively) reflecting the natural background of this element in the Middle and the Eastern region. Leachable Copper: Cupper exhibited LCu ranged between 8.92 and 86.46% (average: 29.17%). The lowest % of LCu was observed at Abu Qir Bay while the highest value found -244- at El-Mex Bay. The antifouling paints used for ships and boats are regarded as one of the important sources, which increased the level of copper in El-Mex Bay. Relatively high % of LCu (> 30%) was observed at Baghoush, Nobarreya, Dekhaila, El-Mex, Western harbor, NIOF, Eastern harbor and Electric power station in the western region. While, relatively low percentage of the non residual Cu observed at stations of the Middle and the Eastern region 13.48% and 16.59%, respectively. Leachable Lead: The LPb % ranged from 12.01 to 95.68% (average: 45.23%). The high % found at El-Mex Bay, while the lowest value found at El-Gamil east. The high extractability percentage of Pb reported at El-Mex Bay indicated a new input in El-Mex Bay, which was probably due to the domestic, industrial effluents and the atmospheric deposition. Relatively low percentage (<30%) of Pb (19.87% and 27.78) was extracted at the non residual fraction (leachable) in the Eastern and the Middle region. Leachable Cadmium: The results showed that LCd % ranged between 11.63 and 86% (average: 37.25%). The lowest value observed at Maadia while the highest % observed at Ras El-Barr. Cadmium showed relatively high % of LCd in the Middle region (average: 45.39%). Cd is contained in some phosphate based fertilizers and petroleum. Such sources could constitute a major source of Cd that may reach humans. In additions, sewage sludge from wastewater treatment may contain significant quantities of Cd. Relatively high percentage of Cd was observed in the residual form in the Western and the Eastern region (>60%), reflecting the natural background of this element in these regions. Leachable Chromium: The LCr % ranged between 0.42 and 61.35% (average: 13.61%). The highest value observed at Baghoush while the lowest value observed at El-Gamil west. The western region showed relatively high percentage of LCr (61.35, 35.42 and 42.27%) at Baghoush, El-Mex Bay and the Eastern harbour, respectively. On the other hand, it exhibited a relatively low % of LCr ranged from 0.42 to 3.56 % (average: 1.51%) at the middle region and from 0.96 to 1.04 (average: 1.00%) at the eastern region, reflecting the low Cr mobility in the study area. Leachable Cobalt: The results showed that the value of LCo ranged between 5.34 and 45.935 (average: 25.63%). The highest value found at the Electric power station and the lowest value observed at Port Said. Relatively low % of LCo was found at most of the stations not exceeding 30%. Leachable Nickel: The % of LNi ranged between 0.55 and 28.83% (average: 13.55%) at the western region, and from 4.49 to 25.20% (average: 12.07%) at the middle region and from 0.55 to 14.17% (average: 7.36%) at the eastern region. The highest value found at Maadia while the lowest value found at Rafah. The relatively low % of LNi (<20%) at most of locations reflects the natural background of Ni in the investigated area. III- Fractionation of trace metals In the present work, fractionation of Fe, Mn, Cr, Ni, Zn and Pb into the different chemical forms (Exchangeable, Carbonate, Fe-Mn oxides, Organic and Residual fraction) has been conducted in order to demonstrate in which forms these metals are chemically chelated, as well as to differentiate between the residual metals (natural background) and non residual ones (man made sources of pollution). Exchangeable fraction The exchangeable metal in sediments is labile, highly toxic and the most bioavailable. The results showed that the exchangeable bound fraction for trace metals (Fe, Mn, Zn, Ni, Cr -245- and Pb) in surfacial sediments along the Egyptian Mediterranean coast was comparatively low, (ND-0.04%), (0.01-0.32%), (ND -3.84%), (0.09-9.35%), (0.01-2.79%) and (0.246.64%), respectively suggesting lower pollution risk and the relatively low mobility of these elemests. Carbonate fraction The range and average percentage of carbonate fraction were: 0.82-54.51 (13.90%) for Pb; 0.87-18.82 (8.83%) for Mn; 0.2-14.89 (3.79%) for Zn and 0.03-12.17 (1.75%) for Cr and only small fraction 0.54-5.30 (0.07%) and 0.02-2.64 (0.81%) for Fe and Ni, respectively. Lead showed appreciable concentration (14.30, 14.93, 45.63, 54.40, 54.51 and 22.60%) in the carbonate fraction at (El-Salloum, Bagoush, Nobarreya, El-Mex Bay, Western harbour and NIOF, respectively) in the western region which characterized by high CaCO3 contents (34.79, 94.45, 95.49, 67.24, 95.57 and 91.64%). This reveals that calcite has a strong affinity for Pb. This also may be attributed to the similarity of its ionic radii to that of calcium in the carbonate crystal lattic to form a mixed carbonate phase. On the other hand, manganese was found in relatively moderate amounts (>10%) (18.82, 11.91, 11.35, 13.53, 15.11, 13.04 and 17.81%) at Maadia, new Damietta, Ras El-Barr, El-Gamil west, El-Gamil east, Port Sail and Rafah, respectively. This may be attributed to anthropogenic inputs. Fe/Mn oxide fraction The range and average percentage of Fe/Mn oxide fraction were: 2.29-87.31 (43.08%) for Mn; 4.92-49.83 (12.32%) for Pb; 1.22-67.26 (18.24%) 1.75-25.38 (10.32%) for Ni; 1.8240.45 (12.24%) for Fe; 0.22-37.34 (8.14%) for Cr. More than 65% of Mn was found to be associated with Fe-Mn oxides in the western region suggesting, that hydrous Fe-Mn oxides may play a major role in controlling the fate and transport of Mn in this region. Moderate amounts of Pb were found binding to Fe-Mn oxide (average: 33.80, 21.47 and 15.18%) in the the study area which has been proved to be sensitive to anthropogenic inputs. Finally, moderately amounts (average: 27.75%) of Zn bounded to the Fe-Mn fraction. was found in the western region. Organic fraction The range and average percentage organic fraction were: 2.34-13.85 (7.42%) (5.79%) for Zn; 0.22-22.97% (6.91%) for (4.52%) for Pb were bounded to organic benthic biota. of percentage of trace metals bounded to the for Fe; 0.91-6.72 (3.75%) for Mn; 0.03-13.01 Ni; 0.48-17.98 (3.61%) for Cr and 2.68-17.25 matter and sulfide, contributed low toxicity to Residual fraction Residual phase of metals are generally much less toxic for organisms in aquatic environment. The results of residual fraction in the surfacial sediments along the Egyptian Mediterranena coast was dominanted. The range and average percentage of the residual fraction were: 39.14-99.20 (86.17%) for Cr; 51-35-95.52 (80.27%) for Fe 50.92-97.90 (80.05%) for Ni and 9.32-97.14 (71.70%) for Zn. This reflects the natural background of Ni, Fe, Cr and Zn in the investigated area. The highest concentration of residual fraction was reported for Mn (71.64 and 64.55%, respectively) and for Pb(67.47 and 57.17%) in the Middle and the Eastern region. This indicates that Mn and Pb are tightly bound to the sediment minerals in the Middle and the eastern region and are not easily released to the environment. Risk assessment code - Risk assessment code has been used to assess environmental risks and estimate possible damage to benthic organisms caused by contaminated sediments. -246- - - From the present study, The range and average values of the exchangeable and carbonate-bound fractions of Cr, Fe, Mn, Ni, Pb, and Zn were: 0.04-12.58 (average: 2.08%)for Cr; 0.005-0.342 (average: 0.068%) for Fe; 0.087-18.96 (average: 8.95%) for Mn; 0.14-10.88 (average: 2.72%) for Ni; 4.32-55.43 (average: 16.82%) for Pb and 0.26-15.27 (average: 4.26%) for Zn. This suggests that Fe has no risk to local environment; Cr, Mn, Ni, and Zn have posed low risk to local environment while Pb was at Medium risk level. V- Acid volatile sulfides and simultaneously extractable metals - Acid volatile sulfide (AVS) is one of the major chemical components that control the activities and availability of metals in the interstitial waters of sediments. Sulfide reacts with several divalent transition metal cations (Cd, Cu, Ni, Pb and Zn) to form highly insoluble compounds that are not bioavailable. - The average concentration of SEM in the three regions can be arranged as follows: western region (0.13±0.07µmoleg-1) > Middle region (0.08±0.04µmoleg-1)> eastern region (0.05±0.05µmoleg-1). - The average value of AVS in the different regions can be arranged as follows: western region (3.31±9.35µmoleg-1)> Eastern region (0.07±0.06µmoleg-1)> Middle region (0.06±0.03µmoleg-1). - The use of different relationships between AVS and SEM to establish mechanical model such as the ratio of SEM and AVS (SEM/AVS), the difference between SEM and AVS (SEM-AVS) or the organic carbon normalized difference between SEM and AVS (SEM-AVS/fOC) to assess metal toxicity has been applied in this study. - According to SEM/AVS model: Western Harbour, Eastern Harbour, Ras El-Barr, ElGamil East, and Port Said are occasionally toxic while the other stations are not toxic. - According to SEM-AVS model: stations at El-Salloum, Nobarreya, El-Dikhaila, ElMex, NIOF, Abu Qir, El-Gamil east and Rafah showed no indication of associated adverse effects, while at the western harbour, eastern harbour, electrical power station, Maadia, Rashid, east and Rashid west, Burullus, New Damietta, Ras El-Barr, ElGamil east and Port Said associated adverse effects on aquatic life are possible. - Organic carbon normalized difference (SEM-AVS/fOC) showed that sediments should pose a low risk of adverse biological effects due to Cd, Cu, Pb, Ni and Zn at all sampling stations C- The Screening level Ecological Risk Assessment: The output of the SLERA (based on the consensus approach) revealed that: - TEC HQ based on the total metal concentrations for Cd, Cu and Zn was less than 1 indicating rare effects. While, TEC HQ for Cr, Pb and Ni were higher than 1 based on the total metals concentrations; indicating frequent adverse ecological effects are expected to occur. - TEC HQ for Pb based on the labile fraction was in the range (TEC HQ > 1 > PEC HQ) indicating that adverse ecological effects are possible but less frequent with respect to Pb. While the TEC HQ for Ni and Cr based on the labile fraction concentration was TEC HQ < 1 indicating rare effects (Stop). -247- - Based on the calculated values of PEC HQ, it can be recognized that the calculated PEC value for Pb was (TEC HQ>1>PEC HQ). Thus it can be concluded that Pb considered as contaminant of less potential concern. D- The potential ecological risk The potential ecological risk indices (Eif) of Cd, Cr, Cu, Pb, and Zn were lower than 30, which indicated slight potential ecological risk of all five metals in the studied stations. According to the evaluating standards, all the stations of the study area had low ecological risk levels (RI <110). E- Multivariate Statistical analyses - To assess the dynamics of trace metals and identify the contributing sources of bioavailable trace metals in the surfacial sediments along the Egyptian Mediterranean coastal area, multivariate statistical analyses such as principal component, cluster analysis and correlation matrix coefficient were carried out. - Data showed that strong positive correlation exists between Fe and (Mn, Co, Cr, and Ni) (r = 0.92, 0.96, 0.69, and 0.85, respectively). It means that these metals tend to accumulate together. The significantly positive correlation with Fe indicates that the elements were derived from similar sources and also moving together. - There is a negative correlation between Fe and Pb (r = -0.3918) suggested that Pb was not strongly controlled by natural weathering processing. - There was a strong positive correlation exists between Zn and (Cu and Pb) (r = 0.80 and 0.63 respectively). These metals were believed to have the same sources which differ from the sources of Fe, Co, Ni, Cr, and Mn. - The obtained results are in agreement with the results of the cluster analysis and the principle component analysis. -248- Conclusion - Information of this study reported for the first time for the surfacial sediments of the Egyptian Mediterranean Sea, constitute a baseline of metals speciation, AVS and SEM in sediments and a reference for future studies on the changes of labile and residual metal fractions over time. - Sediments are important hosts for trace metals and such should be included in environmental monitoring programs. - The distribution of Fe, Mn, Ni and Co, among the three regions of the study area was similar and arranged as the following: Middle region> Eastern region> Western region. While, the distribution of Zn, Pb, Cd are also similar and arranged as the following: Western region> Middle region> Eastern region. Copper was distributed among the three regions of the study area as the following: Middle region> Western region> Eastern reigon. The distribution of chromium was different from the other elements and its distribution among the different regions of the study area as the follwoing: Eastern region> Middle region> Western region. - Different metal assessment indexes were used and their applicability to interpreat the pollution status was discussed. The potential ecological risk indices of Cd, Cr, Cu, Pb and Zn, indicated slight potential ecological risk of these metals. The calculated modified degree of contamination was less than 1.5 indicating zero to very low contamination. - The application of EF as a tool for estimating the anthropogenic impact on sediments is not an appropriate tool where a relatively low natural Fe concentration exists as it will gives incorrect higher values of EF. - Application of the geochemical accumulation index may lead to more realistic results in comparison with EF in sediments of the study area as low Fe content of sediments in almost all stations of the western region and station 20 (Rafah) in the eastern region. - Relationships between metal speciation and total metals concentrations reflected the stability of the metals, it can be arranged in the order of: Cr> Fe> Ni> Zn> Pb> Mn. - Results of single acid extraction method (Leachable) was in agreement with the results of sequential extraction procedure for (Fe, Cr, Mn, Zn, Pb and Ni): - The single extraction procedure using 1 N HCl (leachable metals) was an easy, simple, cheap and quick procedure that provides an accurate data base of the availability of metals in any aquatic environment which are often readily available to organisms affecting them directly. On the other hand, it does not differentiate between the non residual fractions (exchangeable, carbonate, Fe/Mn oxides, Organic) and residual fraction, as it can be obtained from the results of sequential extraction procedure. - Sequential extraction procedure should be used to better differentiate the form of Fe, Mn, Cr, Zn, Ni and Pb. These fractions play an important role in controlling the fate and transport of metals in the sediment. - Determination of the total concentration of a metal in sediment is not a particularly useful indicator of sediment toxicity, as it does not distinguish between the natural and anthropogenic components of the metal. This is supported by the finding obtained by comparing the results with SQG proposed by USEPA and the obtained results of sequential extraction procedure. - According to SQG proposed by USEPA the concentration of Cr, Fe, Ni was moderately polluted to highly polluted. While according to RAC, these metals posed no risk to local environmet. -249- - The acid volatile sulfide (AVS) levels in the Egyptian Mediterranean Sea sediments revealed wide variation. It varied from 0.015 to 31.33 µmoleg-1, which is in agreement with the values reported for samples from the US and Canada. - The values of SEM/AVS at the western Harbour, Eastern Harbour, Ras El-Burr, El-Gamil East, and Port Said are occasionally toxic while the other stations are not toxic. - According to SEM-AVS model: stations at El-Salloum, Nobarreya, El-Dikhaila, El-Mex, NIOF, Abu Qir, El-Gamil east and Rafah showed no indication of associated adverse effects, while associated adverse effects on aquatic life are possible at the western harbour, eastern harbour, electrical power station, Maadia, Rashid, east and Rashid west, Burullus, New Damietta, Ras El-Barr, El-Gamil east and Port Said. - Results showed that [SEM-AVS]/fOC < 130 µmoleg-1 at all the sampling sites revealing that sediments posed a low risk of adverse biological effects due to Cd, Cu, Pb, Ni and Zn at all stations. - The output of the SLERA (based on the consensus approach) revealed that rare negative effects are possible due to Cd, Cu, Cr, Ni and Zn. And lead was considered as a contamint of less potential concern. Recommendations - Information of this study constitutes a baseline of metals speciation, AVS and SEM in sediments and should be used as a reference for future studies on the changes of labile and residual metal fractions over time. - The application of EF as a tool for estimating the anthropogenic impact on sediments is not an appropriate tool where a relatively low natural Fe concentration exists as it will gives incorrect higher values of EF. - Application of the geochemical accumulation index (Igeo) may lead to more realistic results in comparison with EF in sediments of lower natural Fe content. - AVS/SEM models and sequential extraction procedure accompanied with measuring the total metal concentration should be included when evaluating the environmental risk of trace metals in sediments. - The capabilities of national institutions to carry out marine pollution monitoring and research should be supported, developed and when necessary established to formulate and apply pollution control and abatement measures. - Commitment with the international agreement and the environmental laws. - Establishment of a Management Information System that stores all previous information and data which will help in future development, management and restoration of the Egyptian Mediterranean coastal zone - Monitoring systems for trace metals in fish, water and sediments in the study area. -250- References 1. 2. 3. 4. 5. 6. 7. 8. 9. 10. 11. 12. 13. 14. 15. 16. 17. 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