Download Characteristics of fish fauna of the Macintyre and Dumaresq Rivers

Queensland the Smart State
Characteristics of fish fauna of
the Macintyre and Dumaresq
Rivers and Macintyre Brook
A report to the Queensland
Murray-Darling Committee
Prepared by Adam Butcher
Department of Primary Industries & Fisheries
May 2007
May 2007
While every care has been taken in preparing this publication, the State of Queensland accepts no
responsibility for decisions or actions taken as a result of any data, information, statement or
advice, expressed or implied, contained in this report.
The Department of Primary Industries and Fisheries has taken all reasonable steps to ensure that
the information contained in this publication is accurate at the time of publication. Readers should
ensure that they make appropriate enquiries to determine whether new information is available on
the particular subject matter.
© The state of Queensland, Department of Primary Industries and Fisheries and the Queensland
Murray-Darling Committee Inc. 2007.
Copyright protects this publication. Except as permitted by the Copyright Act 1968(Cth),
reproduction by any means (photocopying, electronic, mechanical, recording of otherwise), making
available online, electronic transmission or other publication of this material is prohibited without
prior written permission from the Department of Primary Industries and Fisheries or the
Queensland Murray-Darling Committee Inc.
Inquiries should be addressed to:
Director General
Department of Primary Industries and Fisheries
Southern Fisheries Centre
GPO Box 46
Brisbane Qld 4001
Chief Executive Officer
Queensland Murray-Darling Committee Inc.
PO Box 6043
Toowoomba West Qld 4350
Contents
1
2
3
4
5
5.1
5.2
5.3
5.4
5.5
5.6
5.7
6
6.1
7
Executive summary………………………………………..…………
ii
Project objectives…………………………………..…………………
Project Methodology…………………………...……………………..
Background………………………..…………………………………..
Geographical scope………………………..…………………………
Methods
Data sources…………………………………………………………..
Data gaps
Species biology/ecology
Native Species
Ambassis agassizii………………………………………………..
Bidyanus bidyanus…………………..……………………………
Craterocephalus amniculus………………………..…………….
Craterocephalus stercusmuscarum fulvus…………..…………
Gadopsis marmoratus…………………..………………………..
Galaxias olidus………………………..…………………………..
Hypseleotris spp……………………………..……………………
Leiopotherapon unicolour……………………………...…………
Maccullochella peelii peelii……………………………………....
Macquaria ambigua……………………..………………………..
Melanotaenia fluviatilis…………………………..……………….
Mogurnda adspersa………………………………..……………..
Nemotalosa erebi…………………………………..……………..
Philypnodon grandiceps………………………………..………...
Retropinna semoni……………………………………..…………
Tandanus tandanus…………………………..…………………..
Alien Species
Carassius auratus…………………………………………………
Cyprinus carpio……………………………..……………………..
Gambusia holbrooki………………………………..……………..
Perca fluviatilis………………………………………..…………...
Information gaps in the biology/ecology……………………..……..
The river continuum concept………………………………………...
The demonstration reach concept……………………………..……
Review of sites on the proposed demonstration reach…….……..
Recommendations on the suitability of sites………………..……..
Recommendations……………..……………………………………..
References…………………………………………………………….
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i
Executive Summary
The Queensland Murray-Darling Committee (QMDC) and the Border Rivers-Gwydir
Catchment Management Authority (BRGCMA) are in the process of establishing a
demonstration reach on the Macintyre River system. A key component of the
investigative stage is to determine the appropriate length of the demonstration reach. This
document informs the debate on demonstration reach length by characterising the species
present within the geographical scope. The geographical coverage of this review is the
Border Rivers region of southern Queensland and northern New South Wales. It includes
waters from the Dumaresq and Macintyre Rivers, and Macintyre Brook and their
tributaries downstream of Glenlyon Dam, Pindari Reservoir, and Coolmunda Dam,
respectively. The downstream limit is near Toobeah on the Macintyre River.
Ten data sets were identified from research projects in this area. These projects have
collectively identified 16 native and four alien species in this section of the Border Rivers
catchment. Although data collection has occurred between 1901 and 2007, very few of
the data sets have spatial, temporal or technical continuity, limiting their usefulness for
direct comparisons.
At least five native fish and one alien species have a restricted distribution within the
Border Rivers region. Species such as flathead gudgeons (Philypnodon grandiceps), river
blackfish (Gadopsis marmoratus), Agassiz’ perchlet (Ambassis agassizii) and silver
perch (Bidyanus bidyanus) are rare species in both river systems. On the other hand,
gudgeons (Hypseletoris sp.), Murray River rainbow fish (Melanotaenia fluviatilis) and
Darling hardyhead (Craterocephalus amniculus) are all relatively abundant in the Border
Rivers region. Other species have variable distributions and abundance, being common in
one river system, but not the other.
The Border Rivers region would be suitable for the proposed demonstration reach. Three
large-bodied species are known to undertake extensive migrations during their life-cycle,
but populations could be accommodated within any demonstration reach site. Many of
the lesser native species would not require extensive longitudinal distances to complete
their life-cycle. Rather, it is the presence or absence of critical habitat over a short spatial
scale that would be a key influence to their population success. However, there is still a
concern about adequate offstream access. Many smaller species require access to either
instream or offstream backwaters for some of their life-cycle. Both the habitat and access
have diminished with the advent of flow regulation and strategies addressing this issue
must be considered if we are to adequately accommodate the full suite of native
freshwater fish present in the Border Rivers region of the Murray-Darling Basin.
ii
Project Title:
QMDC native fish strategy Demonstration
Reach—Macintyre River
Phase 1: Characteristics of fish fauna of the
Macintyre and Dumaresq Rivers and
Macintyre Brook
Prepared by
Adam Butcher, DPI&F, Queensland
Reviewed by
Adjunct Assoc. Professor Mark Lintermans
Research Program Coordinator
Native Fish Strategy
Murray-Darling Basin Commission &
Dr. Peter Jackson, Consultant
1.
Project objectives
1. To use existing data to determine the characteristics of the fish faunas of the
Macintyre and Dumaresq Rivers, and Macintyre Brook.
2. To use this information to make recommendations on the appropriate length of
a demonstration reach in the Macintyre River that would impact on the fish
fauna.
3. To use this information to comment on the suitability of using sites on the
Macintyre Brook or Dumaresq Rivers as control and treatment sites for the
demonstration reach.
4. To provide information on knowledge gaps in relation to the fish faunas of
these rivers.
2.
Project Methodology
The project will involve:
1. Identification of, negotiation for access to, and collation of existing databases
on fish faunas in the three rivers with regard to species present, distributions
and relative abundances.
2. Identification of data gaps.
3. Documenting the life cycles of the species present, particularly in relation to
normal home range, migrations, spawning and juvenile rearing areas from
existing information sources.
4. Identify information gaps for individual species.
1
5. Review the river continuum concept to identify the influence of riverscapes on
fish dynamics, and define key concepts that underpin demonstration reach
principles.
6. Use this information to make recommendations on suitable demonstration
reach lengths that encompass and enhance previously defined fish faunas.
7. Review the proposed control and demonstration sites for suitability according
to the criteria specified in Section 5.
8. Use this information to make recommendations on the suitability of sites on
the Macintyre Brook or Dumaresq River as control sites, or to recommend
other options for reach and control sites.
9. Provide recommendations on any additional work related to the fish fauna that
needs to be done before the locality and length of the demonstration reach, and
the locality of control sites can be determined.
3.
Background
Current estimates put native fish populations in the Murray-Darling Basin at 10% of
the pre-European settlement levels (Anon. 2004). They are in urgent need of
rehabilitation. This need for regeneration of fish populations is driven by the belief
that they are an allegory of riverine health. As the largest river system in Australia,
the Murray-Darling Basin supports the largest social and agricultural community
outside the capitals of each state. A recent survey of the Murray-Darling Basin has
classified 95% of the river length as degraded, with 30% as modified substantially
from its original condition (Norris et al. 2001). While there are a range of reasons for
the decline in fish populations in the Murray-Darling Basin (Anon. 2004), it is
apparent that their decline is commensurate with the decline in river health.
The Murray-Darling Basin Commission recently released a 10 year plan for fish
rehabilitation (Anon 2004) to ensure that the significant declines in native fish
populations within the Murray-Darling Basin are addressed and rehabilitated. These
are to be achieved through 13 objectives, condensed into the following six driving
actions:
• rehabilitating fish habitat;
• protecting fish habitat;
• managing riverine structures;
• controlling alien fish species;
• protecting threatened native fish species; and
• managing fish translocation and stocking.
A recent Murray-Darling Basin Commission workshop on native fish habitat
rehabilitation and management recommended five key actions to drive future habitat
rehabilitation and management actions (Lintermans et al. 2004). These were:
• protecting fish habitat;
• managing rivers holistically;
• involving stakeholders in riverine protection and restorations;
2
•
•
building knowledge and capacity for integrated management of aquatic
habitats; and
developing demonstration reaches.
Demonstration reaches are reaches of river where a number of interventions are
implemented (e.g.: restoring fish passage, rehabilitating riparian vegetation, reestablishing woody debris, controlling alien fish, etc.) to demonstrate how a
coordinated program will beneficially impact on populations of native fishes.
Demonstration reaches are favoured by many because they demonstrate an integrated
approach, using several rehabilitation actions that can achieve a quantifiable
improvement in fish populations. They engage community awareness and support,
focus the attentions of funding agencies, and provide scientific knowledge of rivers
and fish (Barrett 2004a). There are several demonstration reaches in the southern
states, but none yet in Queensland. The southern examples appear to be allied with
pre-existing management actions.
The Queensland Murray-Darling Committee (QMDC) and the Border Rivers-Gwydir
Catchment Management Authority (BRGCMA) are in the process of establishing a
demonstration reach on the Macintyre River system. The Dumaresq, Severn and Mole
Rivers and the Macintyre Brook have been included in the brief as there may be
control and/or reference sites established on these rivers. The project is currently in
the investigative stage with a focus on determining the current condition of the river
and identifying what interventions are needed and where they should happen.
A key component of the investigative stage is to determine the appropriate length of
the demonstration reach. Recent discussions at a demonstration reach workshop in
Canberra have indicated that the length of a reach should be governed by the fish
fauna in question and the life cycles of the fish species involved. For example, will
the reach be long enough to impact on the fish species present or will some species
move outside the reach during their life cycle and be influenced by factors other than
those occurring in the reach. This document informs the debate on demonstration
reach length by characterising the species present within the geographical scope.
4.
Geographical scope
The geographical coverage of this review is the Border Rivers region of southern
Queensland and northern New South Wales, from the Great Dividing Range
(~151°30’E), west to Toobeah (~149°45’E), north to the southern slopes of Mt.
Bodumba (~28°20’S), and south to the northern extremities of the New England
Tablelands of northern New South Wales (~29.25°S) (Fig. 1). It includes waters from
the Dumaresq and Macintyre Rivers, and Macintyre Brook, and their tributaries
downstream of three major impoundments:
• Coolmunda Dam on Macintyre Brook;
• Glenlyon Dam on Pike Creek, a tributary of the Dumaresq River; and
• Pindari Reservoir on the Severn River (NSW), a tributary of the Macintyre River.
3
Figure 1: Geographical area where the proposed demonstration reach and control
and reference sites will occur. Data supplied by QMDC.
The region comprises two distinct hydrological zones. These were defined by Moffat
and Voller (2002) as upper and lower foothills based on altitude, and can be
reconciled to the Sustainable Rivers Audit (SRA) terminology developed by
Whittington et al. (2001). The SRA defines geomorphology on two scales: Functional
Process Zones and Valley Process Zones. Functional Process Zones are segments of
river that have similar discharge and sediment regimes as defined by their gradient,
stream power, valley dimensions and boundary material. Valley Process Zones are an
aggregation of Functional Process Zones and are geomorphically similar regions
within a river valley. They are described as regions of sediment source, transport and
deposition. The zones contained within the Border Rivers region of the MurrayDarling Basin comprise:
1. the upper foothills/sediment source zone 400-600 metres above sea level (a.s.l.)
occurs within between Stanthorpe/Inverell and Inglewood/Texas/ Wallangara.
This includes parts of the Macintyre Brook between Lake Coolmunda and
Inglewood, the Dumaresq River between Pike Creek and Texas, the Macintyre
River above Wallangara, and the Severn River (NSW) between Ashford and the
Pindari Reservoir. These sections are predominantly pool and riffle habitats with
semi-permanent flowing clear water. Submerged aquatic plants are common.
4
2. the lower foothills/sediment transport zone 150-400 metres a.s.l. between the
upper foothills zone and Toobeah on the Macintyre River. This region is
characterised by a network of pools, intermittently connected during floods. The
sides of pools are often clay or mud, while the bottoms are covered with sand or
silt. Areas of bedrock and rubble are common. Waters are quite turbid, visibility
is usually less than 30 centimetres, and submerged aquatic vegetation is patchy
and uncommon.
Methods
5.
5.1 Data sources
Relevant data has been identified from ten different sources (Table 1) and these were
contacted and asked to provide information on the sites sampled during each project,
and the fish species found. These projects cover a range of sites from the lower
foothills region of the Macintyre River below Goondiwindi, to the upper foothills
region of the Macintyre, Dumaresq and Mole Rivers on the north-western slopes of
the New England Tablelands.
Table 1: Data sources contacted during compilation of this report. Abbreviations are
listed below the table.
Dataset
#
1
Organisation
Project
DPI&F1
Meso-scale
movements
2
DPI&F/
Fisheries
(NSW)2
3
NRM&W 3
4
5
UNE4
DNR (NSW)5/
4
UNE
6
7
8
DPI&F
1
DPI&F
1
6
CU
9
ARI (GU)7
10
Qld Museum
Abbreviations are:
1. DPI&F
2. Fisheries (NSW)
3. NRM&W
4. UNE
5. DNR (NSW)
6. CU
7. ARI (GU)
SRA tri-annual
survey
Critical flows for
fish
life-history
strategies and
flows
Pindari Fish
Monitoring Project
Regional
impoundment
stocking surveys
Macintyre River
fishway surveys
Anabranch
geomorphology
and productivity
Dryland Refugia
project
Historical records
Sampling location
Macintyre River between Goondiwindi and Mungindi
Severn, Dumaresq, Macintyre and Mole Rivers, and
adjacent tributaries
Macintyre River between Goondiwindi and Mungindi
Dumaresq and Mole Rivers
Severn, Macintyre and Mole Rivers
Coolmunda and Glen Lyon dams
Boggabilla Weir Fishway, Macintyre River, (only
studied pit-tagable sized fish)
Anabranches to the Macintyre River below
Goondiwindi
Macintyre River at Goondiwindi, Talwood-Boomi,
Mungindi, and Collarenebri.
Opportunistic sampling in the Border Rivers region
Department of Primary Industries and Fisheries, (QLD)
New South Wales Fisheries
Natural Resources, Mines and Water (QLD)
University of New England, Armidale
Department of Natural Resources, (NSW)
Canberra University, Canberra
Australian Rivers Institute, Griffith University
5
These projects have collectively identified 16 native and four alien species in this
section of the Border Rivers catchment (Table 2). This compares to the more than 35
native and 11 alien fish species in the Murray-Darling Basin, some of which are
estuarine, and others are restricted in their distribution to highland habitats (more than
600 metres a.s.l.).
Although data collection has occurred between 1901 and 2007, very few of the data
sets have spatial, temporal or technical continuity (see Table 3). This limits their
usefulness for making meaningful comparisons between data sets, or defining
temporal changes in abundance for individual species. However, it does allow us to
establish distributions for individual species.
The SRA data set contains the most temporally contiguous data, although the number
of sites and gear used varies in different years. However, there was a consistent level
of sampling in the years of 2001, 2002 and 2005. A ‘relative abundance’ index (Table
4) can be inferred by sub-sampling the data from these years across all uniform
sample sites. This is not a true relative abundance index, though, because of the
sampling gear diversity between years and sites, and the differences in levels of
sampling between the two rivers. However, the inferred relative abundance index can
be used to inform the species characterisation debate (see section 5.3) at both the
Border Rivers regional scale (combined) and the two individual river valleys.
Table 2: List of data sets with number of sites sampled, gear type used and river
system sampled. Gear type is abbreviated in the table and abbreviations are
expanded below the table.
6
Data set
1
1
1
2
Year
2005
2006
2007
1975
# sites
30
30
30
6
Gear used
M, F, BtE
M, F, BtE
M, F, BtE
BtE, CMT
2
2
2
1976
1998
1999
2
1
10
BtE, CMT
CMT?
BtE
2
2000
15
2
2001
20
2
2002
22
2
2003
21
2
2
2004
2005
10
23
BPE, BtE,
CMT, F
BtE, CMT,
F
BtE, CMT,
F
BtE, CMT,
F
LDN
BtE, CMT,
F
3
1996
4
3
1997
4
3
1998
4
4
2005
13
MGn, CMT,
F
MGn, CMT,
F
MGn, CMT,
F
LDN, S,
CMT
River system
Macintyre River, below Goondiwindi
Macintyre River, below Goondiwindi
Macintyre River, below Goondiwindi
Beardy & Macintyre River, Tenterfield
Creek
Severn River (NSW)
Macintyre River
Macintyre, Dumaresq, Severn (NSW)
Rivers
Tenterfield Creek
Beardy, Deepwater, Macintyre & Mole
Rivers, Tenterfield Creek
Beardy, Deepwater, Macintyre, Mole &
Severn (NSW) Rivers, Tenterfield Creek
Beardy, Dumaresq, Macintyre, Mole &
Severn (NSW) Rivers, Tenterfield Creek
Dumaresq & Macintyre Rivers
Beardy, Deepwater, Dumaresq,
Macintyre, Mole & Severn (NSW) Rivers,
Tenterfield Creek
Severn (QLD), Dumaresq & Macintyre
Rivers
Severn (QLD), Dumaresq & Macintyre
Rivers
Severn (QLD), Dumaresq & Macintyre
Rivers
Macintyre, Severn (NSW), Mole &
Dumaresq Rivers
Data set
4
Year
2006
# sites
13
4
2007
13
5
5
5
5
6
2005
2005
2005
2005
1976current
2002
8
8
8
8
7
2
Gear used
LDN, S,
CMT
LDN, S,
CMT
BtE
BtE
BtE
BtE
BtE
Bte
8
9
10
2001
4
F, S, LDN
1901various
unknown
2002
Gear abbreviations are:
• BPE
Backpack Electrofishing;
• BtE
Boat Electrofishing;
• CMT
Collapsible Minnow Traps;
• F
Fyke nets;
• LDN
Larval Drift Nets;
• M
Mini fykes;
• MGn
Multi-mesh Gill nets;
• S
Seine net.
River system
Macintyre, Severn (NSW) , Mole &
Dumaresq Rivers
Macintyre, Severn (NSW) , Mole &
Dumaresq Rivers
Macintyre, Severn (NSW) & Mole Rivers
Macintyre, Severn (NSW) & Mole Rivers
Macintyre, Severn (NSW) & Mole Rivers
Macintyre, Severn (NSW) & Mole Rivers
Coolmunda and Glen Lyon dams
Below and above Boggabilla weir,
Macintyre River
Macintyre River between Goondiwindi
and Talwood
Macintyre River, below Goondiwindi
Border Rivers and tributaries
Table 3: Combined list of all species of fish captured during the projects listed in
Table 1. Presence in data set # refers to the number of each data set in Table 1.
Species
Ambassis agassizii
Bidyanus bidyanus
Craterocephalus amniculus
Craterocephalus stercusmuscarum fulvus
Gadopsis marmoratus
Galaxias olidus
Hypseleotris spp
Leiopotherapon unicolor
Maccullochella peelii peelii
Macquaria ambigua
Melanotaenia fluviatilis
Mogurnda adspersa
Nemotalosa erebi
Philypnodon grandiceps
Retropinna semoni
Tandanus tandanus
Carassius auratus*
Cyprinus carpio*
Gambusia holbrooki*
Perca fluviatilis*
Presence in data
set #
1,2,3,4,
7,8,9
1,2,3, 5,6,7
2,
1,2,3,4,5, 7
3,
2,3,
1,2,3,4,5, 7, 9
1,2,3,4,5,6,7,8,9
1,2,3,4,5,6,7, 9
1,2,3,4,5,6,7, 9
1,2,3,4,
7,8,9
2,3,4,
1,2,3,4,
7, 9
1,
1,2,3,4,5,
9
1,2,3, 5,6,7
1, 3,4,
7
1, 3,4,5,6,7,8,9
1, 3,4,5,
9
2,
Relative
distribution
7
6
1
6
1
2
7
9
8
8
7
3
6
1
6
6
4
8
5
1
*denotes alien species.
7
Table 4: Inferred Relative Abundance Index of native fish caught in the Macintyre
and Dumaresq River valleys. Note that neither the flathead gudgeon (Philypnodon
grandiceps) nor river blackfish (Gadopsis marmoratus) were recorded in data set 2
and thus are not included in this table.
Species
Ambassis agassizii
Bidyanus bidyanus
*Carassius auratus
Craterocephalus amniculus
Craterocephalus stercusmuscarum
*Cyprinus carpio
Galaxias olidus
*Gambusia holbrooki
Hypseleotris spp
Leiopotherapon unicolor
Maccullochella peelii peelii
Macquaria ambigua
Melanotaenia fluviatilis
Mogurnda adspersa
Nematalosa erebi
*Oncorhynchus mykiss
*Perca fluviatilis
Retropinna semoni
Tandanus tandanus
Relative
Abundance –
Macintyre River
0.05
0.14
3.81
11.67
2.05
5.71
0.33
4.10
23.81
2.71
3.14
3.10
9.24
0.00
26.29
0.00
1.29
1.76
2.00
Relative
Abundance –
Dumaresq River
0.20
0.00
4.63
12.30
2.03
2.23
8.90
74.00
96.75
0.25
2.33
0.75
5.20
4.58
0.08
0.03
0.65
2.90
29.55
Relative
Abundance
– combined
0.1
0.0
4.3
12.1
2.0
3.4
6.0
49.9
71.6
1.1
2.6
1.6
6.6
3.0
9.1
0.0
0.9
2.5
20.1
*denotes alien species.
The presence/absence of any single species in each data set is governed by several
factors. On a mechanical scale, this includes factors such as the selectivity of
sampling methods used and sites sampled of any single species. On a whole of
catchment spatial scale, the geographical distribution of each species will be an
influencing factor. On a single river scale, access to suitable habitat via longitudinal
and lateral connectivity will influence their presence/absence. On a reach scale,
availability of suitable habitat will be a primary determining factor. Thus, the relative
abundance of each species outlined in table three cannot be determined by an
integrated assessment across all data sets. However, the number of data sets in which
a species is found can be used to infer a relative distribution within the MacintyreDumaresq Rivers system, with any score below four indicating a restricted
distribution (providing the reader accepts the mechanical and spatial factors
influencing these results).
A quick examination of table three highlights the very restricted distribution of five
species: the Darling hardyhead (Craterocephalus amniculus), the river blackfish
(Gadopsis marmoratus), the mountain galaxias (Galaxias olidus), the purple-spotted
gudgeon (Mogurnda adspersa), and the flathead gudgeon (Phylipnodon grandiceps).
The Darling hardyhead and the mountain galaxias are usually restricted to upper
foothill waters (greater than 600 metres a.s.l.) in the Macintyre-Dumaresq River
system. Similarly, the purple-spotted gudgeon, while declining in the southern
Murray-Darling Basin, is found in the Border Rivers above 240 metres (a.s.l.) and
would not be expected to be present in many of the data sets. The river blackfish is
more common in waters above 150 metres (a.s.l.) in the southern Murray-Darling
Basin, and it is listed as present in the Macintyre River (data set 4), but restricted to
upper foothill waters. The flathead gudgeon has only been found in the lower foothill
8
waters of the Macintyre River (data set 1), and it appears to be quite rare in the Border
Rivers region of the Murray-Darling Basin (see section 5.3, below).
At least five native fish and one alien species have a restricted distribution within the
Border Rivers region. While this might imply rarity of these species, their absence is
probably explained by the diversity of sample location between data sets (i.e.: not
sampling in locations where these fish might occur). The Relative Abundance Indices
(RBI) in table four give a more accurate indication of species abundance, although
being an arbitrary relative scale, it is not possible to compare between species (i.e.: a
species with an RBI of four does not mean it is twice as abundant as a species with an
RBI of two). From table four, it is apparent that species such as Philypnodon
grandiceps and Gadopsis marmoratus are rare as they are not present in any of the
SRA data for the Border Rivers, and only occur in one database. Ambassis agassizii
and Bidyanus bidyanus are also rare species in both river systems. On the other hand,
Hypseletoris sp., Melanotaenia fluviatilis and Craterocephalus amniculus are all
relatively abundant in the Border Rivers region. We can also infer that Nematalosa
erebi is relatively common in the Macintyre River, but not as common in the
Dumaresq River (only three have been recorded in the SRA database since 2000 for
the Dumaresq River and tributaries). Other species with divergent abundance,
depending on the river, include Leiopotherapon unicolor and Macquaria ambigua,
which are more common in the Macintyre River, and Galaxis olidus, Mogurnda
adspersa and Tandanus tandanus, which are more common in the Dumaresq River.
5.2 Data gaps
Examining table one, it is apparent that there are data gaps, particularly from
Macintyre Brook. The SRA database contains the only record of sampling in this
water body, at Whetstone Weir which was sampled in 2005. This water body has not
been surveyed adequately to determine its species suite. Lake Coolmunda, upstream
on Macintyre Brook, has been sampled for stocked fish occasionally by DPI&F
officers using electrofishing, but there are no records for any other instream sampling.
If this is to be used as a suitable demonstration reach control or reference site (as has
been suggested by QMDC), then there will have to be some survey work to determine
species assemblages and habitat condition.
Other areas in need of further information are the impacts of declining lateral
connectivity (caused by drought and floodplain alteration) on fish abundances, and the
impacts declining longitudinal connectivity (caused by barriers) to fish distribution
and abundance. There are numerous weirs and dams on each river, and the degree of
impeded connectivity of each needs to be ascertained. This is discussed further in
section 5.5.
5.3 Species Biology/Ecology
The idealised fish life-cycle involves changes in body-shape, behaviour, habitat, diet
and sexual development, which comprise the life-history, (Fig. 2). At each stage in
their development, there may be a need to move to a more suitable habitat. Access to
this habitat may provide suitable food and shelter resources, or shelter from predation,
thereby enhancing the chance of survival and recruitment. These habitats can be in
backwaters or main channel habitats within the mainstream, or offstream in
anabranches or billabongs.
9
Collectively these ontogentic shifts can be divided into three main functions:
reproduction; nursery phase; and recruitment. Some or all of these phases will be
applicable to the life-histories of most native freshwater fish.
Sexually mature
adult population
May migrate to
spawning grounds
Reproduction
Recruitment
May be a juvenile
migration to adult
habitat
eggs
Nursery
May be affixed to substrate
or drift in current to a
suitable nursery area
juveniles
May be a
movement to postlarval or adult
habitat
larvae
Figure 2: The idealised model of a fish life-cycle, highlighting potential temporal
patterns for migration.
Much of the biology/ecology information for each species below comes from
publications on studies within the Murray-Darling Basin, supplemented by excellent
information available from studies within their distribution elsewhere (e.g.: Pusey et
al. 2004). The combined information is presented species by species below, following
the order presented in table 2.
Native Species
Ambassis agassizii
Common Name/s: Agassiz’s glassfish, Olive perchlet
Family: Chandidae
Discovered by: Steindachner, 1866
Most of the information about this species comes from studies in the eastern
Queensland coastal drainages. However, it is a fish with a wide distribution along
eastern Australian coastal rivers between northern Queensland and the central-north
coast of New South Wales (Pusey et al. 2004). Historically, it enjoyed a wide
distribution within the Murray-Darling Basin, but is now considered to be threatened
in the southern states (Vic, S.A.), and uncommon in southern New South Wales
(Harris & Gehrke 1996). It has been recorded in the Dumaresq and Macintyre Rivers
(Morris et al., 2001), but is quite rare in both distribution (Fig. 3) and abundance
(Table 4). Ambassis agassizii is commonly found in pools of water with a moderate
depth (around 0.5 metres depth) and slow velocity (less than 0.05 m.sec-1).
In south-eastern Queensland, it has been collected in waters of 20-60 centimetres
depth and velocities up to 0.44 m.sec-1 (Pusey et al. 2004). It is a pelagic species,
10
commonly found over fine sediment substrates (mud, sand, clay). While not
demonstrating a strong affinity to banks, it is commonly found close to cover such as
aquatic macrophytes and filamentous algae, occasionally aggregating into loose
schools during upstream movements (Morris et al. 2001). A. agassizii has been shown
to have a wide temperature (11.0 – 33.60C), and oxygen level tolerance (0.3 to 19.5
mg.l-1) (Pusey et al. 2004).
Figure 3: Recorded distribution of Ambassis agassizii in the Border Rivers region of
the Murray-Darling Basin, based on the ten datasets in table one.
This species has a lifespan of approximately four years, but are sexually mature after
12 months (Moffatt & Voller, 2002). A. agassizii is a serial spawner with an extended
reproductive season from spring through to autumn (Milton & Arthington 1983), but
with a peak in late spring to early summer. Spawning cues are unknown, but aquariabased research has shown that it can be triggered by increasing photoperiod and water
temperature. Thus, it may not be driven by rising water levels or flooding. Spawning
has been shown to occur amongst fine-leafed vegetation (Leggett & Merrick 1986).
On the east coast, larvae have been observed in large schools in surface waters of
tributaries, moving into the mainstream aquatic vegetation after reaching 8-12
millimetres in length (Pusey et al. 2004). They have been reported to disperse and
forage during darkness, and aggregate around cover during daylight (Allen & Burgess
1990). A. agassizii has been observed to undertake upstream movements in east coast
waters, after flood events, but movement is restricted to periods during lower velocity
after flood events. It has been observed to actively move into offstream billabongs in
the lower foothill waters of the Macintyre River during in-bank flow events
(Hutchison, pers. comm.). It is known to feed extensively on aquatic insects and
micro-crustaceans (Hansen 1995).
Pusey et al. (2004) have reported that threats to its survival in the Murray-Darling
Basin include alien fish species, habitat degradation and flow regulation. Alien
species are thought to actively feed on larvae and juveniles. Disturbance of riparian
habitat leading to increased turbidity can reduce macrophyte vegetation. Loss of flow
or artificial flows during breeding can cause loss of eggs from macrophyte vegetation,
reducing the chance of successful recruitment.
Bidyanus bidyanus
Common name/s: Silver perch, black bream
11
Family: Terapontidae
Discovered by: Mitchell 1838
This species once had a wide distribution throughout the Murray-Darling Basin, but
has declined markedly throughout the lower Murray-Darling Basin. Self-sustaining
populations are now thought to be restricted to the Queensland Murray-Darling Basin
(Moffatt & Voller 2002), and the upper Murray River. In the Border Rivers region, it
has a relatively wide distribution (Fig. 4) assisted, in part, by local stocking programs,
but a rare abundance (Table 4). A shoaling species, they are commonly found in slow
or standing pools, often in association with large woody debris, or reeds, as well as
fast flowing turbid waters (Koehn & O’Connor 1990) of lowland rivers. They are
often found in open water, or in association with submerged or emergent aquatic
vegetation. Bidyanus bidyanus is reportedly able to tolerate a wide range of
temperature (2-360C) (Lake 1966a).
Figure 4: Recorded distribution of Bidyanus bidyanus in the Border Rivers region of
the Murray-Darling Basin, based on the ten datasets in table one.
B. bidyanus have been reported to live up to 26 years (Mallen-Cooper & Stuart 2003),
and can reach up to eight kilograms, although less than 16 years and 1-1.5 kilograms
is more common in the southern Murray-Darling Basin (Morris et al. 2001). Males
mature at approximately three years, while females take up to five years to mature.
These fish are known to school and migrate upstream to spawn (Allen et al. 2002),
usually in spring or summer when water temperatures exceed 230C (Lake 1966a), on
the back of a receding flood. Eggs are pelagic and readily displaced by current.
Larvae are free swimming by five days old and strongly phototactic. This is thought
to assist their wide distribution across the flood plain. Post-larval juveniles are found
18 days after the eggs are fertilized. Juveniles feed primarily on filamentous algae and
phytoplankton, although some zooplankton is also in their diet (Lake 1966b). Adults
feed on aquatic micro-invertebrates and algae (Moffatt and Voller 2002).
B. bidyanus is listed as critically endangered in Victoria, and vulnerable in New South
Wales (Morris et al. 2001). Factors leading to a decline in B. bidyanus populations
throughout the Murray-Darling Basin include instream habitat degradation, alterations
to river flow and water temperature regimes, and instream barriers (such as weirs and
dams) to spawning migrations (Morris et al. 2001). These threats are thought to
impact on both spawning and recruitment success, leading to localised population
extinctions.
12
Craterocephalus amniculus
Common name: Darling River hardyhead
Family: Atherinidae
Discovered by: Crowley & Ivanstoff, 1988
Craterocephalus amniculus is endemic in the upper tributaries of the Darling River,
including the Condamine, Peel, Namoi, Macintyre and Cockburn Rivers, and
Warialda, Tenterfield and Boiling Down Creeks (Ivanstoff & Cowley 1966). In these
upland regions, it is relatively common (Table 4), but restricted in its distribution (Fig.
5). Adults are found in small schools (10-15) in clear slow-flowing waters or in weed
at the edges of such waters (Ivanstoff & Cowley 1966). Little is known about the
biology or ecology of this species other than it is commonly found in waters less than
700 metres a.s.l., but can be found as low as 240 metres a.s.l. (Dean Gilligan pers.
comm.). It is probably very similar in biology to the fly-specked hardyhead (see
below), but exploits a different ecological niche.
Figure 5: Recorded distribution of Craterocephalus amniculus in the Border Rivers
region of the Murray-Darling Basin, based on the ten datasets in table one. Note that
additional records of C. amniculus can be found in the upland waters to the east of
map.
Craterocephalus stercusmuscarum fulvus
Common name: Fly-specked hardyhead
Family: Atherinidae
Discovered by: Ivanstoff, Crowley and Allen, 1986
The Craterocephalus stercusmuscarum fulvus is widely distributed across northern
Australia from Timor Sea drainages in Northern Territory, to the east coast rivers of
Queensland, down to the Tweed River, and historically inland into much of the
Murray-Darling Basin (Pusey et al. 2004). In 1986, it was divided into two
subspecies: a northern variant (Craterocephalus stercusmuscarum stercusmuscarum)
and a southern variant (Craterocephalus stercusmuscarum fulvus) by Ivanstoff et al.
(1986). The southern variant, C.s. fulvus, is moderately common in coastal rivers of
southern Queensland from the Elliot to the Tweed Rivers. Historically, it occurred
throughout much of the Murray-Darling Basin, although it was patchy in its
distribution. Currently, it is found in patches of the Queensland and northern New
South Wales Murray-Darling Basin including the Border Rivers, Moonie and
Condamine-Balonne catchments (Moffatt & Voller 2002). It has a wide distribution
13
within the Border Rivers region (Fig. 6), and has a relatively low, but not rare, level of
abundance (Table 4). It is also found in patches in Victoria and South Australia, but
has disappeared from much of the southern Murray-Darling Basin. On the east coast,
it is a pelagic schooling species, found in pools or runs with moderately low flow (less
than 0.4 to 0.86 m.sec-1) in depths of 10 to 60 centimetres, over medium to fine
substrates (sand, fine to course gravel) (Pusey et al. 2004). It has been collected in
areas closely associated with macrophyte vegetation, filamentous algae or submerged
marginal vegetation. It has been reported to congregate in areas where streams flow
into still water (Allen et al. 2002). C. s. fulvus is known to tolerate temperatures
ranging from 12.4 to 33.60C, and oxygen levels of 2.9 to 19.5 mg.l-1 (Pusey et al.
2004).
Figure 6: Recorded distribution of Craterocephalus stercusmuscarum fulvus in the
Border Rivers region of the Murray-Darling Basin, based on the ten datasets in table
one.
C. s. fulvus live up to three years, but are sexually mature within 12 months. They
have an extended spawning season from late winter through to summer, but a peak
occurs in late winter to early spring (Pusey et al. 2004). The spawning stimulus is
unknown, but corresponds to increasing photoperiod and water temperature.
Spawning takes place in aquatic macrophytes and submerged vegetation (Milton &
Arthington 1983). Evidence from fishway sampling on the east Queensland coast
indicates that for the northern variant (C. s. stercusmuscarum), low numbers move all
year round, but a peak in upstream migration occurs during summer as a consequence
of flow events (Stuart & Berghuis 1999). These movements are considered to be
dispersal/recolonisation events, especially after dry periods. Movements of the
southern variant are less well studied. C. s. fulvus is a microphagic carnivore
consuming aquatic insects and micro-crustaceans, as well as aquatic algae and
macrophytes.
It is listed as endangered in New South Wales and Victoria (Treadwell and Hardwick
2003). Its spawning habitats are threatened by erosion and increased siltation (Pusey
et al. 2004). Being a facultative migrator, it is susceptible to instream barriers that
prevent dispersal/recolonisation. It is vulnerable to competition and predation
interactions with alien species. Unseasonable flows during peak reproductive periods
are likely to diminish reproductive success (Morris et al. 2001).
14
Gadopsis marmoratus
Common name: River blackfish
Family:
Discovered by: Richardson, 1848
Gadopsis marmoratus enjoy a wide distribution throughout the lower Murray-Darling
Basin and remnant populations can still be found in the uplands zones of the
Condamine and Border Rivers of Queensland and New South Wales (Moffatt &
Voller 2002). It is also found in many coastal streams of south-east Australia and
Tasmania (Morris et al. 2001). While common in patches, it has suffered a general
decline in total numbers throughout its range, most probably due to siltation of habitat
and over fishing (Morris et al. 2001). It is quite rare within the Macintyre-Dumaresq
River systems (Table 4), occurring only in the upland waters of tributaries of the
Dumaresq River (Fig. 7). They exhibit strong site fidelity, with most fish being
associated with bank undercuts during daytime, and moving to open and boulder
habitats at night, presumably to feed (Khan et al. 2004). It is a hardy species
commonly found in slow flowing stream pools at depths from 20 to 60 centimetres
(Koehn et al. 1994). It has a preference for slow moving water (less than 0.20 m.sec1
), but has been recorded in waters of 0.04 to 0.34 m.sec-1, and in temperatures
ranging from five to 20 C. Adult G. marmoratus are tolerant of slightly brackish water
(up to 10 ppt) (Allen et al.2002).
Figure 7: Recorded distribution of Gadopsis marmoratus in the Border Rivers region
of the Murray-Darling Basin, based on the ten datasets in table one.
In the northern Murray-Darling Basin, G. marmoratus has a reported lifespan of over
six years, but is reproductively mature at two years (Moffatt & Voller 2002). The
spawning season runs from November to January, when adults form pairs and spawn
in hollow logs (Jackson 1968). The male parent actively guards the eggs until
hatching. Larval and juvenile habitats are unknown, but given the highly territorial
behaviour of adults, it is highly likely that they undertake dispersal migrations (Morris
et al. 2001). This is a predatory species, feeding on aquatic macroinvertebrates,
terrestrial insects and small fish, such as gudgeons (Moffatt & Voller 2002).
G. marmoratus has undergone a marked decline in its range, and probably abundance
throughout the Murray-Darling Basin. This has been attributed to a high susceptibility
to over fishing associated with strong site fidelity and low fecundity. A decline of
habitat quality associated with riparian destruction and agricultural run-off, causing
15
siltation of habitat may also be a contributing factor (Morris et al. 2001). It has a
preference for lower water temperatures and thus is restricted to the uplands region of
Condamine and Severn (QLD) Rivers (Michael Hutchison, pers. comm.).
Galaxias olidus
Common name: Mountain galaxias
Family:
Discovered by: Günther, 1866
Galaxias olidus are found in upland streams draining both sides of the Great Dividing
Range from southern Queensland to South Australia and Kangaroo Island (Allen et al.
2002). It has become scarce in areas accessible to alien fish species, such as brown
trout (Salmo trutta) and rainbow trout (Oncorhynchus mykiss). It is quite rare in the
Macintyre River system, being restricted to waters that are higher than 400 metres
(a.s.l.) (Table 4). It is much more common in the upper regions of the Dumaresq
River system (Fig. 8). Adults are found in clear pools of mountain streams, shoaling
around rocks or logs, or in open water (Allen et al. 2002). They are tolerant of very
cold water, having been caught in ice-melt fed streams (Koehn & O’Connor 1990).
Figure 8: Recorded distribution of Galaxias olidus in the Border Rivers region of the
Murray-Darling Basin, based on the ten datasets in table one.
G. olidus live for four years, and are reproductively mature by one (Moffatt & Voller
2002). Spawning occurs from August to late October when water temperatures range
between eight and 10°C (O’Connor & Koehn 1991). Adults move upstream to
shallow riffle areas to lay demersal, adhesive eggs over gravel substrates (Allen et al.
2002). Eggs hatch about 46 days later and feeding juveniles are found another eight
days later (O’Connor & Koehn 1991). Juveniles and adults can be found shoaling in
the same pools (McDowell & Fulton 1996). Their diet consists primarily of aquatic
invertebrates and terrestrial invertebrates, with larger fish consuming a greater
proportion of terrestrial vertebrates, especially in areas with substantial overhanging
riparian vegetation (Cadwallader et al. 1980).
The biggest threat to the survival of this species is predation from alien fish such as
brown trout and rainbow trout (Koehn & O’Connor 1990). This, combined with
barriers to spawning migrations, has probably led to localised population depletions.
The loss of riparian vegetation, leading to declining dietary sources of terrestrial
invertebrates, and increased sediment loads and subsequent loss of spawning habitat
may have also depressed successful recruitment for some populations.
16
Hypseleotris spp.
Common name: Carp gudgeons
Family: Eleotridae
Discovered by:
Hypseleotris spp. of the Murray-Darling Basin are a complex group of small fish.
While initially divided into western carp gudgeon (Hypseleotris klunzingeri Ogilby,
1898), Midgley’s carp gudgeon (Hypseleotris species one), lake’s carp gudgeon
(Hypseleotris species two), and Murray-Darling carp gudgeon (Hypseleotris species
three), recent genetic research indicates that they may in fact be a group of five
species, but capable of inter-breeding (Bertozzi et al. 2000). Murray-Darling Basin
Commission protocols require these species be classified as a group (Hypseleotris
spp.) until further work can elucidate the specific differences.
Collectively, Hypseleotris spp. have a Murray-Darling Basin-wide distribution, as
well as occurring in many coastal streams from central New South Wales to central
Queensland, the Bulloo River and Cooper Creek (Lake Eyre Basin). They are one of
the most widely distributed (Fig. 9) and abundant species (Table 4) within the
Macintyre-Dumaresq River system. They have also been widely translocated (Pusey
et al. 2004). They occur in a variety of lentic and lotic habitats. Although generally
considered to be a benthic species, they also occur in the water column over a range
of depths from 10 to 50 centimetres. They are found on sediments ranging from mud
to coarse gravel, usually associated with aquatic vegetation, leaf litter, undercut banks
or root balls (i.e.: structures that may afford protection).
Figure 9: Recorded distribution of Hypseleotris spp. in the Border Rivers region of
the Murray-Darling Basin, based on the ten datasets in table one.
Adults are tolerant of a wide range of water temperatures (eight to 32°C) being caught
in southern mountain streams and arid desert water holes. They are found in anoxic to
hyper-oxic water (0.6 to 13 mg.l-1), and in a range of turbidities (0.5 to more than 680
NTU) (Pusey et al. 2004).
Hypseleotris spp. are a short lived group (two to three years) of small fish (seven
centimetres, maximum). Adults are sexually mature by 12 months and spawning
occurs from spring to early summer in the Murray-Darling Basin when water
temperatures rise above 22.3°C (Anderson et al. 1961). Males establish a territory and
pair with a female. The adhesive eggs are attached to the underside of large gravel or
17
aquatic plants and are actively defended by the male during incubation (Cadwallader
& Backhouse 1983). Hypseleotris spp. are known to spawn during floodplain
inundation and this, coupled with an extended spawning season, may be regarded as
an adaptation to the unpredictable onset of the wet season flooding. Juveniles have
been caught in similar locations to the adults. Juveniles have been found in the lower
foothills zone of the Macintyre River in November 2005, in the absence of any natural
flow (Hutchison, pers. comm.). Hypseleotris spp. are a macrophagic carnivore,
feeding primarily on aquatic insects, microcrustaceans, and other macroinvertebrates
(Balcombe & Humphries 2006). Small scale mass migrations have been recorded in
coastal streams (Berghuis et al. 2000) where large aggregations have been observed
below instream barriers. However, these were postulated to be recolonisation
movements after downstream displacements by flood events.
Being a small fish, Hypseleotris spp. form a significant link in freshwater
trophodymanic webs. Although not considered to be threatened, their larvae are
susceptible to predation from alien fish species such as eastern gambusia (Gambusia
holbrooki). Also, being a periodically migratory fish (Hutchison – pers. comm.), they
would be susceptible to instream barriers to passage.
Leiopotherapon unicolor
Common name/s: Spangled perch, bobby
Family: Terapontidae
Discovered by: Günther 1859
Leiopotherapon unicolor are one of the most widely distributed freshwater fish in
Australia (Pusey et al. 2004), being found in coastal rivers from Geralton (Western
Australia), north and east to Newcastle (New South Wales), and inland in the MurrayDarling, Lake Eyre, Bulloo-Bancannia and Western Plateau drainage Basins. It is
found in a wide variety of habitats including desert springs, bores, billabongs,
impoundments, channels, rivers and streams. It is widely distributed within the
Macintyre-Dumaresq River system (Fig. 10), but is more abundant in the Macintyre
than the Dumaresq River (Table 4). Its distribution south is thought to be limited by
the 4.4°C isotherm (Lewellyn 1963). It is commonly found over muddy, sand and fine
gravel substrates in still to low velocity water bodies and can be found in ‘isolated’
water holes that may not have been connected to the main channels for many years. It
is usually associated with a benthic habitat, or in association with aquatic
macrophytes, large woody debris or root masses. It is a hardy fish capable of
tolerating a wide range of salinity (0.2 to .5.5 0/00), oxygen (0.4 mg.l-1) and turbidity
levels (1.5 to more than 680 NTU) (Pusey et al. 2004).
18
Figure 10: Recorded distribution of Leiopotherapon unicolor in the Border Rivers
region of the Murray-Darling Basin, based on the ten datasets in table one.
L. unicolor live up to five years and are sexually mature within the first 12 months.
They breed during the summer wet season cued by water temperatures rising above
20°C (Lewellyn 1963). Adults broadcast spawn over an inundated floodplain and the
eggs sink to the substrate. The larvae hatch within three days and are feeding within
four days of spawning. Juveniles metamorphose by 28 to 35 days of hatching (Pusey
et al. 2004). They are a highly predatory fish consuming a variety of aquatic
organisms and around 10 % vegetable matter (algae, aquatic macrophytes and
terrestrial vegetation). L. unicolor are one of the most active migratory freshwater fish
in Australia. They have been observed to travel up very small streams, leaping up to
one metre to surmount low instream barriers such as culverts. They are thought to
undertake both spawning and dispersal migrations (Pusey et al. 2004).
This fish is not considered to be threatened in the Murray-Darling Basin, but is known
to be of less abundance in regulated rivers when compared to unregulated rivers
(Gehrke 1996).
Maccullochella peelii peelii
Common name: Murray cod
Family: Percichthyidae
Discovered by: Mitchell 1838
This species was once widely distributed within the Murray-Darling Basin from the
upper Condamine River down to the lower reaches of the Murray River in South
Australia. However, over fishing and river regulation have led to a decline in
populations throughout its native range (Rowland 1989), although increasing numbers
have been recorded recently from the Queensland section of the Murray-Darling
Basin. It is widely distributed (Fig. 11) and reasonably common (Table 4) within the
Border Rivers region, but, as it is the target of a large stocking program, it is difficult
to tell if this is a result of natural populations, or the stocking programs. It is a large
fish growing to over one metre in length with historical records of it being more than
100 kilograms (Moffatt & Voller 2002).
This species is found in a range of habitats from small clear rocky streams in the
uplands of northern New South Wales to large turbid waterholes of the lowland
19
creeks and rivers. It prefers deeper waterholes with large woody debris, rocks or an
undercut bank. There is little information available about its environmental tolerances.
Figure 11: Recorded distribution of Maccullochella peelii peelii in the Border Rivers
region of the Murray-Darling Basin, based on the ten datasets in table one.
Being the largest freshwater fish in Australia, it is not surprising that Maccullochella
peelii peelii can live for more than 40 years, and that they take up to four years to
attain sexual maturity. In the southern Murray-Darling Basin, they spawn between
October and December, cued by water temperatures rising above 15°C (Koehn &
Harrington 2006). They are an annual spawner, but spawning success is closely linked
to high flow events during the breeding season (Rowland 1998). The mature adults
will migrate upstream some 80 to 100 kilometres into a small anabranch, forming
pairs that spawn adhesive eggs in hollow logs, on snags, under rocks or firm clay
(Moffatt & Voller 2002). The male will remain and guard the nest until hatching.
Larvae disperse downstream in the current, becoming active feeders 10 to 19 days
after hatching (Humphries 2005). Juveniles feed on zooplankton, aquatic insects and
small native fish such as gudgeons. Adults feed on other fishes, crustaceans and
molluscs (Harris & Rowland 1996).
M.p. peelii is threatened by several factors including over fishing, loss of spawning
habitat, inability to migrate past barriers, river regulation and cold water pollution
(Morris et al. 2001). In the mid 1800s to 1930s it was subject to over fishing by a
large commercial fishery, and post 1950s has been over fished by a recreational sector
that consider it to be the premier freshwater angling fish in eastern Australia
(Rowland 1989). Floodplain management since the early 1900s, with the construction
of weirs and dams, has severely inhibited the annual spawning migration, changed the
flow regime to water on demand into the irrigation industry, often leading to cold
water releases from dams that are detrimental to the survival of larvae (Todd et al.
2005), and reduced the frequency and magnitude of flooding, which has had a
detrimental effect on larval survival. Recent agricultural developments within the
floodplain environment have removed access to many anabranch sites for spawning
and removed many snags from rivers and creeks.
20
Macquaria ambigua
Common names: Golden perch, yellowbelly
Family: Percichthyidae
Discovered by: Richardson, 1845
Macquaria ambigua is widely spread throughout the Murray-Darling Basin, except at
higher altitudes and above large impoundments (Allen et al. 2002), and the Fitzroy
River in central Queensland. A separate species, Macquaria species B, occurs in the
Lake Eyre and Bulloo River catchments (Musyl & Keenan 1992). M. ambigua has
been widely translocated to many rivers and impoundments in south east Queensland
and northern New South Wales. They are widely distributed within the MacintyreDumaresq River system (Fig. 12) but appear to be much more common in the
Macintyre than the Dumaresq River (Table 4). Like cod, they have been extensively
stocked and this dichotomy of abundance may reflect stocking activity in Queensland
waters. They inhabit generally turbid, slow-flowing rivers, creeks, billabongs and
backwaters (Morris et al. 2001). They prefer deep pools containing cover such as
dead trees or fallen timber, undercut banks or rocky ledges (Moffat & Voller 2002).
They are reported to withstand temperatures ranging from four to 36°C and salinities
up to 330/00 (Merrick & Schmida 1984), oxygen levels ranging from three to 15 mg.l1
, and turbidity above 400 NTU (Pusey et al. 2004).
Figure 12: Recorded distribution of Macquaria ambigua in the Border Rivers region
of the Murray-Darling Basin, based on the ten datasets in table one.
Research from the middle Murray River region indicates that M. ambigua live for
more than 26 years, with males and females attaining sexual maturity in two and four
years respectively (Mallen-Coooper & Stuart 2003). They are active spawners from
October to March, cued by the addition of water to their environment, after water
temperatures have exceeded 23.6°C (Lake 1966a). This does not have to be a major
flood (King 2003), but inundation of dry ground leads to important plankton blooms,
which are used as food by the larvae (Lake 1966a). Larvae shoal up after four days
then disperse at five days and commence feeding on microcrustaceans, zooplankton
and aquatic insects (Cadwallader & Backhouse 1983). Juveniles and adults are
opportunistic carnivores, feeding on fish, shrimp and yabbies (Morris et al. 2001). M.
ambigua are macro-scale migrators, with adults travelling long-distances upstream
during high flow events to colonise habitats that are only occasionally accessible.
Juveniles and sub-adults make strong upstream dispersal migrations during spring and
21
summer, stimulated by rising water levels. Peak migratory behaviour is during
evening and early morning (Harris & Rowland 1996).
M. ambigua populations are threatened by loss of access to floodplains, unnatural
flows and barriers to migration. Weir and dams obstruct natural migratory paths to
isolated upstream water holes. Unseasonable water flows, released for irrigation, can
make the floodplain environment uninhabitable for larvae and juvenile M. ambigua,
which diminishes recruitment success (Morris et al. 2001).
Melanotaenia fluviatilis
Common name/s: Murray River rainbowfish, Crimson-spotted rainbowfish
Family: Melanotaeniidae
Discovered by: Castelnau, 1868
This small species (up to 90 millimetres, maximum) occurs throughout the MurrayDarling Basin in all catchments, but generally in the lowland areas (Allen 1996,
Moffat & Voller 2002). There is unpublished genetic work by Unmack (cited by
Morris et al. 2001) that suggests the Melanotaenia fluviatilis from the Paroo, Warrego
and upper Darling Rivers is actually the desert rainbowfish, M. splendida tatei (Zeitz
1896). However, Allen et al. (2002) consider M. splendida tatei to be confined to the
central desert areas and Lake Eyre Basin (Coopers Creek, Diamantina and Georgina
Rivers), and the central-eastern Barkley Tablelands of the Northern Territory.
M. fluviatilis is considered to be relatively abundant in much of the northern MurrayDarling Basin, but is declining in the Victorian and New South Wales regions (Allen
et al. 2002). It is both abundant (Table 4) and widely distributed in the Macintyre and
Dumaresq Rivers (Fig. 12). It is found in a wide range of habitats including rivers,
streams, billabongs, swamps and drains, preferring slow-flowing or still waters with
dense aquatic vegetation (Cadwalader & Backhouse 1983). This is the most southerly
ranging species of Melanotaenia and the only species adapted to cold winter
temperatures (eight to 28°C) (Allen et al . 2002). They have been caught in quite
turbid waters (0.5 to 528 NTU).
Figure 13: Recorded distribution of Melanotaenia fluviatilis in the Border Rivers
region of the Murray-Darling Basin, based on the ten datasets in table one.
This species lives for three years, attaining sexual maturity after 12 months. They
breed between October and January cued by rising water temperatures. Females can
22
spawn up to three to four times per day over several days. Adults pair for a single
spawning of up to 10 demersal eggs. Eggs adhere to aquatic plants and larvae hatch in
six to seven days. Larvae are carnivorous, aggregating near the water surface to feed
on zooplankton (Merrick & Schmida 1984). Adults feed on aquatic invertebrates and
terrestrial insects (Cadwalader & Backhouse 1983). Although not considered to be a
migrating species, large numbers have been observed to aggregate below weirs during
summer (M. Hutchison, pers. comm.).
The biggest threat to this species is the loss of aquatic vegetation, from riparian
disturbance, leading to erosion/siltation. Other factors include larval predation by
alien species such as the eastern gambusia (G. holbrooki). It is also possible that
instream barriers may prove to be a hindrance to re-colonisation of upstream habitats.
Mogurnda adspersa
Common name/s: Purple-spotted gudgeon, southern purple-spotted gudgeon
Family: Eleotridae
Discovered by: Castelnau, 1868
Mogurnda adspersa was once distributed in eastern coastal streams from central Cape
York, south to the Clarence River, northern New South Wales, and west into the
Murray-Darling Basin and some coastal drainages of South Australia (Pusey et al.
2004). Its range in the Murray-Darling Basin is now severely restricted to the upper
Condamine River, the Border Rivers region of Queensland-New South Wales and
patchy populations in the southern Murray-Darling Basin. It is listed as endangered in
New South Wales and critically endangered in Victoria (Morris et al. 2001). It is more
common to the upper foothills regions of the Dumaresq River (Fig. 14) than the
Macintyre River (Table 4). It is reported to be a shallow (10 to 60 centimetre) pooldwelling species commonly found in slow-flowing (less than 0.1 m.sec-1) weedy areas
(Briggs 1998). However, Moffat and Voller (2002) state M. adspersa are more
commonly associated with rock or cobble habitat in the Border Rivers uplands region
(higher than 200 metres a.s.l.).
Figure 14: Recorded distribution of Mogurnda adspersa in the Border Rivers region
of the Murray-Darling Basin, based on the ten datasets in table one.
It is tolerant of a wide range of temperatures (10.5 to 20°C) in the Murray-Darling
Basin (Briggs 1998), but able to cope with temperatures up to 32°C in south-eastern
Queensland (Pusey et al. 2004), and tolerant of low oxygen levels (0.6 to 12.8 mg.l1
). Although it can tolerate high turbidity (0.2 to 200 NTU) (Pusey et al. 2004) it
23
appears to prefer clear water (averaging 6 NTU). M. adspersa are tolerant of a wide
range of salinities and have been captured from uplands freshwater streams (840
metres a.s.l.), down to estuarine waters (Hansen 1988).
This is a small fish (up to 12 centimetres maximum) that lives up to four years of age.
It is mature at 12 months (Moffatt & Voller 2002) and spawns during the wet season
from November to April (Allen et al. 2002). It is a serial spawner, and, although
spawning cues are unknown, they are speculated to be rising temperature (more than
20°C) and photoperiod (Hansen 1988). Flooding is not essential to spawning (Larson
& Hoese 1996). Males are territorial, and establish a nesting site. Adults pair off and
the female lays between 100 to 1300 small adhesive eggs onto the hard substrate
(rocks, woody debris, broad-leafed aquatic vegetation). The male will fan and defend
the nest until hatching three to nine days later (temperature dependant). The diet of
juveniles (mainly zooplankton) and adults are reported to be similar (Allen et al.
2002), although prey size is obviously related to gape size. Prey consists primarily of
aquatic insects, terrestrial invertebrates, molluscs and other microinvertebrates (Pusey
et al. 2004). There is very little literature on their movements, although Pusey et al.
(2004) speculate that on the east coast, they may have a facultative mass dispersal
phase, although they are rarely reported from fishway studies.
The decline of M. adspersa in the Murray-Darling Basin has been correlated with the
invasion of eastern gambusia (G. holbrooki) by Wager and Jackson (1993). It is
highly likely that M. adspersa are also susceptible to instream barriers to dispersal
migration/recolonisation, and rapid fluctuations in water levels brought on by river
regulation during reproduction and recruitment. Riparian disturbance, causing
sedimentation, and loss of habitat may also influence recruitment success.
Nemotalosa erebi
Common name/s: Bony bream, bony herring
Family: Clupeidae
Discovered by:Günther, 1868
Nemotalosa erebi is the most widely spread freshwater fish in Australia (Pusey et al.
2004). It is found in coastal drainages from the Pilbara and Kimberly regions of
Western Australia, across the Northern Territory, including its arid interior, the arid
interior of South Australia, the Murray-Darling Basin and coastal Queensland rivers
as far south as the Albert River. In these areas it is an abundant species, one of the few
to thrive since European settlement (Moffatt & Voller 2002). It is found in a range of
habitats from saline lakes to lowland rivers and streams, billabongs and floodplains. It
thrives in impoundments and is only restricted from higher, cooler, fast-flowing
waters possibly because of an intolerance to lower water temperatures (Puckridge &
Walker 1990). It is a schooling species and, in the Murray-Darling Basin, is often
found in slow or still water commonly swimming in open water or near large woody
debris. It is widely distributed in the lowland and lower foothills zones of both the
Macintyre and Dumaresq Rivers (Fig. 15), but is much more abundant in the
Macintyre River (Table 4). It is tolerant of a wide range of salinities and temperature
(eight to 29°C), but is intolerant of low oxygen levels, being the first fish to perish
when ephemeral water bodies begin to dry out (Allen et al 2002). It has been found in
highly turbid waters (more than 600 NTU) in the Macintyre River (Hutchison, pers.
comm.).
24
Figure 15: Recorded distribution of Nemotalosa erebi in the Border Rivers region of
the Murray-Darling Basin, based on the ten datasets in table one.
Although usually a smaller fish (around 10 to 15 centimetres maximum) it is known
to reach more than 40 centimetres and eight years of age (Moffatt & Voller 2002). It
is sexually mature at two years of age and spawns in summer, irrespective of the
water level, with the onset of water temperatures rising above 18 to 20°C (Puckeridge
& Walker 1990). Spawning takes place in shallow still water such as sandy
embayments/backwaters. Eggs are scattered randomly and develop rapidly,
suggesting that larval survival is closely reliant on availability of phytoplankton
blooms. Adults are primarily detritiphores, but also consume algae, microcrustaceans
and aquatic insects. N. erebi are a highly migratory species, able to rapidly recolonise
habitat when conditions are conducive. They are one of the most common species
found traversing fishways (Mallen-Cooper et al. 1995, Pusey et al. 2004) but are
restricted to these migrations during daylight hours only. Their migrations are divided
into reproductive movements by adult fish and recolonisation movements by juvenile
and sub-adult fish.
N. erebi is not threatened in the Murray-Darling Basin. It is an important component
of the trophic web in any freshwater habitat within its distribution. Being highly
migratory, it is susceptible to barriers to migration, and conditions that lead to anoxic
water chemistry.
Philypnodon grandiceps
Common name: Flathead gudgeon
Family: Eleotridae
Discovered by: Krefft, 1864
Philypnodon grandiceps are a widely spread species, occurring in coastal drainages
from the Burdekin River in central northern Queensland to the Gawler River, South
Australia, Kangaroo Island and northern Tasmania. It is also patchy throughout much
of the Murray-Darling Basin (Pusey et al. 2004, Allen et al. 2002). It has not been
recorded in the Border Rivers region before the Murray-Darling Basin Commission
funded meso-scale movement project (Hutchison, pers. comm., Fig. 16), and is
considered to be extremely rare in this location (one record only, 83 millimetres TL).
P. grandiceps has been caught in a variety of lentic and lotic habitats including rivers,
streams, floodplain billabongs and wetlands up to 520 metres a.s.l. in the MurrayDarling Basin (Harris & Gehrke 1996). It is common to low gradient, moderate depth
25
pools (10 to 60 centimetres) and runs (less than 0.1 m.sec-1) in south-east Queensland
(Pusey et al. 2004) in areas with medium to course substrate and aquatic vegetation,
leaf litter, undercut banks or root masses. In the Murray-Darling Basin it is known to
frequent areas with fine substrate, lying motionless on the substrate, but capable of
rapid bursts of movement over short distances to avoid capture, or pursue prey
(Cadwallader & Backhouse 1983). It is tolerant of a wide range of water quality (11 to
31°C, 2.6 to 12 mg.l-1 D.O., 0.6 to 460 NTU) (Pusey et al. 2004).
Figure 16: Recorded distribution of Philypnodon grandiceps in the Border Rivers
region of the Murray-Darling Basin, based on the ten datasets in table one.
The maximum age and age at maturity of this small fish (less than 12 centimetres) are
unknown, but it breeds in freshwater mainly from mid-spring to summer, although
larvae are found from spring to autumn (Humphries et al. 2002). Spawning may be
cued by rising temperatures (higher than 18°C). Adults engage in elaborate courtship.
The adhesive eggs are deposited on a hard substrate such as rock or wood debris and
guarded by the male until hatching four to six days after fertilisation. Larval habitat is
unknown, but juveniles are common to runs and pools of regulated section of the
Campaspe River, north-west Victoria (Humphries et al. 2002), feeding on
microcrustaceans. Adult P. grandiceps are considered to be microphagic carnivores,
feeding primarily on aquatic insects, molluscs, and other macro-invertebrates.
Obligative dispersal migration has been recorded for this species by several authors
working in east coast streams (summarised by Pusey et al. 2004) and its use of larval
drift as a dispersal mechanism has led Humphries et al. (2002) to classify it as a
facultative potamodrous migratory species.
Although not listed as threatened, P. grandiceps is extremely rare in the Border
Rivers region of the Murray-Darling Basin, and has undergone reductions in
distribution in most other areas within the Murray-Darling Basin (Pusey et al. 2004).
Its survival is threatened by barriers to movement on key stages of its lifecycle, loss of
habitat to agriculture in lowland areas, and predation by alien/translocated species
(Pusey et al. 2004).
26
Retropinna semoni
Common name: Australian Smelt
Family: Retropinnidae
Discovered by: Weber, 1895
Retropinna semoni are a relatively widespread freshwater species in eastern and
southern Australia. It is found in coastal flowing freshwaters from central Queensland
to south-eastern South Australia and throughout the Murray-Darling Basin and Lake
Eyre Basin (Pusey et al. 2004). It is found in a wide range of macro habitats in both
lowland and upland zones and into the headwaters of streams in southern Victoria,
New South Wales and Queensland. It is widely distributed (Fig. 17) and relatively
common in the Macintyre and Dumaresq Rivers (Table 4). It is a species with a
preference for moving water microhabitats (0.2 to 1 m.sec-1) such as riffles/runs, often
observed in the shallow (less than 60 centimetres) slack-water eddies adjacent to high
energy discharge points (Harris & Gehrke 1996), but can also be found in abundance
in lakes. However, it is also found in inland lakes and impoundments such as dams
and weir pools. It is commonly found over intermediate to course-sized substrates
such as sand and gravel, often in association with submerged aquatic macrophytes and
filamentous algae. Being a pelagic schooling species, it is commonly found in the
upper portion of the water column (Hansen 1989), in open water during high
discharge and in close association with coarse substrates, aquatic vegetation and leaf
litter during low discharge or no flow. R. semoni is tolerant of poor water quality, but
intolerant to capture/handling (Moffatt & Voller 2002).
Figure 17: Recorded distribution of Retropina semoni in the Border Rivers region of
the Murray-Darling Basin, based on the ten datasets in table one.
It has been captured in waters with a wide range of temperatures (8 to 32 0C), low
levels of oxygen (0.6 to 16 mg.l-1), and high levels of turbidity (up to 680 NTU)
(Harris & Gehrke 1996).
R. semoni has been known to live for over four years, but is largely an annual species,
attaining sexual maturity in less than one year. Spawning can occur for over nine
months of the year in the Murray-Darling Basin, but peaks in winter and early spring
(Milton & Arthington 1985) during low and stable discharge periods when larvae and
juveniles have a greater chance of encountering high densities of small prey.
Spawning can extend into the summer months during periods of higher and variable
discharge (Humphries et al. 1999). Adhesive eggs are broadcast by the spawning
shoals of fish and adhere to aquatic vegetation and gravel substrate. R. semoni is
27
known to undertake short upstream migrations (Moffatt & Voller 2002), usually prior
to reproduction. Individuals have been recorded both descending and ascending
barrages on coastal Queensland streams (Stuart & Berghuis 1999). Generally there is
thought to be some facultative potamodry as a dispersal mechanism for juveniles and
sub-adults (McDowall 1996).
Tandanus tandanus
Common name/s: Eel-tailed catfish, Jewfish, freshwater catfish
Family: Plotosidae
Discovered by: Mitchell, 1838
This species enjoys a wide distribution along the east coast of Queensland from the
wet tropics of Cape Tribulation south to the Manning River of central-northern New
South Wales (Pusey et al. 2004). While once common throughout the Murray-Darling
Basin, it has undergone a decline in many southern parts of the Basin (Moffatt &
Voller 2002). Although this species is found in a wide range of habitats on the east
coast, in the Murray-Darling Basin it is thought to prefer turbid waterholes of the
lowland zones. It is widely distributed throughout the Macintyre and Dumaresq
Rivers (Fig. 18) and is common in the Macintyre and abundant in the Dumaresq
(Table 4). It is commonly caught near large woody debris during the daytime in pools
with abundant riparian vegetation, moving about the waterhole at night to feed. Along
the east coast, it is commonly found in waterholes with still or a slow moving current
(less than 0.2 m.sec-1), with sand or gravel substrates (necessary for its breeding
cycle) (Pusey et al. 2004). Adults are usually solitary, although juveniles are known to
aggregate into schools and frequent shallower waters than the adults.
Although some authors have reported a close association of this species with aquatic
vegetation in the Murray-Darling Basin, recent reports conclude that the significance
of this association is unclear and warrants further investigation (Pusey et al. 2004). T.
tandanus is tolerant of a wide range of temperatures (8.3 to 33.60C) and laboratory
experiments have shown that juveniles will survive short exposures to temperatures
down to 40C. This is a hardy species capable of surviving in low oxygen levels (0.3 to
16.1 mg.l-1) (Clunie & Koehn 2001), and highly turbid waters of the Murray-Darling
Basin (0.2 to 910 NTU).
Figure 18: Recorded distribution of Tandanus tandanus in the Border Rivers region
of the Murray-Darling Basin, based on the ten datasets in table one.
T. tandanus will live up to 15 years, attaining sexual maturity within three to five
years (Davis 1996a). The breeding season extends from spring to late summer with a
28
peak between January and March. Adults pair and build a nest in coarse sediments
(Davis 1996b). It is thought that rising temperatures are a primary trigger for
spawning behaviour, although rising water levels may also be a factor (Davis 1996c).
The males will guard the nest until the eggs hatch. It has been suggested that the time
of nest building and spawning coincides with stable conditions of low flows, but that
post hatching juveniles take advantage of floodplain inundation associated with late
summer flooding to access additional food resources (Davis 1996d). Adults are
thought to be generally sedentary, although there are reports of T. tandanus ascending
fishways in the winter months, and it has been suggested that these fish were
migrating back upstream after flood downstream displacement (Stuart & Berghuis
1999). Juveniles are probably more mobile than adults, being engaged in
dispersal/recolonisation movements (Reynolds 1983). However, the overall degree of
site fidelity shown by this species indicates their susceptibility to local populations to
anthropogenic disturbances. T. tandanus is primarily an opportunistic carnivore,
consuming aquatic invertebrates, fish, microcrustaceans and terrestrial invertebrates in
varying concentrations, depending on availability (Davis 1996c).
T. tandanus is listed as vulnerable in Victoria in the lower Murray-Darling Basin, but
not in the Queensland portion of the Murray-Darling Basin (Morris et al. 2001).
Survival of the species is threatened by a range of anthropogenic interactions
including introduction of alien fish that disrupt nests and prey on the eggs and larvae,
impoundments that flood suitable nesting habitat, draw-downs of impounded waters
that strand nests, irregular artificial flow regimes that disturb the breeding cycle,
riparian habitat destruction that increases siltation and decreases aquatic vegetation,
and de-snagging to increase stream flow (and decrease flood duration). Pusey et al.
(2004) have linked their basin wide decline to the development of water
infrastructure, while alien species introductions, agricultural runoff and riparian
destruction are linked to localised population declines. Clunie and Koehn (2001a - not
sighted) have prepared a recovery plan for this species.
Alien species
Carassius auratus
Common name: Goldfish
Family: Cyprinidae
Carassius auratus were first introduced into Australia in the 1860s as an ornamental
fish (Brumley 1996). They are now widespread in the Murray-Darling Basin.
Populations of C. auratus often establish in impoundments, building to substantial
numbers before declining after the stocking of predatory species such as Murray Cod
(Maccullochella peelii peelii), Golden Perch (Macquaria ambigua), and trout (Salmo
trutta and Onchorynchus mykiss), which consume large numbers of goldfish. They are
widely distributed in both the Macintyre and Dumaresq Rivers (Fig. 19) and common
in both river systems (Table 4). While usually found in warm, slow-flowing lowland
rivers or lakes, they are also found in association with freshwater vegetation and
slower-flowing areas of upland rivers and streams. They are tolerant of high summer
temperatures and low oxygen concentrations (Allen et al. 2002). They spawn during
summer with fish maturing at 100 to 150 millimetres in length. Eggs are laid amongst
freshwater plants and hatch in about one week. Their diet includes small crustaceans,
freshwater insect larvae, plant material and detritus (Brumley 1996).
29
Figure 19: Recorded distribution of Crassius auratus in the Border Rivers region of
the Murray-Darling Basin, based on the ten datasets in table one.
They have been linked to the introduction of 'Goldfish ulcer' disease in Australia, but
are otherwise considered a 'benign' introduction, with few or no adverse impacts
documented.
Cyprinus carpio
Common name/s: Carp, European Carp, Common Carp, Koi Carp
Family: Cyprinidae
Cyprinus carpiowere first introduced into Australia sometime between 1850 and
1870, but remained in two relatively confined locations (Sydney and the
Murrumbidgee Irrigation Area) until the early 1960s (Brumley 1996). These two
populations were different strains of the one species and showed no sign of spreading.
In the early 1960s a third strain, the Boolarra strain, was illegally introduced by a fish
farmer in Victoria. A large, but ultimately unsuccessful eradication program was
mounted and the Boolarra strain rapidly colonised watercourses throughout Australia.
A recent genetic study of C. carpio in Australia has identified a fourth strain (Koi) in
the ACT and Tasmania (Davis et al. 1998). C. carpio are present in the majority of
Murray-Darling Basin slopes and lowland rivers and creeks, and some upland streams
as well. They are widely distributed in the Macintyre and Dumaresq River systems
(Fig. 20) but are more common in the Macintyre than the Dumaresq River (Table 4).
They are usually associated with warm, slow-flowing lowland rivers or lakes and are
tolerant of a wide range of environmental conditions such as extremely low levels of
dissolved oxygen (Koehn et al. 2000).
30
Figure 20: Recorded distribution of Cyprinus carpio in the Border Rivers region of
the Murray-Darling Basin, based on the ten datasets in table one.
Males are sexually mature at two to three years (300 millimetres) and females at three
to four years (350 millimetres), and spawning usually occurs in spring and summer
when water temperatures are between 17 and 25°C. Spawning fish congregate in
shallow water to lay adhesive eggs in clumps on freshwater vegetation, logs and
submerged grass. The small eggs (0.5 millimetre diameter) hatch in two to six days,
depending on water temperature (Brumley 1996). C. carpio feed by 'mumbling' in the
sediment on the bottom or banks of water bodies. This involves sucking in sediment,
sorting the edible items from the inedible sediment, and expelling the sediment
through the gill openings. Dietary items include zooplankton, freshwater insect larvae,
crustaceans, molluscs and, to a lesser extent, plant material (Brumley 1996). C. carpio
are vectors of the parasitic copepod Lernaea sp., which infests a range of native and
alien fish species.
The impacts of C. carpio are not clear but their feeding behaviour has led to
considerable concern that C. carpio may be increasing turbidity levels in waterways,
and undermining river banks. Their high abundance in many streams and lakes
indicates they are probably competing with native fish for food and space.
Gambusia holbrooki
Common name/s: Eastern gambusia, Gambusia, Mosquitofish, Top Minnow, Plague
Minnow
Family: Poeciliidae
Native to rivers draining to the Gulf of Mexico, G. holbrooki were introduced into
Australia in the 1920s for mosquito control. Further introductions were made by
health authorities in the 1930s and the species was distributed to many military camps
during World War Two. The species is now widely distributed throughout Australia,
in farm dams, slow-flowing waters and shallow wetlands (Allen et al. 2002). They are
widely distributed throughout the Macintyre and Dumaresq Rivers (Fig. 21), but are
far more abundant in the Dumaresq River than the Macintyre (Table 4). G. holbrooki
have an affinity for peripheral margins of still or slow flowing waters, and in amongst
freshwater plants (McDowell 1996a). Their tolerance of a wide range of water
temperatures, oxygen levels, salinities and turbidity, coupled with their ability to
breed rapidly, has enabled them to densely populate many habitats, in the absence of
predators (Lloyd et al. 1986).
31
Figure 21: Recorded distribution of Gambusia holbrooki in the Border Rivers region
of the Murray-Darling Basin, based on the ten datasets in table one.
G. holbrooki mature at about 25 millimetres long, with the fertilised eggs developing
inside the female and live-born young being a few millimetres long at birth. Maturity
can be reached after only two months and individuals can breed several times a year
(Pen & Potter 1991). They are primarily carnivorous with the diet containing a range
of small freshwater invertebrates and wind-blown terrestrial insects (Pen & Potter
1991). While often referred to as Mosquitofish, mosquito larvae are only a minor
component of their diet.
They are an aggressive species and will chase and fin-nibble fish much larger than
them. They also prey on the eggs of native fish and amphibians. G. holbrooki are
implicated in the decline of at least nine species of native fish in Australia.
Perca fluviatilis
Common name/s: Redfin Perch, Redfin, English Perch, European Perch
Family: Percidae
Native to the cool-temperate waters of the Northern Hemisphere, Perca fluviatilis
were first introduced to Tasmania in 1862 and to Victoria in 1868. This species is
widely distributed throughout the temperate portion of the Murray-Darling Basin, but
absent from the Queensland portion of the Basin. They have been found in head
waters of the Dumaresq (Beardy River) and the Macintyre Rivers (NSW Severn
River), usually higher than 700 metres a.s.l., but have also been recorded from upper
foothill waters as low as 240 metres a.s.l (Fig. 22) during colder months of the year.
They are quite rare in these headwaters (Table 4) and only two records (data set two
only) exist from waters inside the proposed demonstration reach. Their distribution is
largely explained by their intolerance of temperatures higher than 31ºC (McDowell
1996). Adult P. fluviatilis are usually found in slow-flowing or still water habitats,
especially where freshwater plants are abundant.
P. fluviatilis generally mature after two to three years, but males may mature at the
end of the first year. Spawning occurs in spring when water temperature reaches
12°C, with thousands of two to three millimetre diameter eggs laid as gelatinous
ribbons amongst freshwater plants. Eggs hatch in one to two weeks and juveniles will
32
often form large schools (McDowell 1996b). Their diet includes crustaceans,
zooplankton and small native fish like eastern gambusia.
P. fluviatilis are a primary host for the Epizootic Haematopoietic Necrosis Virus
(Langdon 1989). This virus, unique to Australia, also affects Macquarie Perch, Silver
Perch and Mountain Galaxias (Galaxias olidus). P. fluviatilis are also a voracious
predator, consuming small native species such as carp gudgeons, juvenile Murray Cod
and juvenile Golden Perch.
Figure 22: Recorded distribution of Perca fluviatilis in the Border Rivers region of the
Murray-Darling Basin, based on the ten datasets in table one.
33
5.4 Information gaps in the biology/ecology of each species
There has been a large investment in research into the biology and life history of
many native fish, documenting the habitat requirements of several key species, such
as Murray cod and golden perch (Anon. 2004). This has led to further investment to
restore appropriate habitat, such as large woody debris (Crook & Robertson 1999,
Crook et al. 2001, Nicol et al. 2004, Bond & Lake 2005), reduce impediments to
passage through the construction of fishways on key barriers (Close & Aland 2001,
Gehrke et al. 2002, Stuart & Berghuis 2002, Baumgartner 2003, Koehn et al. 2003,
Koster 2003, Mallen-Cooper 2004, Baumgartner 2006), re-establish connectivity
between river and floodplain environments (Koehn & Nicol 1998, King et al. 2003)
and restore elements of the natural flow regime that trigger key life history stages,
such as migration and spawning (Koehn et al. 2003). However, there are still key
knowledge gaps in the specific biology and habitat requirements of many small native
fish species (Table 5). Some of the areas where knowledge is present for individual
species rely on inferred information gained for research into the same species, but in
locations outside the Basin. The utility of such information needs to be carefully
assessed as it may not be appropriate to infer that behaviour of populations occurring
in coastal tropical streams will be the same as populations occurring in semi-arid
Murray-Darling Basin waters. The knowledge base for alien species is also highly
patchy, depending on the species in question. It is important to understand the ecology
of alien species so that we can gain an insight of their overall impact on native fish
species in the Border Rivers region.
From table five, it is apparent that there are at least 11 of the 15 species that require
further information. They are the olive perchlet (Ambassis agassizii), the Darling
River hardyhead (Craterocephalus amniculus), the fly-specked hardyhead
(Craterocephalus stercusmuscarum fulvus), the River Blackfish (Gadpsis
marmoratus), the mountain galaxias (Galaxias olidus), the carp gudgeon complex
(Hypseleotirs spp.), the Murray-Darling rainbowfish (Melanotaenia fluviatilis), the
purple-spotted gudgeon ( Mogurnda adspersa), the bony herring (Nemotalosa erebi),
the flathead gudgeon (Phylipnodon grandiceps), and the Australian smelt (retropinna
semoni).
Key information gaps fall into two main categories: the need for migration; and
knowledge of their spawning, or nursery habitat. For many species, the habitat
requirements are unknown (Table 6). Of those that we do have knowledge about,
some require aquatic vegetation, or cobbles/gravel, or large woody debris for
spawning habitat. Several species are known to require access to backwaters, both
instream or on the floodplain, or amongst macrophyte beds for their larval habitat.
Some are known to require slow-flowing waters either amongst aquatic vegetation, or
off-stream in floodplain channels for juvenile habitat.
A second important information gap is the longitudinal linkages between the
egg/larval/juvenile/adult habitats (Table 7), and how individuals move between them
to complete their life-cycle. Some of this information is being addressed by a MurrayDarling Basin Commission funded project investigating meso-scale movement.
However, as this project is based in the lower foothills zone of the Macintyre River, it
is anticipated that some additional information will still be required from other
hydrographical zones, and from high flow (flood) years
34
2(3)
3
3
3
3
3
3
3
2(p)
3
2
3
3
2
3
3
Agassiz’ perchlet
Silver perch
Darling River hardyhead
Un-specked hardyhead
River blackfish
Mountain glaxias
Carp gudgeons
Spangled perch
Ambassis agassizii
Bidyanus bidyanus
Craterocephalus
amniculus
Craterocephalus
stercusmuscarum
fulvus
Gadopsis marmoratus
Galaxias olidus
Hypseleotris spp
Leiopotherapon
unicolor
Maccullochella peelii
Macquaria ambigua
3
3
3
3
2
2(3)
2(3)
2(3)
Physiological
Tolerances
2(3)
3
2
QMDC Macintyre River – Fish fauna characterisation
(Treadwell and Hardwick 2003)
Melanotaenia fluviatilis
2
3
3
Mogurnda adspersa
3
3
3
Nemotalosa erebi
3
Philypnodon
2(3)
2(3)
grandiceps
3
3
3
Retropinna semoni
Australian smelt
2
3
3
Tandanus tandanus
Eel-tailed catfish
Table symbols are:
3
indicates knowledge is recorded
2
indicates that knowledge is not recorded
2 (3) indicates that knowledge is known from studies outside the Murray-Darling Basin
3(no) indicates that knowledge is recorded, but the event does not happen
(p)
indicates patchy distribution
(r)
indicates restricted distribution
Cod
Golden perch
Murray-Darling
rainbowfish
Purple-spotted gudgeon
Bony bream
Flathead gudgeon
Adult
Habitat
2(3)
3
3
Good
Distribution
2
2
3(r)
Common Name
Species
2
3
3
3
QDPI&F
2
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
2
2
2
2
3
3
Spawning
habitat
2(3)
3
2
Reproductive
cues
2
3
2
2(3)
3
2(3)
3
3
2
3(no)
3(no)
2
3
2(3)
2
3
2
Migration
-
2
2
2
3
3
3
2
3
2
3
2
Larval
habitat
2(3)
3
2
Table 5: Summary of knowledge and gaps for native freshwater fish species present in the Border Rivers region of the Murray-Darling Basin.
35
2
3
3
2
3
3
3
3
2
3
3
3
2
Juvenile
habitat
2(3)
3
2
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
2
Diet
Juveniles found in shallow inchannel waters associated with
cover
Not yet recorded
Pelagic, drifting in benthic
habitats in main channel; not
recorded from floodplain
habitats
Demersal eggs dispersed over
shallow substrates & vegetation in
channel & across floodplain
Adhesive eggs laid on hard
substrates & inside hollow logs
Hypseleotris spp
Leiopotherapon
unicolor
Maccullochella
peelii
Shallow ponded areas & inchannel habitats during low
flows
Adult Habitat
In deep holes with habitats that provide high
levels of cover from woody debris, rocks,
undercut banks or overhanging vegetation
Forms shoals in turbid, slow flowing shallows
over substrates including bedrock, sand,
gravel & mud with cover from boulders &
aquatic vegetation
Found in rivers, billabongs, lakes, isolated
dams, bores & wells, also recorded from
ephemeral pools & across inundated
floodplains over substrates including bedrock,
sand, gravel & mud with cover from boulders
& aquatic vegetation
High mountain streams with fringing and
overhanging vegetation, gravel & boulders
Slow flowing pools with abundant cover from
woody debris & undercut banks and coble
open water at night
Shoals in moderate depth pools/runs with fine
sediment, usually in shallow, vegetated areas
Slow-flowing, clear waters of small creeks &
streams, in shallows or at surface, frequently
among aquatic vegetation
Slow/standing pools with nearby cover from
littoral macrophytes & woody debris
Shoals in slow/still water with fine sediment
substrate, close macrophytes & woody debris
QDPI&F
Juveniles found in shallow inchannel waters, similar to adult
habitat
Not yet recorded
Adhesive eggs laid in shallow
flooded backwaters amongst
macrophytes & woody debris
QMDC Macintyre River – Fish fauna characterisation
Not yet recorded - habitat likely
to be similar to adults, from
loose shoals in pools
Data deficient - habitat likely
to be similar to adults, from
loose shoals in pools
Adhesive eggs laid amongst
cobbles in riffle areas
Galaxias olidus
36
Not yet recorded
Silt/detritus substrate
Adhesive eggs laid in hollow snags
or spaces between boulders
Not yet recorded
Gadopsis
marmoratus
Not yet recorded
Adhesive eggs laid over rocks &
crevices/weedy areas
Craterocephalus
stercusmuscarum
fulvus
Not yet recorded
Floodplain & channel waters
Benthic habitats in
backwaters & floodplain
areas rich in zooplankton
Not yet recorded
Amongst aquatic vegetation in
main channel
Juvenile Habitat
Surface waters of tributaries
Larval Habitat
Not yet recorded
Adhesive eggs laid amongst fine
leaved aquatic vegetation
Semi-buoyant, pelagic eggs
released into water column near
surface in flooded backwaters of
low gradient streams
Spawning Habitat
Craterocephalus
amniculus
Bidyanus bidyanus
Ambassis agassizii
Species
Table 6: Habitat requirements for native freshwater fish species in the Border Rivers region of the Murray-Darling basin, recorded from the 10 data
sets outlined in table one.
Not yet recorded, but probably
similar probably to adults
Shoal in backwaters of
floodplain habitats, creeks &
weir pools, associated with
phytoplankton blooms
Slow flowing backwaters,
pools & littoral zones
Semi-buoyant eggs dispersed in
shallow sandy substrate backwaters
during floods
Adhesive eggs laid over hard
substrates rocks , woody debris,
broad-leafed aquatic vegetation
Adhesive eggs scattered over
macrophytes or gravel substrate
Eggs laid in circular nest in shallow
sand & gravel substrates
Nemotalosa erebi
Philypnodon
grandiceps
Retropinna semoni
Tandanus
tandanus
QMDC Macintyre River – Fish fauna characterisation
Backwaters & still littoral
habitats in main channels &
billabongs
Forms loose shoals over
gravel & mud substrate with
cover from macrophytes &
detritus
Not yet recorded
Not yet recorded
Adhesive eggs laid over hard
substrates, rocks , woody debris,
broad-leafed aquatic vegetation
Mogurnda
adspersa
Not yet recorded
37
Shoals near surface of still or slow flowing
waters in backwaters of large rivers, streams
& billabongs, with submerged vegetation,
woody debris & overhead cover
Amongst fringing vegetation & hard benthic
substrates in still or very slow flowing areas in
clear streams & off-channel habitats such as
large floodplain lakes, billabongs & small
terminal lakes
Forms shoals over muddy & vegetated littoral
zones in standing & flowing waters in main
channel & floodplain areas near large woody
debris
Slow flowing lowland reaches in shallow
littoral habitats with abundant submerged
cover from overhanging banks, woody debris
or vegetation
Shoals in large numbers in eddies of highdischarge points amongst coarse substrates
close to macrophytes
Solitary species in benthic habitats in lakes
and sluggish turbid streams in deeper holes
near leaf litter and woody debris with coarse
substrate and fringing vegetation
Warm, turbid slow flowing rivers, floodplain
lakes and anabranches often associated with
deep pools, woody debris & overhead cover
QDPI&F
Not yet recorded, but probably
similar to adults
Runs & run/pool interface
Not yet recorded, but probably
similar to adults
Shoal in shaded backwaters
& still littoral zones, near
surface
Adhesive eggs laid amongst
macrophytes
Melanotaenia
fluviatilis
Larvae are rarely observed
Macquaria
ambigua
Juveniles associated with slow
flowing backwaters, deep pools,
anabranches & inundated
floodplain habitats, amongst
woody debris
Pelagic eggs released in water
column near surface in-channel or
on floodplain
Data deficient - known to aggregate
below barriers during flows
No
Craterocephalus amniculus
Craterocephalus
stercusmuscarum fulvus
Gadopsis marmoratus
Data deficient
Data deficient
No
Philypnodon grandiceps
Retropinna semoni
Tandanus tandanus
QMDC Macintyre River – Fish fauna characterisation
Data deficient
Nemotalosa erebi
38
No
Data deficient
QDPI&F
Possible upstream dispersal movement in
spring - summer during increased flows
Possible upstream dispersal movement in
spring - summer during increased flows
Data deficient
Facultative dispersal movement in
drift
Data deficient
Non-spawning, within pool movement
recorded
Data deficient
Data deficient
juveniles may move upstream during
increased flows
Larvae move around in flood waters
Data deficient
Data deficient
Obligate larval drift downstream
during spring & early summer
Eggs & larvae swept downstream
Facultative upstream migration of some
individuals
Facultative long distance upstream
migration
Data deficient - known to aggregate
below barriers during flows
Data deficient
Data deficient
Facultative dispersal movement in
drift
Data deficient
Downstream dispersal of juveniles
Large scale movement unlikely due to
parental care
Large scale movement unlikely due
to parental care
downstream displacement of larvae
Data deficient
Data deficient
juveniles move upstream & downstream
during increased flows
Data deficient
Juvenile Migration
Data deficient
Data deficient
Larvae swept downstream
Data deficient
Larval Migration
Upstream migration
Mogurnda adspersa
Melanotaenia fluviatilis
Macquaria ambigua
Maccullochella peelii peelii
Leiopotherapon unicolor
Hypseleotris spp
Possibly undertake a compensatory short
upstream migration
Data deficient - known to aggregate
below barriers during flows
Data deficient
Bidyanus bidyanus
Galaxias olidus
Long upstream migration
Ambassis agassizii
Spawning Migration
Some evidence of off stream movement
during increased flows
Species
Table 7: Migration requirements for native freshwater fish species in the Border Rivers region of the Murray-Darling basin, recorded from the 10 data
sets outlined in table one.
5.5 The river continuum concept: a holistic approach to
understanding fish in rivers
To understand a river, we need to visualise the physical variables within a river
system as a continuous gradient of physical conditions between the headwaters and
the mouth (Vannote et al. 1980). Within any river, the biological element moves
towards a balance between a tendency for efficient use of energy inputs through
resource partitioning (food, substrate, etc.) and an opposing tendency for a uniform
rate of energy processing throughout the year, and downstream communities are
fashioned to capitalise on upstream processing inefficiencies.
Separate to, but contiguous with the river, are the floodplains. These are distinct
because they do not depend on upstream processing inefficiencies of organic matter,
although their nutrient pool is influenced by periodic lateral exchange of water and
sediments with the main channel (Junk et al. 1989). Thus, the position of a floodplain
within the river network is not a primary determinant of the processes that occur
within the stream, but the potential of the floodplain to add to the energy system of
the river is enormous. Any fish species that can access the floodplain energy sources
may derive significant advantage over instream restricted fish species.
This gives rise to the flood-pulse concept (Junk et al. 1989) where fish productivity is
strongly related to the extent of accessible floodplains (Arthington et al. 2005),
whereas the main river is used as a migration route by most of the fishes. In
Queensland, flood events are usually associated with summer and autumn rain, at a
time when temperatures are highest and drivers for productivity are maximised.
From the biological perspective, the river can also be viewed over a variety of scales
ranging from catchment (several rivers) to the individual river, to a reach within the
river, and down to the micro-habitat occupied by a particular fish species during a
particular phase of its life-cycle. Fausch et al. (2002) present a persuasive argument
for a holistic view of the river to understand how processes interacting across scales
set the context for stream fishes and their habitats. Ecological studies that focus on
fish in one environment only, may fail to identify the causal links to a declining
population. The recruitment bottleneck is a good example when habitat for adult fish
may be perfectly adequate, but access to juvenile habitat or spawning habitat may
have been lost or reduced in another part of the riverscape, leading to reduced
recruitment. Thus, a study focusing only on environments where the adults occur
could completely miss this crucial causal linkage. This idea is highlighted in
Schlosser’s (1991) dynamic landscape model for stream fish ecology. This model
comprises a holistic spatial arrangement of spawning, feeding, rearing and refugia
habitats and the necessity for movement among them for fish to complete their life
history. Thus, an awareness of fish biology and ecology, the need to move between
habitats and reaches, and knowledge of why these movements occur and their relative
importance is a fundamental step in understanding how to sustain or enhance fish
populations in a region.
Within the Murray-Darling Basin, some native species are able to complete their
entire life history without moving beyond a small home-range, e.g. river blackfish
(Gadopsis marmoratus), (Khan et al., 2004), two-spined blackfish (Gadopsis
bispinosus), (Lintermans, 1998) and mountain galaxias (Galaxias olidus) (Berra,
1963). However, most species need to move during their life history, (whether
QMDC Macintyre River – Fish fauna characterisation
39
between different instream habitats, the river and floodplain habitats, or long distance
movements), and impediments to movement and habitat loss can have a major impact.
Thus, it is important to know the habitat requirements for each stage of a fish’s life
history, the temporal and spatial requirements governing their need for movement,
and the key threats to their life-cycle. Such information can lead to informed
management decisions for developing reach restoration strategies. These have been
summarised by Treadwell and Hardwick (2003) and are presented below in Table 8.
Table 8: Key threats to each native fish species recorded from the Border Rivers
region of the Murray-Darling Basin (Treadwell & Hardwick 2003).
Species
Ambassis agassizii
Bidyanus bidyanus
Craterocephalus amniculus
Craterocephalus
stercusmuscarum fulvus
Gadopsis marmoratus
Galaxias olidus
Hypseleotris spp
Leiopotherapon unicolor
Maccullochella peelii
Macquaria ambigua
Melanotaenia fluviatilis
Mogurnda adspersa
Nemotalosa erebi
Philypnodon grandiceps
Retropinna semoni
Tandanus tandanus
Key threats
Loss of habitat (macrophyte beds), altered flow regimes and
possibly increased salinity and water temperatures.
Flow regulation, barriers to movement, cold water pollution, and
unknown impacts of stocking on the gene pool of remnant
populations
Reduced distribution due to habitat degradation
Loss of habitat and floodplain connectivity, barriers, thermal
pollution, increasing salinity of deflation basin lakes and predation
and competition for habitat from introduced fish species such as
carp, redfin perch and eastern gambusia
Habitat degradation, particularly de-snagging and sedimentation
that has reduced available cover and filled the interstitial spaces in
the cobble substrate, and introduced fish species such as trout
Predation by trout and sedimentation of spawning sites
Loss of aquatic vegetation as habitat and sites for egg attachment
and parasite infestation
Barriers to migration, reduced flow in rivers, loss of macrophyte
beds and cold water pollution
River regulation, barriers to migration and loss of critical habitat
are the major threats to Murray Cod. De-snagging has
significantly reduced the optimum habitat for cod in the Basin
River regulation, thermal pollution, flow alteration, barriers to
upstream spawning areas
River regulation, altered flows and competition from mosquito fish
Competition and predation by introduced species, increasing
salinity and loss of habitat
No major threats, although barriers to movement, impacts to
floodplain habitats, and cold water pollution may pose risks
Loss of habitat and limited information on the biology
Barriers to movement and predation from exotic species may pose
risks
Competition with Carp, loss of suitable breeding habitat, barriers to
movement and thermal pollution
The range of threats to the survival of native freshwater fish in Australia has been
documented by several authors (Kearney et al. 1999, Morris et al. 2001, Pusey et al.
2004, Barrett 2004b), and, from table eight, can be summarised into seven categories:
• flow regulation – causing loss of connectivity and access to critical habitat
(both instream and floodplain/anabranch habitat), and
reversal/loss of seasonality of flows;
• infrastructure – dams, weirs and crossings causing barriers to movement;
• loss of habitat – de-snagging, infilling from siltation, loss of shading and root
mass;
40
QMDC Macintyre River – Fish fauna characterisation
•
•
•
•
thermal pollution – cold water from dam releases and hot water from riparian
vegetation clearing;
increased salinity – caused by excessive land clearing, or raised water tables
from ground water sourced irrigation;
introduced fish – either alien or translocated species can cause excessive
competition or predation;
lack of knowledge – leading to ill-informed management decisions.
These can be addressed by rehabilitation/mitigation activities and are best aggregated
in a demonstration reach.
5.6 The demonstration reach concept and the ideal demonstration
reach length
The key concepts that define a demonstration reach are that it needs to promote
aquatic habitat rehabilitation, promote community interest and participation, have
well defined objectives at it’s start, and be viewed as a long-term commitment by all
stakeholders (Barrett 2004b). A successful demonstration reach has three key factors
that underlie its success. Firstly, it needs to comprise a suite of management actions
that collectively enhances the fish community. Secondly, when management actions
are strategically located between ‘good’ riverine habitat, they can lead to improved
riverine health on a much larger scale. Thus, it is very important to ensure that any
demonstration reach is of sufficient spatial and temporal scale to demonstrate a
quantifiable result. Thirdly, demonstration reach projects must be aimed at
community engagement and stewardship by integrating intervention actions with
community and stakeholder groups, and focusing funding agencies towards coinvestment for a better return on financial inputs.
To be successful, any demonstration reach program will have to be extensive in
duration (maybe 10 years or more), although some interventions such as riparian
rehabilitation may show a positive response after only one or two years. This is
because most benefits to fish populations may not be demonstrable in the short term,
but rather over a generational time frame of five to 50 years. This is not unexpected,
given the time frame of European occupation that has accompanied the decline in
native fish populations in the Murray-Darling Basin. To maintain this continuity,
demonstration reach programs need to be well organised and coordinated to ensure
that effective on-ground work is achieved and communication is targeted to multiple
interest groups. This will require substantial support by the local stakeholder groups,
as well as relevant regional NRM, State, and Federal agencies, both ‘in principle’ and
financially over the extended time frame of the demonstration reach project. The time
frame for any demonstration reach must be adequate to engender the public attitudinal
shift necessary to foster responsible stewardship of adjacent lands, to make the
necessary investment to achieve large spatial scale improvement of instream habitat,
and to allow the river system adequate time to respond to the intervention. Ideally, a
favourable response by a river system would be reflected in an ecologically balanced
increase in fish populations.
Demonstration reach rehabilitation actions cover a range of activities and a range of
social acceptance. These may include (in no particular order):
• riparian fencing to keep stock out, with or without limited crash grazing;
• off stream watering for stock;
QMDC Macintyre River – Fish fauna characterisation
41
•
•
•
•
•
•
•
•
•
•
•
woody weed control;
bank stabilisation to control erosion hotspots;
instream habitat complexity rehabilitation including rock/cobble and large
woody debris introduction;
alien fish removal/control;
fish passage enhancement such as fishway construction;
fish migration barrier removal;
restriction or removal of non-seasonal stream flow;
removal or restriction of seasonal flow harvesting;
negotiated allocation of impoundment water for environmental flow;
limited stocking of threatened species to re-establish viable native populations;
scientific research into establishing key restrictions to viable native fish
populations.
It is important to understand that no single intervention provides a panacea to
declining fish stocks. Rather, a range of actions will be necessary to achieve the
desired outcome. It is equally important to understand that each action has a cost,
socially, economically and environmentally. The willingness of user groups to accept
these costs varies according to the impact on particular groups.
The idealised demonstration reach length is very much dependant on the suite of
species present, both current and historically. Understandably, for smaller fish it will
be shorter, but for larger fish it may be much longer. To understand the individual
species requirements, we need to examine what habitat and movements are necessary
within the life-cycle.
Fish move for a range of reasons such as breeding, dispersal/ recolonisation, moving
to nursery habitats, foraging and parasite removal. Within the Border Rivers region of
the Murray-Darling Basin, there are at least 16 species of native fish (Moffat & Voller
2002), some of which have some aspects of their movement requirements well
documented (e.g.: Golden perch, Murray cod), but there are still large knowledge gaps
for the majority of native species, particularly small species (Treadwell & Hardwick
2003). Fishway monitoring has provided some information on upstream movements of
several, mainly larger, native species (Berghuis & Boradfoot, 2005 unpublished report)
but there is little information available on downstream (O’Connor et al. 2003, 2004,
2005) or lateral movement requirements, and limited information on small species or
juvenile life stages (Treadwell & Hardwick 2003).
The Queensland Murray-Darling Committee has proposed that the Macintyre River
demonstration reach should be in the Border Rivers region somewhere between the
lower foothills of the Macintyre River, near Toobeah, 69 kilometres west of
Goondiwindi, upstream into the Severn River (NSW) below Pindari reservoir, and into
the Dumaresq River, terminating at the junction of the Dumaresq River and Pike Creek.
This is a region in excess of 250 kilometres in river length.
The selection of a demonstration reach within this region is dependant on various
social, economic and environmental factors, but from a fish ecology and social point of
view this region has several beneficial aspects. It is contained within a single
geographical region (western slopes of the New England Tableland) and would provide
42
QMDC Macintyre River – Fish fauna characterisation
very good public access to key ‘hotspots’ along the demonstration reach length. Some
of these hotspots are reviewed in section 5.6.
There are three species of fish, present in the proposed demonstration reach that
undertake large-scale migration during their life history. These are the silver perch
(Bidyanus bidyanus), the Murray cod ( Maccullochella peelii, peelii), and the golden
perch (Macquaria ambigua). Silver perch are known to undertake a long pre-spawning
migration in summer, to areas behind the peak of a flood (Reynolds 1983), provided
that there are no barriers to that migration. Mature Murray cod will migrate upstream
some 80 to 100 kilometres into a small anabranch, forming pairs that spawn adhesive
eggs in hollow logs, on snags, under rocks or firm clay (Moffatt & Voller 2002). The
male will remain and guard the nest until hatching. Adults will often return
downstream to their ‘territory’. Golden perch have been recorded to migrate over
large distances in excess of 1000 kilometres (Reynolds 1983). However, a recent
study in the Murray River indicated that only a small proportion of fish undertake
such extensive migrations, usually associated with spring spawning behaviour, and
many Golden perch return to a ‘home range’ (O’Connor et al. 2005).
There is insufficient data for most of the other species present in the Border Rivers
region. As most of these are smaller fish than the three highly mobile species
described above, it is highly unlikely that any would require extensive longitudinal
distances to complete their life-cycle. Rather, it is the presence or absence of critical
habitat over a short spatial scale that would be a key influence to their population
success. It is quite conceivable that most of the species present in the Border Rivers
region could be accommodated within a shorter demonstration reach project of some
30 to 50 kilometres in length, provided that adequate habitat exists or can be
rehabilitated. However, there is still a concern about adequate offstream access.
Many smaller species require access to either instream or offstream backwaters for
some of their life-cycle. Both the habitat and access have diminished with the advent
of flow regulation and strategies addressing this issue must be considered if we are to
adequately accommodate the full suite of native freshwater fish present in the Border
Rivers region of the Murray-Darling Basin.
5.7 Review of sites on the proposed demonstration reach
During late March, the author of this report, the Native Fish Strategy Coordinator for
Queensland, and a representative from QMDC travelled through the Macintyre Brook,
Dumaresq and Macintyre River valleys between Bonshaw, northern New South
Wales, and Toobeah on the New South Wales-Queensland border. The following
observations were made during this ground-truthing site visit, supplemented by
comments from a DPI&F report on Fish Barriers in the Queensland section of the
Murray-Darling Basin (Piltz – unpublished).
Dumaresq River
The Dumaresq River is a tributary of the Macintyre River. Beginning in the uplands
near Sundown National Park, the river flows southwest where it defines the states
border, and joins the Macintyre River near the town of Yelarbon. Major tributaries of
the Dumaresq River include the Mole and Severn (QLD) Rivers and Pike Creek. This
system is considered by DPI&F fishway officers to be of importance to fish migration
because of the low number of significant barriers throughout a larger portion of the
system.
QMDC Macintyre River – Fish fauna characterisation
43
However, a major installation, Glenlyon dam (254,310ML), on Pike Creek was built
to deliver water ‘on demand’ down the Severn and Macintyre Rivers for the irrigation
industry. Water from this dam is delivered via an off-take located at the bottom near
the dam wall and can be delivered at up to 1000ML per day for irrigation purposes.
There is some evidence that releases up to 350ML per day may cause cold water
plumes for some 30 to 40 kilometres downstream (Glenn Wilson – pers. comm.).
Water delivered at 1000ML will impart a cold water plume much further downstream
and may have significant impact on native fish, especially during critical periods such
as spring (rising water temperature) when such cold water plumes may negatively
influence spawning success. This water could also interfere with natural water levels
in critical habitat such as egg laying sites and backwater nursery areas during critical
periods in the life history of native fish.
The Bonshaw weir is located 126 kilometres upstream of the Dumaresq-Macintyre
Rivers junction, just outside Bonshaw (NSW). It is a stepped construction built upon a
rocky base (Fig. 23). Rocky areas protrude from the riverbed at the base of the barrier,
dividing the immediate downstream pools. Approximately 10 to 40 metres below the
weir is a smaller timber barrier, which is in disrepair, which diverts water in several
directions. A culvert road crossing has been installed across the river 50 metres
downstream from the base of the barrier. Riffles and deeper pools are continually
linked further downstream (Fig. 24) with good instream habitat including,
rocky/gravel beds, fallen timber and overhanging trees. Some silting was evident
directly above the weir, but this was not excessive. The riparian vegetation above the
weir is only a thin strip, but is in a satisfactory state. The habitat includes fallen trees,
overhanging vegetation and steep banks throughout the reach (Fig. 25). This region
had good grass cover and no significant erosion was noted, indicating good bank
stabilisation.
Figure 23: The stepped Bonshaw Weir (left), with rocky base
and timber barrier (right), in disrepair, diverting the
water in several directions.
44
QMDC Macintyre River – Fish fauna characterisation
Figure 24: Riffle and deeper pools downstream of Bonshaw Weir (photo –Piltz)
Figure 25: Thin strip of riparian vegetation lines the upstream reaches, with
instream woody debris.
Carp were observed in the downstream pool of the Bonshaw weir, and the site would
benefit from programs to remove alien fish. The riparian vegetation on both sides of
the weir pool is in good condition, but very thin and may not be an adequate source
for future instream large woody debris (Fig. 25). It would benefit from some riparian
rehabilitation to improve the density of this buffer. The south bank is setup as a
camping reserve and would provide good public access. Immediately downstream of
the weir, the banks are poorly vegetated and would benefit from some rehabilitation.
Depending upon further investigation into the river’s hydrology, a rock ramp fishway
appears to be the most appropriate infrastructure to facilitate fish passage over this
weir. This could be designed to circumvent the first downstream pool, avoiding
backwater habitat more suited to invasive pest species such as carp.
Myall Creek joins the Dumaresq River three kilometres downstream of Bonshaw.
This area is a stock reserve with creek access for watering. Myall Creek is mostly dry
QMDC Macintyre River – Fish fauna characterisation
45
with several semi-permanent watering holes. It has sections of reasonable riparian
vegetation, but does exhibit areas of severe bank erosion from cattle access to
watering points. These have led to instream sediment slug development. It would
benefit from establishing off-stream watering points for transient stock and riparian
rehabilitation.
Between Bonshaw (NSW) and Yelarbon (QLD) is a typical rural property adjacent to
the Dumaresq River. Like many properties that abut the river, the occupants harvest
water for stock and irrigation. The steep southern bank is mostly well vegetated, but
has been cleared almost to the change in slope (Fig. 26). The northern bank is much
flatter and vegetation has been ‘thinned’ to facilitate grass development for stock
feed. Where the riparian buffer zone has been cleared too close to the bank, signs of
erosion exist, and there is evidence that the landholder has identified this as a
potential problem and attempted to address this by dumping chopped vegetation into
the void (Fig. 27). This site would be of particular concern to the landholder as it is
adjacent to his pump shed. Carp were observed feeding on the substrate in the long
waterhole downstream of the pump.
This site, like many others along the river banks, would benefit from an intensive
riparian rehabilitation program to control erosion and stabilise the bank, and some
carp control. However, unlike several other sites, this site has good public access, and
provided access can be negotiated, would prove a good demonstration reach action
site.
Figure 26: Typical river banks of the Dumaresq, steep on one
side and gentle on the other. Note openness of
northern bank, and gravel substrate.
46
QMDC Macintyre River – Fish fauna characterisation
Figure 27: Grazier instigated erosion control (chopped
branches, tin and wire) on steep southern bank of
Dumaresq River.
Downstream of the Bonshaw weir is the Cunningham Weir, approximately 68
kilometres upstream of the junction between the Macintyre and Dumaresq Rivers. It is
a 4.6 metre barrier, constructed from a variety of materials ranging from timber, rocks
and metal sheeting (Fig. 28). As a weir, this structure is of questionable integrity as
there is water passing through the structure in many locations. However, it is still a
significant barrier to fish migration. The weir pool is long (more than two kilometres)
and utilised by landholders for stock watering and irrigation. The banks are well
vegetated and appear to be stable except in several points where stock access water.
At these locations the banks are eroding and sediment slugs have filled in the stream
bed.
Below the barrier is a large pool, about two to three metres deep, which shallows a
further 60 metres downstream. This pool contained large schools of adult bony bream,
rainbow fish, carp gudgeons and harydheads, as well as carp and eastern gambusia.
Below the pool is a road crossing constructed from culverts (Fig. 29); the water
deepens beyond this into adjoining pools. The riparian vegetation adjacent to the
culvert is in moderate to poor condition, but the instream cobble appears to have
prevented significant erosion and stream bed infill.
QMDC Macintyre River – Fish fauna characterisation
47
Figure 28: Cunningham Weir leaking through the wall in several
locations, and the downstream pool.
Figure 29: Downstream road crossing and culvert at Cunningham Weir (photo – Piltz)
Located at a major road reserve between Yetman (NSW) and Yelarbon (QLD), the
Cunningham Weir has good public access. The weir is a substantial structure (4.6
metres high) and of questionable integrity. If the owners of the structure were to
upgrade this facility, it would present a good opportunity to build a vertical slot
fishway to facilitate fish passage. Both the weir and downstream pools would benefit
from introducing habitat complexity via large woody debris. The downstream banks
are highly degraded, but appear stable. They would benefit from riparian
rehabilitation as this would supply future demand for stream shading and habitat
complexity.
A further 11 kilometres downstream of Cunningham Weir is the Glenarbon Weir (Fig.
30 - not sighted). It has a non-functional fishway installed (Fig. 31 - not sighted),
which is a pool pass structure (Piltz – pers. comm.). At the base of the barrier on the
48
QMDC Macintyre River – Fish fauna characterisation
right hand side, outlet works are running over a rocky area as shown. The pool
downstream does not appear to be disjointed and contains good quality habitat such as
rock cobble areas throughout the riverbed.
The riparian vegetation both up-stream and downstream, which includes canopy cover
and good under-story preventing erosion, was in fair condition. Above the weir the
instream habitat, including fallen trees, aquatic and overhanging vegetation (Fig. 32 not sighted), was plentiful. No silting was obvious directly above or below the barrier.
Figure 30: Glenarbon Weir with a fishway (photo – Piltz).
Outlet
Figure 31: Down stream pool at Glenarbon Weir showing the fishway outlet (marked)
and the quality of habitat (photo – Piltz).
Further fish survey work and hydrology detail would be required to ascertain if fish
passage is necessary at the Glenarbon Weir, but DPI&F fishway officers felt that a
rock-ramp fishway would be best suited for this weir, in place of the existing but nonfunctional vertical-slot fishway, as structure height is not great. Additional works
QMDC Macintyre River – Fish fauna characterisation
49
would involve riparian rehabilitation and probably alien fish removal (carp buster
program).
Figure 32: Instream habitat (fallen trees) upstream of Glenarbon
Weir (photo – Piltz).
Dumaresq River Summary
The Dumaresq River locations surveyed all possessed essential riparian and instream
habitat, with variation in structure types. All these sites were typical of an upper
foothills zone river, with nearly continuous water flow, good water clarity, and a
stream bed largely of cobble and gravel. It is one of the few areas in the Queensland
portion of the Murray-Darling Basin where dense aggregations of aquatic
macrophytes occur. However, this is a regulated river with the 253,000ML Glenlyon
Dam located on a major tributary, Pike Creek. Water releases from this dam are
thought to contribute cold water pollution for many tens of kilometres downstream
and interfere with flow heights during critical stages of native fish life history. Several
other tributaries such as the Mole and Severn (QLD) Rivers, and Tenterfield Creek
are unregulated and are a source of natural flow. If the three minor barriers were to
have fish passage infrastructure installed, it would open up 240 kilometres of water
that fish could navigate, taking the open water up to Nundubbemere Falls. Carp have
been observed near all three weirs and any project to install fish passage on either of
these weirs would also require a concurrent alien fish removal programme.
Various forms of disturbance were noted at all sites along the Dumaresq River,
including cattle trampling of banks, removal of riparian vegetation, and erosion
gullies leading to some instream sediment slugs. However, the over-all river health
appears to be in good condition with modification of important habitats remaining at
minimal levels. This is also an attractive river for public access with dedicated
camping reserves established at many points with good all weather access.
Macintyre Brook
The Macintyre Brook is a tributary of the Dumaresq River, branching approximately
five kilometres south of Yelarbon, and running in a north-easterly direction east of
Inglewood. It contains four major barriers along the 80 kilometre stretch of river
below the 75,000ML Coolmunda Dam. This dam is recognised as an eastern border to
50
QMDC Macintyre River – Fish fauna characterisation
the region where a demonstration reach could be established. There are two main
reasons for this. Firstly, at 16 metres in height, it would be difficult to facilitate fish
passage past Coolmunda Dam wall. Secondly, because there are no reports of alien
fish above this barrier, it may be best if no fish passage above the dam wall was built.
Inglewood Weir (not sighted – refer to Piltz report) is approximately 25 kilometres
downstream of the Coolmunda Dam wall. This is a concrete structure (Fig. 33)
developed to supply water to the township of Inglewood. On one side, the weir pool
banks are stable, but open to provide an amenity to an adjacent golf course. On the
other side bank disturbance is medium due to the presence of agricultural practices on
adjacent land, although riparian vegetation is in fair condition with little to no erosion
being present on the steep banks. There is little silting in the weir pool, except closer
to the bank, which is covered with reeds and other macrophytes. Instream habitat is
notable and varying, including aquatic plants, fallen timber and overhanging
vegetation.
Figure 33: Inglewood Weir (photo – Piltz).
Downstream of the weir is a 10 metre long pool that has been filled in by silting, and
then a culvert road crossing. Immediately below this road crossing, a riffle zone has
been created due to a bottleneck resulting from the culvert. This area has good
riparian vegetation providing shading, and complex instream habitat. Riffle zones,
pools at various depths and aquatic plants are all present, as well as other diverse
habitats, although some silting is evident on the southern side.
QMDC Macintyre River – Fish fauna characterisation
51
Figure 34: Riparian and instream habitat downstream of Inglewood weir (photo – Piltz).
The Inglewood Weir has good public access and would benefit from a riparian
rehabilitation program. This would ensure the future supply of large woody debris for
instream habitat complexity. Fish passage could be achieved by either a rock-ramp or
a vertical slot fishway. This would depend on hydrology information, the close
proximity of the road-crossing downstream, and the silting at the base of the structure.
Whetstone Weir (not sighted), a further 16 kilometres downstream of Inglewood
Weir, is a five metre structure of timber pylons and rails, and has been packed with
gravel and rock (Fig.35). The sides have been secured by concrete pads. The weir
pool has good riparian vegetation and instream habitat (Fig. 36), although there is
some bank vegetation disturbance. Bank stability is in good condition with no erosion
or silting being noted upstream of the weir.
At the base of the weir structure is a large 40 metre pool of variable depth up to 2.5
metre, and below this pool there is a concrete road crossing (Fig. 37), with five square
channels under the road. This enables suitable downstream flow with the possibility
of allowing adequate passage for fish, although light penetration appeared poor.
52
QMDC Macintyre River – Fish fauna characterisation
Figure 35: Whetstone Weir on Macintyre Brook (photo – Piltz).
Figure 36: Whetstone Weir pool on Macintyre Brook (photo – Piltz).
Figure 37: Road crossing below Whetstone Weir (photo – Piltz).
QMDC Macintyre River – Fish fauna characterisation
53
Numerous riffle zones are present downstream of the road crossing (Fig. 38), along
with a quantity of deeper pools at various depths. The instream habitat and riparian
vegetation is in good condition, including large woody debris, rocks, gravel beds and
aquatic vegetation.
Figure 38: Downstream of Whetstone Weir road crossing with good stream
habitat (photo – Piltz).
This region of Macintyre Brook represents some very good habitat. Water turbidity is
not quite as low as similar regions on the Dumaresq River, but riparian zones and
instream habitat complexity is good. Fish passage is a problem and considerable
structure refurbishment may be required as much of the Whetstone Weir main
structure is in fair to poor condition. A vertical slot fishway would be the most
appropriate structure for this weir as the barrier is five metres high (Piltz – pers.
comm.).
A third weir, Ben Dor, occurs some 19 kilometres upstream of the Macintyre BrookDumaresq River junction. At 5.6 metres in height, it is a significant barrier to fish
movement. This site has not been surveyed.
Some 10 kilometres upstream of the Macintyre Brook-Dumaresq River junction is the
1.2 metre high Sunny Girl Weir (not sighted). This is a privately owned structure built
of timber posts and rails (Fig. 39). Water is constantly being released via gaps
throughout the length of the weir. Tall grasses, trees and debris are across the length
of the barrier. Upstream riparian vegetation is in very good condition with no visible
sign of silting or erosion (Fig. 40). The riparian vegetation is notable with ample overhanging trees and bank cover, while instream aquatic vegetation and timber habitat
are diverse and complex. This reach of river varies between 30 to 40 metres wide with
significant depth throughout.
54
QMDC Macintyre River – Fish fauna characterisation
Figure 39: Sunny Girl Weir downstream of woody debris crossing the water
body (photo Piltz).
Figure 40: Sunny Girl Weir pool (photo – Piltz).
Downstream of the barrier is a long pool (about 20 metres by five metres)
approximately 1.5 metre deep in places and terminating at a road crossing (Fig. 41).
This crossing has good flow and light penetration under the bridge. The riparian
vegetation is in excellent condition with no silting or erosion. Instream structures
include rocky areas, over-hanging vegetation and fallen timber.
QMDC Macintyre River – Fish fauna characterisation
55
Figure 41: View of Sunny Girl Weir from road crossing downstream (photo – Piltz).
This area provides a good example of integrating adjacent agricultural practices with
good stream stewardship. The barrier itself is in disrepair and significant
refurbishment would be required if fish passage infrastructure, such as a rock ramp
fishway, was to be built on the barrier.
Macintyre Brook Summary
Macintyre Brook provides a good potential reference zone for the demonstration
reach project. Although smaller in size than either the Dumaresq or Macintyre Rivers,
it is generally in less disturbed condition. It is within a similar hydrological zone to
the Dumaresq and Macintyre Rivers (upper foothills) and has only four barriers, all
within 44 kilometres of each other. Fish habitat throughout this stretch of river shows
little evidence of human influence (other than weir installations and some recreational
fishing activities) compared to the other catchments. The habitat along this system is
both diverse and complex and the brook provides significant potential for natural fish
populations. Although Macintyre Brook is not of great length, the appropriate fish
habitat is substantial, enhancing native fish species’ chances of recruitment for the
whole catchment. One drawback is the downstream extent of cold water pollution
from Coolmunda Dam.
Macintyre River
The Macintyre River runs from Mt Rumbee, south-west of Glenn Innes, west through
Inverell, and north-west through Wallangra before being joined by the Severn River
(NSW) near Wallangra, and then the Dumaresq River some 25 kilometres east of
Goondiwindi. Pindari Dam is located on the Severn River (NSW) between Ashford
and Emmaville. Although it is a deep dam of 322,000ML, and capable of delivering
up to 3000ML per day, it has multiple off-takes at various depths and thus cold water
pollution is not such a significant issue with this dam as in other rivers, except during
blue-green algal blooms, when bottom water is mixed with surface water to dilute the
bloom. However, flow regime changes can occur when out-of-season irrigation flows
56
QMDC Macintyre River – Fish fauna characterisation
are released that do not coincide with natural flows. These can impact on native fish
access to critical habitats.
Much of the Macintyre east of Wallangra is in the uplands zone (more than 600
metres a.s.l.). Below Wallangra it conforms to an upper foothills category (Moffat and
Voller 2002), and then to lower foothills west of Yetman to the western border of the
proposed demonstration reach at Toobeah (65 kilometres west of Goondiwindi). In
the uplands zone, it is typical of many rivers in the region, having nearly continuous
cool, clear water flow, with abundant over-hanging vegetation and diverse and
complex instream habitats, such as large woody debris, rocks, cobbles, deep pools,
riffles and runs, and deep pools. Aquatic vegetation is not common.
There are numerous areas between Wallangra and Yetman where the Macintyre River
conforms to the typical upper foothills habitat, having pools and riffles similar to the
uplands, but a greater predominance of cobble and gravel substrate. Aquatic
macrophytes are common and riparian vegetation is both dense and diverse. However,
there are also large tracts of river that pass through agricultural land. In some of these
areas the riparian vegetation has been cleared for grazing and agricultural purposes. In
these areas, the banks exhibit severe signs of erosion from stock access to watering
points. Instream habitat is simplified due to infill from siltation and water turbidity is
high. The area suffers from infestations of large woody weeds, such as willow, privet,
blackberry and osage orange.
Further downstream into the lower foothills zone of the river between Goondiwindi
and Yetman there are two major barriers and a common theme in land use. This zone
has shallow and deep pools intermittently connected during flow events. The banks
are predominantly clay and mud, while the bottom is usually covered in silt or sand
with the occasional rock bar. The water is highly turbid (Fig. 42). Riparian buffers do
exist, and can be more than 50 metres thick (Fig 43). Adjacent land use is almost
entirely agricultural and banks show periodic signs of erosion and impact from stock
access (Fig. 44). Instream habitat is often compromised by siltation, although in many
areas there is an abundance of large woody debris. The two large barriers,
Goondiwindi and Boggabilla Weirs, form significant barriers to fish migration. While
fishways have been built on both, recent surveys question the efficacy of each to fish
passage (Berghuis – pers. comm.). Recent surveys below the Goondiwindi Weir have
also found aggregations of rainbow fish, bony bream, hardyheads and gudgeons, as
well as carp, golden and spangled perch. It is thought that smaller native fish have
great difficulty negotiating this barrier.
QMDC Macintyre River – Fish fauna characterisation
57
Figure 42: Highly turbid waters of Macintyre River.
Figure 43: Riparian vegetation on the Macintyre River ranges from over 50
metres thick (left) to narrow, or absent (right).
58
QMDC Macintyre River – Fish fauna characterisation
Figure 44: Signs of erosion and stock access on the bank of the
Macintyre River.
Macintyre River Summary
This river has several attributes that lend it to a demonstration reach. The river
traverses a range of hydrological zones from the uplands to the lower foothill regions.
Within these zones there are areas with good riparian habitat and adjacent highly
disturbed areas. The river has a well documented suite of native fish fauna, and is
very accessible by the public in key areas. There are some fish migration barriers in
need of remediation and these are located near major population centres.
There is evidence of local public interest in rehabilitation in the area, such as the
Yetman Fishing Club’s submission to round five of the NSW Recreational Fishing
Trust for a fish rehabilitation program. This application is for work in the Macintyre
River catchment near Yetman. The Yetman Fishing Club, in collaboration with the
Border Rivers-Gwydir Catchment Management Authority plan to revegetate two
kilometres of riparian habitat, manage woody weed infestations, protect 200 metres of
bank from soil erosion, develop various recreational fishing infrastructure and
signage, hold a carp buster program and build a boat ramp.
There are several factors that detract from the Macintyre River as a demonstration
reach site, such as the two major barriers to fish migration and non-seasonal irrigation
flows. This river would benefit from programs to remove alien fish.
QMDC Macintyre River – Fish fauna characterisation
59
6.
Recommendations on the suitability of sites on the
Macintyre and Dumaresq Rivers, and Macintyre Brook for
demonstration reach and control
The Macintyre River presents a good candidate for a demonstration reach. It contains
several key physical attributes that would inhibit fish population enhancement, but
these could be overcome with strategic investment. It meets several of the
demonstration reach criteria, including interest from local groups and regional NRM
groups (Queensland Murray-Darling Committee and Border Rivers-Gwydir
Catchment Management Authority). The proposed reach is large enough to
accommodate a range of management interventions, which would be adequately close
to major urban centres, and have good public access to ensure that any benefits would
be highly visible. The expectation of a positive impact on both fish populations and
stream habitat is realistic. The relevant state government body has indicated an
interest in developing a demonstration reach in the region.
Macintyre Brook presents an interesting case as a reference site. While the riparian
and instream habitat are generally in excellent condition, it does have at least four
significant barriers to fish migration, there are issues of cold water pollution, and
there is little information available regarding the fish fauna abundance and diversity.
These issues would need to be addressed before any demonstration reach program
could proceed to use this as a reference site.
The Dumaresq River also presents an interesting mix of attributes as a demonstration
site. It contains many examples of suitable habitat for a control site, but this is heavily
confounded by a significant upstream impoundment (Glenlyon Dam), three
downstream barriers (discussed in section 5.6), and the release of cold water for
irrigation harvesting. These issues, while not adequate to completely dismiss this river
as a demonstration site, do need further discussion as to the relevance of this site.
60
QMDC Macintyre River – Fish fauna characterisation
6.1 Recommendations
1. The Macintyre River be supported as a demonstration reach action site in the
Border Rivers catchment of the Murray-Darling Basin.
2. The Macintyre Brook be supported as a reference site, pending further
investigation of the fish assemblage and structure.
3. The Dumaresq River be considered as a demonstration reach action site in the
Border Rivers catchment of the Murray-Darling Basin.
4. Key stakeholders be made aware of, and support the temporal timeframe
necessary to achieve this demonstration reach program.
5. Key stakeholders be fully informed of the key threats to each species of native
fish in the Border Rivers catchment (see table 4, page 20).
6. Key stakeholders be made aware of the full suite of intervention programs (see
section 5.6) and be informed on the cost-benefit of undertaking any or a range
of these as management actions.
7. Further research is needed to establish the larval/juvenile habitat of several
native fish in the Border Rivers catchment, including the olive perchlet
(Ambassis agassizii), flyspecked hardyhead (Craterochephalus
stercusmuscarum fulvus), purple-spotted gudgeon (Morgunda adspersa), and
Australian smelt (Retropinna semoni).
8. Further research/survey work is needed to establish the need and extent of
lateral and longitudinal migration by several of the smaller native fish,
including flyspecked hardyheads (Craterochephalus stercusmuscarum fulvus),
carp gudgeons (Hypseleotris spp.), rainbow fish (Melanotania fluviatilus),
purple-spotted gudgeons (Morgunda adspersa) and flathead gudgeons
(Phylipnodon grandiceps).
9. Further research is needed to establish the impacts of non-seasonal irrigation
flows on native fish populations, with respect to cold water and non-seasonal
changes in river height effects on access to critical instream and offstream
habitat.
Acknowledgements
Thanks go to Natalie Baker and Gavin Prentice for valuable input during the
conceptual process of this report and their keen observations and commentary during
the road trip. The reviews by Peter and Mark are greatly appreciated, as is the diligent
editorial review by Amy Radford.
QMDC Macintyre River – Fish fauna characterisation
61
7.
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