Download Research in crop production and turfgrass has identified grass

EXECUTIVE SUMMARY
Project Title: Development of Phosphorus Filtering Systems for Environmental Protection.
Principal Investigators: Chad J. Penn and Gregory E. Bell.
University:
Oklahoma State University
Address:
368 Ag Hall
Stillwater, OK 74078-6027
Telephone: 405-744-2746
Fax: 405-744-0354
e-mail: [email protected]
Project Justification: This project satisfies the request for research in Product Testing under the subcategories of 1)
new technology with limited information on turfgrass applications, 2) recycled materials, and 3) alternative
construction methods and materials.
Project Description: Based on research to date, turf inhibits runoff better than any other surface. Even some manmade materials specifically designed to reduce erosion do not inhibit runoff as well as turf (Krenitsky et al., 1998).
However, based on previous studies, runoff from turf cannot be entirely prevented and can potentially contain
unacceptable levels of nutrients and pesticides. Systems to test filtering materials, mostly waste products from
industrial operations, have been constructed or are under construction. Laboratory research has identified electrical
arc furnace steel slag as a waste product with extremely high potential as a phosphorus and heavy metal filter. Both
active and passive filtering mechanisms will be tested at our field research site and at Stillwater Country Club for
their use in field suppression of nutrient contamination in runoff and surface water. Following the work in this
proposal we expect to have all of the information necessary to use steel slag as the standard with which to compare
other potential materials as chemical filters.
How Ours is Different: The OSU Turfgrass Research Runoff Site is one of the best sites for plot-type runoff
research in the world. We have expertise in turfgrass runoff research and in the use of filtering materials and
additives to soil and water for the reduction of chemical contamination. We have a laboratory specifically designed
for this type of research and we have identified at least one working golf course for testing of design and materials.
A pond filter is in place at our turfgrass research site and a ditch filter is in place at Stillwater Country Club. The
OSU Turfgrass Runoff Site is being modified to accommodate this work and construction will be completed within
a few weeks of this proposal deadline. We have tested a number of waste materials for their efficacy at removing
chemical contamination, primarily phosphorus, from water and identified several with potential. If this work is
successful it will be immediately applicable for field use. This research will further demonstrate the USGA’s
continuing commitment to environmental quality. The OSU Turfgrass Research Team has demonstrated its
dependability by successful completion of previous projects. Everything that we need is already in place and we
have a great deal of experience in this area. We have a graduate student committed to our program to continue this
work in 2011 and beyond.
Potential Benefits: At the completion of the project we expect to have a thorough analysis and knowledge of steel
slag for use as a chemical filter in turfgrass systems. We will know the material’s attributes, its limitations, and its
effectiveness for use in multiple types of filtering systems. We will have developed a standard for comparison with
other potential filter materials and we will have adjusted and perfected our testing devices. If the studies are
successful, Golf Course Superintendent’s will have an immediate source of reference for construction of active and
passive filtering devices and a filter material that is suitable for use in those devices.
Deliverables:
1. Information and development of chemical filter systems for removal of contaminants in golf course runoff
and/or surface water.
2. Early development of systems and materials that will further reduce chemical contamination of surface waters.
3. At least one, probably two peer-reviewed publications in addition to professional articles in TERO, GCM, and
others.
Introduction:
Research in crop production and turfgrass has identified grass swards and grass buffer strips as
impediments to the transport of nutrients and pesticides in runoff (Bell and Moss, 2008). Dense grass swards have
unique characteristics that encourage water to infiltrate soil and impede and filter runoff (Easton et al., 2005).
Research has also demonstrated that the runoff-reduction characteristics that naturally occur in a grass sward are not
sufficient to prevent the substantial runoff caused by major storm events.
Easton et al. (2005) reported that the establishment of turfgrass on bare soil increased soil infiltration by
more than 65% over a two-year period. As shoot density increased, infiltration rate increased and runoff decreased.
Nonetheless, turfgrass sites can contribute to nutrient and pesticide losses to surface water in concentrations greater
than recommended.
Before and during a precipitation event, many factors combine to affect the volume of runoff that will
occur for any given precipitation rate on any given turfgrass stand. These factors include antecedent soil moisture
(Cole et al., 1997) relevant soil physical properties, (Linde et al., 1995), turfgrass species (Easton and Petrovic,
2004), turf density (Easton et al., 2005), and slope at the site (Walker and Branham, 1992). Once surface runoff
begins, flow is channeled through natural and artificial drainage into surface water features such as lakes, ponds, and
streams. An important environmental hazard caused by nutrient runoff is eutrophication (Daniel et al., 1998). Low
levels of nitrogen (N), mostly in the form of nitrate (NO3-), and dissolved reactive phosphorus (DRP), primarily
forms of phosphate (H2PO4-, HPO42-, and PO43-), can cause algal blooms resulting in a loss of oxygen in surface
water. This process is called eutrophication. Although N is a major factor in potential eutrophication, phosphorus
(P) is believed to be the most important contributor (Sharpley et al., 2000). Eutrophication is responsible for the
“dead zones” in the Mississippi Delta and Chesapeake Bay as well as numerous lakes and other water features
throughout the world. States have begun to pass legislation that restricts the application of P fertilizer to turfgrass
(Rosen and Horgan, 2005).
Fertilizers are important as a source of plant available P. Most inorganic fertilizers, however, are highly
soluble and if not properly applied, increase the risk of P loss to surface runoff (Bell and Moss, 2008). Phosphate-P
can contribute to eutrophication at concentrations as low as 25 µg L-1 (Burton, Jr. and Pitt, 2002) and is typically the
limiting factor for eutrophication of surface water (Sharpley et al., 2000).
Kunimatsu et al. (1999) studied the loading rates of nutrients discharged from a golf course in Japan.
Samples were taken from a stream that ran from a forested basin through the golf course. They found that an
increase in nutrient discharge from the stream was due primarily to the N, P and K applied to the golf course as
fertilizer. Mallin et al. (2002) found significant increases in nitrate, ammonium, total P, and DRP in the outflow of a
golf course pond compared with the inflow. However, appropriate modern golf course designs usually include
containment features that restrict off-site water transport and facilities for re-use of on-site water. A good design can
be very effective. Ryals et al. (1998) investigated three golf courses in North Carolina for nutrient and pesticide
contamination. They found chlorothalonil, chlorpyrifos, and 2,4D residues in on-course water features but all of the
pesticide detections were below environmental hazard levels. Although pesticides were found at each course none
of the outflows contained pesticides at detectable levels. The highest on-site nitrate concentration was 2 mg L-1 with
all other samples occurring below 0.7 mg L-1. On-site concentrations of P did not exceed 10 µg L-1 and averaged
0.09 µg L-1 at the course with the highest concentration. Kohler et al. (2004) in a 4-year study at Purdue
University’s Kampen Golf Course demonstrated that the construction of a golf course wetland could store and filter
runoff from the golf course and surrounding areas improving the quality of the water entering the course from the
surrounding watershed compared with the water quality exiting the course.
Although golf courses have been the focus of recent studies and professional turfgrass managers have been
criticized, most nutrient runoff from urban turfgrass may be the result of poor management by inexperienced
homeowners. A survey of landscape management practices in Georgia reported that three of four homeowners
managed their own landscaping and fully controlled fertilizer and pesticide applications (Varlamoff et al., 2001).
Although professional turfgrass managers receive training in application management, many homeowners do not. A
survey of four communities in North Carolina revealed that about 60% of the homeowners applied pesticides to their
lawns and that 78% of those calibrated their equipment prior to application (Osmond and Hardy, 2004). In contrast,
homeowners in these four communities plus one other could usually report the amount of fertilizer applied but rarely
could report the rate applied. Only 20% of the homeowners based their fertilization activities on soil tests and even
the lawn care companies used tended to fertilize during the wrong season for warm-season grasses. Clearly,
procedures for the management of nutrient runoff must be applicable and economically feasible for home lawns as
well as golf courses and other professionally managed systems.
Other than environmentally sound management, the most common practice specifically employed for
reducing nutrient runoff from crop production fields are grassed buffer strips, also called vegetative filter strips. The
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United States Department of Agriculture Natural Resources Conservation Service (USDA-NRCS) defines
conservation buffers as small areas or strips of land in permanent vegetation designed to intercept pollutants and
manage other environmental concerns (USDA-NRCS, 2000). Buffers may enhance fish and wildlife habitat,
improve or prevent further degradation of water quality, improve soil quality, reduce flooding, conserve energy, and
conserve biodiversity (USDA-NRCS, 2000). Grass vegetation is recommended for vegetative buffers or filter strips
(USDA-NRCS, 1997). Buffer performance has been widely studied in agricultural settings and has been effective
for reducing pesticide and nutrient losses from agricultural lands (Baker et al., 2000; Sharpley et al., 2000).
Cole et al. (1997) and Baird et al. (2000) using the same methods at the same site determined that a 1.5-in.
high bermudagrass buffer bordering a 0.5-in. bermudagrass stand was effective for reducing runoff and that a 3.0-in.
buffer was more effective than the 1.5-in. buffer. In a similar study Moss et al. (2005) determined that the effects of
grass buffers were enhanced by mowing them at increasingly higher heights. In all three of these studies however,
the P concentrations leaving the buffers were greater than those suspected to encourage eutrophication. Rice and
Horgan (2009) estimated that similar concentrations from a 25-acre site were sufficient to encourage eutrophication
in a 2.5 acre pond, 6 feet deep. Procedures to further reduce P concentrations in runoff from turfgrass and other
areas need to be considered.
Information from the United States Geological Survey (USGS) indicated that 80% of the P and 71% of the
N delivered to the Gulf of Mexico comes from agricultural sources (January 2008 numbers) with 12% P and 9% N
from urban areas. According to the Environmental Working Group, the “dead zone” in the Mississippi delta will
worsen unless agriculture reduces non-point source P pollution (www.ewg.org, Figure 1).
Figure 1. Pie charts (left) present the origin of N and P eluting into the Gulf of Mexico from the Mississippi River.
From: Environmental Working Group, www.ewg.org. Original information from the USGS.
We can probably assume that much of the nutrient runoff originating from urban areas comes from
hardscape (concrete, asphalt, brickwork, etc.). However, a significant amount also originates from turfgrass,
planting beds, and other vegetated areas. In addition, the use of grassed buffer strips to reduce P loading is
continually increasing but problem areas continue to expand. Golf courses incorporate the best type of buffer
management but are still likely to contain nutrient concentrations in runoff that exceed those believed to encourage
eutrophication (Moss et al., 2005). In fact, they are not always successful. In a recent study, Stier and Kussow
(2009) found that neither buffers of fine fescue nor prairie grasses were effective for reducing P loading to surface
water on a Wisconsin golf course. Further means appropriate for nutrient runoff reduction in turfgrass systems, golf
courses included, need to be studied or discovered. Unless we can reverse this P loading more laws will be passed
restricting P application and superintendents will no longer be in control of fertilization, one of their most important
management practices.
High levels of phosphate in inland waters have been reduced through the use of chemical amendments.
Chemical amendment usually involves an addition of alum or gypsum (precipitating phosphates as aluminum salts)
to surface waters. Application of P sorbing materials (PSMs), typically alum, will reduce dissolved reactive
phosphorus (DRP) concentrations in solution, thereby decreasing the potential for P to contribute to algal blooms
(Lind, 2002). For example, following alum addition to two sandpit lakes in the Platte River basin (Fremont, NE),
total P was reduced from >100 mg L-1 to <50 mg L-1 (Holz and Hoagland, 1999). Liquid alum additions have also
been shown to reduce soluble P in irrigation return flows (Leytem and Bjorneberg, 2005). A reduction in DRP
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losses in runoff and leaching can also be expected when PSMs are applied to high P soils (Elliott et al., 2002;
Rhoton and Bigham, 2005; Peters and Basta, 1996). Alum is often used to reduce phosphate concentrations in water
treatment facilities and their retention pools preventing severe algal blooms (Lind, 2002). Chemical treatment
provides for immediate reductions of excess phosphate runoff. However, over time such chemical treatment will
contribute to elevated background phosphate levels in surface waters as the phosphates slowly release from their
metal precipitates.
Most management practices such as vegetative buffer strips, target P transport by removing particulate P
from overland flow. Turfgrass, however, is already effective for sediment removal (Gross et al., 1990; Kaufman III
and Watschke, 2007). Removal of dissolved reactive phosphorus (DRP) presents more difficulty and requires P
sorbing materials (PSMs). Phosphorus sorbing materials typically contain aluminum (Al), iron (Fe), calcium (Ca),
and/or magnesium (Mg) that function to remove soluble P from solution by precipitation and/or adsorption. The byproducts of several industries such as flue de-sulfurization gypsum (FGD), steel slag, and drinking water treatment
residuals are potential PSMs . The application of a PSM to soils high in P has been successful for reducing DRP
concentrations in runoff and leachate (Penn and Bryant, 2006).
Directly amending surface water with a PSM can reduce bio-available P (Lind, 2002). However, the longterm stability of sorbed P following direct application of PSMs to surface waters is questionable. Like chemical
treatment, the total P within the system is not reduced (i.e. P is not truly removed; only shifted to a less soluble
form). Direct removal of P from surface waters is preferable. To address this problem, we have developed P
removal structures that are placed in hydrologically active areas such as drainage ditches in order to serve as large
landscape P filters (Penn et al., 2009). These structures are filled with PSMs that directly remove P from water
passing through them. This filtering process reduces the P concentration of water flowing from small watersheds,
(crop production fields, lawns, or golf facilities) into larger bodies of water. Depending on the chemical and
mineralogical make-up of PSMs from industrial processes, many will also have a strong affinity for heavy metals
and other contaminants.
A P removal structure constructed at the University of Maryland Eastern Shore utilized acid mine drainage
residuals from a coal mine reclamation site as a PSM. After rigorous laboratory testing and characterization, the
materials were deemed safe in regard to pH, heavy metals, sodium (Na), and total dissolved solids. Following the
laboratory testing a field structure was designed and constructed to capture runoff. (Fig. 2).
During the first flow event (tropical storm Ernesto) which deposited 12 in. of rainfall in 24 hr, DRP
concentrations in ditch flow reached a maximum of 15 mg L-1 P, of which nearly 100 percent was removed by the
structure. In addition, the materials contained in the structure also removed several heavy metals and some nitrogen
(Fig 2).
Figure 2. (a) Cross sectional diagram of the P removal
structure that is partially buried to accommodate the inlet
flume installed at the ditch bottom. The effluent pipe
discharges at a point downstream that allows for a 1% slope
from the effluent outlet. (b) Photo of the P removal structure.
(c) Dissolved metals, phosphorus, and total nitrogen sequestered from ditch water expressed as a percentage
removed from water entering the structure during a 24 h rainfall event.
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Two years after construction, the P removal structure was still very effective at reducing P and heavy
metals from agricultural ditch flow. A similar structure has been constructed at Stillwater Country Club, Stillwater
OK. In addition, a forced-flow filtering device was constructed for P removal from a pond at the Oklahoma State
University Botanical Garden and Turfgrass Research Center that has historically been susceptible to algal blooms
and a third system, a multiple plot system to test the filtering of drainage and runoff water, is under construction.
After several years of rigorous laboratory testing of potential PSMs we have identified several industrial
process waste products that demonstrate potential. Of those, steel slag appears to be the most promising. The
material is inexpensive and easily obtained. As we expand our testing program we will need a standard with which
to compare materials in the lab and in the field. We intend to use steel slag to fill that need. Consequently, the
material requires rigorous testing to determine its P sorption qualities, its handling characteristics, and its useful
lifespan.
In addition to testing materials for use in filtering P, we are also interested in determining approximately
how much P can be expected to occur from runoff from unfertilized turfgrass. In previous studies of P runoff at our
site and others it has been assumed that DRP in runoff was a result of P fertilizer. However, that may not be true.
There may be naturally occurring DRP that constitutes a major component of runoff. Recently, Bierman et al.,
(2010) experienced high P concentrations in runoff from plots that had not been fertilized. The researchers
attributed this high level to poor turfgrass quality during the second year of their study. In year 1 and year 3 P
concentrations were consistent with P applied as fertilizer. We too, have experienced highs and lows in P
concentrations in runoff that are difficult to explain. Perhaps there are variables such as bare soil exposure that are
prominent factors influencing P concentration in runoff. In that case, we may be able to further document the
environmental advantages of a dense turfgrass stand over competing plant systems.
The objectives of this study are to:
1. Test the steel slag material for its DRP-reduction potential in both active and passive filtering systems such
as:
a. Active filtering systems that pump water through containers of PSM for potential practical use in
pond, lake, or stream reclamation.
b. Passive stream and ditch filters for use in filtering surface water as it leaves one site (perhaps a
golf course) and enters another (perhaps a housing development).
c. Passive runoff and leachate collection systems for both surface and subsurface drainage where a
PSM is substituted for the gravel or sand layer that normally surrounds a drainage pipe to filter
DRP.
2. To determine approximately how much runoff P from a mature bermudagrass site is due to natural causes
(rainfall, soil, plant material) and how much can be attributed to synthetic fertilizer.
3. To identify standard expectations for use in evaluating PSMs.
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Materials and Methods
An active filtering system was constructed and installed on a pond at the Oklahoma State University
Turfgrass Research Center (Figure 3). Water is pumped from the pond, forced through a filter tank containing P
sorbing materials (PSMs), and returned to the pond. This structure is not meant to remediate the pond in regard to P,
instead, the role of this structure is to serve as a “testing ground” for assessing the effectiveness of potential PSMs.
Filter materials are not lost in the flow and are not distributed directly to the water body. The simple containment
structure allows filter materials to be conveniently removed and replaced with new or different products. The
convenience of the system and its close proximity to campus allow for frequent sample collection and constant
monitoring. The forced flow provides for a very accurate measure of the quantity of water passing through the
system and reliable estimates of the filtering potential and longevity of the product. When the system was installed
in 2008 the P concentration in the pond varied from 0.1 to 0.9 ppm, depending on season. During initial testing the
filter was filled with drinking water treatment residuals and run for 20 h per day until P saturation. The materials
removed 50% of the P added to the system during 140 h of flow. This particular structure will serve as a pilot scale
unit for testing potential PSMs such as steel slag.
Figure 3. The pond filter at the OSU Turfgrass
Research Center is housed in a small shed and
circulates pond water at approximately 2.25
gal/min.
A material that has shown promise for
removing P from passive overland flow is steel
slag. We obtained some electric arc furnace slag
from Ft. Smith Arkansas. This material was
sieved to ¼ inch in size and the > ¼ inch size
fraction was used in laboratory flow-through
experimentation. We will also use this material
in the pond filter (Figure 3) and a ditch filter
recently constructed at Stillwater Country Club,
Stillwater, OK (Figure 4).
This particular site receives runoff from both a portion of the golf course and a portion of the surrounding
residential area resulting in DRP concentrations > 1 ppm during storm flow. Runoff is captured in a large pond on
the course. The ditch containing the filter is an overflow for the pond. Water from the pond drains through the ditch
filter then off of the course into a residential drainage swale that empties into Stillwater Creek. Briefly, water is
channeled through a culvert into the 8 x 10 ft ditch filter which will be filled with slag to a depth of 8 inches (Figure
4). Water from the culvert infiltrates down through the sorbing material (i.e. slag) and treated water exits through a
4 inch pipe downstream. The system is constructed and automatic samplers and flow meters have been purchased
and installed to measure flow and sample water entering and exiting the filter. Water samples will be analyzed for
total DRP, inorganic P, nitrate, ammonium, trace metals, and pH. The ditch structure is in a highly visible location
at the Stillwater Country Club which should spark a great deal of interest in the project.
Figure 4.The ditch filter designed to capture and filter high phosphorus runoff from part of Stillwater Country Club
and part of the surrounding residential area. Slag will be placed into this structure to a depth of 8 inches.
5
A third testing system is under construction at the OSU Turfgrass Runoff Site at the OSU Turfgrass
Research Center (Figure 5). The primary purpose of the system being constructed is to provide experimental
precision and test alternative uses for filter materials. The OSU Turfgrass Runoff site has expanded from 6 plots to
12 plots. Each plot measures 17 ft x 80 ft and is supported by its own automatic sampler and flow meter. Each plot
will have to be reduced to about 17 ft x 35 ft to accommodate a trench high enough on the slope to have sufficient
fall from the bottom of the trench to the Parshall flumes where flow is measured and samples are collected. The site
will be designed to collect runoff from the plot into a trench filled with filtering material that removes P, heavy
metals, possibly N, and other contaminates. The filtered runoff will collect into a typical drainage pipe at the bottom
of the trench and flow in a subsurface pipe to the samplers. The design simulates a collection trench or a typical
subsurface drain pipe surrounded by gravel or sand. However, in this case filter material is substituted for the gravel
or sand. To accommodate easy removal and replacement of filtering materials the trench will be lined by either a
wooden, galvanized, fiberglass, or plastic structure that contains the filter material (Figure 6). Under field
conditions, a containment structure would not be necessary. In a field system the trench might be lined with a
geotextile but it would otherwise be free of components except for the filter material and the drain pipe.
Figure 5. The OSU Turfgrass Runoff site prior to trenching for addition of the proposed filter mechanisms.
The experimental design for the study is a split plot with main plots of filter material (steel slag or pea
gravel) and subplots of fertilizer (P applied or no P applied). Studies are to be initiated by natural rainfall runoff but
could be expanded to include simulated rainfall runoff if additional funding is identified. Flow will be calculated in
five-minute intervals for each runoff event and samples of treated runoff collected at the same interval. By
experimental design, the steel slag filter will be compared with pea gravel for its ability to remove DRP, heavy
metals, and N. A second very small pipe will be used to collect raw runoff as it enters each trench for further
analysis. Runoff collected in the small pipe will flow to a designated container and will be analyzed to determine
the average pre-filter chemical content of runoff entering the trench during each event.
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Figure 6. A potential design for containment of the filter material in a runoff collection trench. This design is made
of treated wood lined with plastic film but plastic, galvanized, and fiberglass containers are being investigated.
Summary:
Based on research to date, turf inhibits runoff better than any other surface. Even some man-made
materials specifically designed to reduce erosion do not inhibit runoff as well as turf (Krenitsky et al., 1998).
However, based on previous studies, runoff from turf cannot be entirely prevented and can potentially contain
unacceptable levels of nutrients and pesticides. Turfgrass managers must be aware of and execute management
practices that help to reduce this potential environmental contamination. Researchers must continue to search for
new economically feasible means of reducing nutrient and pesticide runoff.
All of the facilities described in this proposal have been constructed or are under construction. USGA
funds will not be needed or used for construction. Funding for this project is primarily needed for labor and sample
analysis. Additional funding may be used for project expansion and will be sought from other sources.
At the completion of the project we expect to have a thorough analysis and knowledge of steel slag for use
as a chemical filter in turfgrass systems. We will know the material’s attributes, its limitations, and its effectiveness
for use in multiple types of filtering systems. We will have developed a standard for comparison with additional
potential filter materials and we will have adjusted and perfected our testing devices.
Funds Requested:
Stipend (graduate student)
Labor (technician and maintenance)
Benefits
Supplies and Materials (research)
Facilities and administration (0%)*
Total
2011
7,000
800
931
1,269
2012
7,210
824
959
1,007
Total
14,210
1,624
1,890
2,276
10,000
10,000
20,000
*By policy the USGA will not pay facilities and administrative costs for projects funded at less than or equal to
$10,000 per year.
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Investigators:
Chad J. Penn received a Ph.D. in soil chemistry from Virginia Tech in 2004. He is currently an assistant professor
in the department of plant and soil science at Oklahoma State University. While serving as a post-doctoral
researcher at the USDA-ARS station at University Park, PA he conducted research on several industrial by-products
as PSMs. At that time he helped to design the first large scale phosphorus removal structure, located on the Eastern
shore of Maryland. He has collected over 20 industrial by-products for use as potential PSMs and is currently
characterizing them for potential use in phosphorus removal structures, particularly with the goal of producing a
simple empirical model for both designing P removal structures and predicting their longevity and effectiveness.
Dr. Penn has constructed a phosphorus removal structure on a golf course at Stillwater Country Club and also a
pond filter located at the Oklahoma State University turf research center He has given over 20 presentations on this
topic in the last five years and has produced several publications on P filtration, including one book chapter. Much
of his previous research on PSMs is in regard to understanding phosphorus sorption mechanisms using novel
techniques such as isothermal titration calorimetry.
Greg Bell received a Ph.D. in agronomy from The Ohio State University in 1997. He is a Professor in the
Department of Horticulture and Landscape Architecture at Oklahoma State University and holds the Wayne and
Jean Huffine Endowed Professorship in Turfgrass Science. Dr. Bell or his graduate students have published 23
refereed journal articles and two book chapters. A third book chapter and a textbook “Turfgrass Physiology and
Ecology: Advanced Management Principles” are awaiting publication. Two papers, “Reducing nutrient runoff from
golf course fairways using grass buffers of multiple heights” and “Nutrient runoff from bermudagrass golf course
fairways after aerification” were published in Crop Science and in Applied Turfgrass Management from his research
program and two more will be submitted this year and/or next year. A book chapter, “Management practices that
reduce runoff transport of nutrients and pesticides from turfgrass”, was published in 2008 and several related articles
have appeared in the professional press including TERO and the Green Section Record.
References:
Baird, J. H., N. T. Basta, R. L. Huhnke, G. V. Johnson, M. E. Payton, D. E. Storm, C. A. Wilson, M. D. Smolen, D.
L. Martin, and J. T. Cole. 2000. Best management practices to reduce pesticide and nutrient runoff from
turf. In Clark, J. M. and M. P. Kenna (ed.) Fate and management of turfgrass chemicals. American
Chemical Society. Washington, DC.
Baker, J. L., S. K. Mickelson, K. Arora, and A. K. Misra. 2000. The potential of vegetated filter strips to reduce
pesticide transport. p. 272-287. In Steinheimer, T. R., et al. (ed.) Agrochemical movement: perspective
and scale. American Chemical Society. Washington, DC.
Bell, G.E. and J.Q. Moss. 2008. Management practices that reduce runoff transport of nutrients and pesticides from
turfgrass. p. 133-150. In M. Nett, A.M. Petrovic, M.J. Carrol, and B.P. Horgan (ed.) The Fate of Turfgrass
Nutrients and Plant Protection Chemicals in the Urban Environment. Symposium Series no. 997,
American Chemical Society, Oxford University Press, Oxford, England.
Bierman, P.M., B.P. Horgan, C.J. Rosen, A.B. Hollman, and P.H. Pagliari. 2010. Phosphorus runoff from turfgrass
as affected by phosphorus fertilization and clipping management. J. Environ. Qual. 39:282-292.
Burton Jr., G.A. and R.E. Pitt. 2002. Stormwater Effects Handbook. CRC Press, Boca Raton, FL.
Cohen, S., A. Svrjcek, T. Durborow, and N.L. Barnes. 1999. Water quality impacts by golf courses. J. Environ.
Qual. 28:798-809.
Cole, J.T., J.H. Baird, N.T. Basta, R.L. Huhnke, D.E. Storm, G.V. Johnson, M.E. Payton, M.D. Smolen, D.L.
Martin, and J.C. Cole. 1997. Influence of buffers on pesticide and nutrient runoff from bermudagrass turf.
J. Environ. Qual. 26:1589-1598.
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Daniel, T.C., A. N. Sharpley, and J.L. Lemunyon. 1998. Agricultural phosphorus and eutrophication: a symposium
overview. J. Environ. Qual. 27:251-257.
Elliott, H.A., G.A. O'Connor, P.Lu, and S. Brinton. 2002. Influence of water treatment residuals on phosphorus
solubility and leaching. J. Environ. Qual. 31: 1362- 1369.
Easton, Z.M. and A.M. Petrovic. 2004. Fertilizer source effect on ground and surface water quality in drainage from
turfgrass. J. Environ. Qual. 33:645-655.
Easton, Z.M., A.M. Petrovic, D.J. Lisk, and I.M. Larsson-Kovach. 2005. Hillslope position effect on nutrient and
pesticide runoff from turfgrass. Int. Turfgrass Soc. Res. J. 10:121-129.
Holz, J.C. and K.D. Hoagland. 1999. Effects of phosphorus reduction on water quality: Comparison of alum-treated
and untreated portions of a hypereutrophic lake. J of Lake and Res. Man. 15:70-82
Kauffman III, G.L. and T.L. Watschke. 2007.Phosphorus and sediment in runoff after core cultivation of creeping
bentgrass and perennial ryegrass turfs. Agron. J. 99:141-147.
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