Searching for threatened upland
galaxiids in the Thomson and La Trobe
river catchments, West Gippsland
Arthur Rylah Institute for Environmental Research
Technical report series No: 248
Published by the Victorian Government Department of Environment and Primary Industries
Melbourne, July 2013
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Citation: Raadik, Tarmo A. and Nicol, Michael D. (2013) Searching for threatened upland galaxiids (Teleostei,
Galaxiidae) in the Thomson and La Trobe river catchments, West Gippsland, Victoria. Arthur Rylah Institute for
Environmental Research Technical Report Series No. 248. Department of Environment and Primary Industries,
Heidelberg, Victoria.
Front cover photos: Main – Hope Creek, South Face Road, La Trobe River catchment; Upper – Tapered Galaxias
(Galaxias sp. 8); Lower – West Gippsland Galaxias (Galaxias sp. 9) (Tarmo A. Raadik).
Authorised by: Victorian Government, Melbourne
Printed by: NMIT Print Room
Searching for threatened upland galaxiids (Teleostei,
Galaxiidae) in the Thomson and La Trobe river
catchments, West Gippsland, Victoria
Arthur Rylah Institute for Environmental Research
Technical Report Series No. 248
Tarmo A. Raadik and Michael D. Nicol
Arthur Rylah Institute for Environmental Research 123 Brown Street, Heidelberg, Victoria 3084
July 2013
Contents
Acknowledgements
ii
Summary
iii
Introduction
1
Methods
3
Site selection
Aquatic fauna sampling
3
3
Results
6
Upland galaxiids
Other aquatic fauna
11
26
Discussion
35
Upland galaxiids
Other aquatic fauna
35
38
Conclusion
39
References
40
Appendix 1 Location of sampling sites
42
Appendix 2 Summary of survey results
46
Appendix 3 Summary of site characteristics
52
Arthur Rylah Institute for Environmental Research Technical Report Series No. 248
i
Acknowledgements
Funding for this project was provided by the (former) Department of Primary Industries, and facilitated by the Forests and
Parks Division of the (former) Department of Sustainability and Environment. We especially thank Dr Lindy Lumsden
(DEPI-ARI) for her support for the importance of the ‘wet bits’ in forested landscapes. We thank Greg Hollis (Baw Baw
Shire Council), Mark Turra (Maintenance Supervisor, Mount Baw Baw Alpine Resort) and Stuart Galloway (Gippsland
Water, formerly Maintenance Supervisor, Mount Baw Baw Alpine Resort) for information on previous anecdotal sightings
of galaxiids on the Baw Baw Plateau. We thank Mark Turra for providing a Yamaha Rhino 4WD all-terrain vehicle to
transport sampling equipment along the hiking trails on the Baw Baw Plateau, and sincere thanks is also extended to the
chefs at the Village Restaurant in the Mount Baw Baw Alpine Resort who prepared warm food for us at any time of day to
ward off hypothermia. We also thank Dale Archer (Melbourne Water, Thomson Reservoir Office), for arranging access to
the Thomson River catchment, and Dave Vaskess (DEPI, Noojee), Jessica Taylor (DEPI, Heyfield) and Cliff Ireland
(Parks Victoria, Dargo) for advice on track conditions and access issues. Silvana Acevedo (Arthur Rylah Institute)
produced the GIS maps, and valuable critical comment on an earlier draft of this report was provided by Paul Reich and
Jenny Nelson (Arthur Rylah Institute). This work was conducted under Fisheries Research Permit RP827 and FFG /
National Parks research permit 10005451.
Arthur Rylah Institute for Environmental Research Technical Report Series No. 248
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Summary
Whilst not a major landscape component based on area of occupancy, aquatic systems represent a different biome to
terrestrial environments. Running waters, in particular, are an important and ubiquitous component of forested
catchments, extending from lower elevations to ridgelines. They bisect the landscape into drainage or catchment units
and support important vegetation communities (e.g. riparian zones) and aquatic organisms. The aquatic ecosystem relies
on biological catchment processes, and in small upland streams in forested catchments, a major pathway of energy into
the aquatic environment is from the riparian zone.
As part of a project to develop an effective landscape approach to the management of threatened fauna that provides
opportunities for sustainable timber production, improved information was needed on selected threatened aquatic fauna
in the forest landscapes of the Central Highlands area in Victoria. Two species of native freshwater fish, considered
threatened and restricted to forested catchments, were selected as priority taxa for field assessment.
These species — Tapered Galaxias (Galaxias sp. 8) and West Gippsland Galaxias (Galaxias sp. 9), recently discovered
as new species, are in the process of being formally described. These species were previously considered to be a single,
morphologically variable species, the Mountain Galaxias (Galaxias olidus).
Galaxias sp. 8 and Galaxias sp. 9 are each known from a short headwater section of a single narrow stream in state
forest in the Thomson and La Trobe river catchments, respectively. They are considered to be critically endangered and
have been nominated for listing under the Victorian Flora and Fauna Guarantee Act 1988. Predation by trout, introduced
into Australia, is a key threatening process for upland galaxiids, typically eliminating them as they colonise new habitat,
particularly in small streams. The species are also sensitive to instream sedimentation caused by catchment disturbance.
The primary aim of this project was to confirm the presence and improve knowledge of Galaxias sp. 8 and Galaxias sp. 9
in the mid to upper portions (> 300 m elevation) of the Thomson and La Trobe catchments, including:

confirm previous distribution;

locate additional populations;

collect demographic and general habitat information; and,

assess potential threats, including wildfire and timber harvesting history.
To value-add to this project and to improve broader aquatic biodiversity knowledge for the smaller streams in each
catchment, data was also collected on additional aquatic fauna (other fish, crayfish and shrimp) encountered at each
sampling site.
Primary sampling sites were the locations at which these species had previously been recorded, including the Baw Baw
Plateau where anecdotal information suggested the presence of an unidentified upland galaxiid. Additional survey sites,
considered highly likely to harbour upland galaxiids, were selected across the upper Thomson and La Trobe catchments
(e.g. sites not known to contain Brown Trout or Rainbow Trout, particularly those upstream of instream barriers such as
waterfalls or steep instream gradients which would prevent trout access).
One hundred and twenty sites were visited during February–May 2012, with 110 sites sampled, primarily by single-pass
backpack electrofishing. This represents approximately 80% of the sites selected as likely to harbour upland galaxiids,
which were recorded from only 4% of all sites visited. More than two-thirds of the sites sampled (n = 73) lacked fish, all
mainly located in headwaters reaches of the La Trobe catchment, and 16 of these also lacked crayfish and shrimps.
Galaxias sp. 8 and Galaxias sp. 9 were confirmed as present but restricted to the original single stream that they were
each previously known from, and new data on their restricted distribution, threats, biology and habitat was collected. No
additional populations of upland galaxiids were located, and their presence (or absence) on the Baw Baw Plateau could
not be confirmed. This provides a high level of confidence that upland galaxiids are rare in terms of distribution in the
forested catchments of the Thomson and La Trobe river systems. It also highlights how rare, and therefore significant,
the few known populations of these galaxiids are, and how significant any additional populations would be if discovered.
Within their restricted ranges, Galaxias sp. 8 was reasonably abundant, although Galaxias sp. 9 was rare and the
species appears to have declined considerably in abundance since 2002. Both species are presumed to have been
historically more widely distributed. Both are considered at high risk of extinction because of their very small range, each
in a single stream, and the risk of impacts from stochastic events such as drought (loss of water) and post-fire impacts
(ash and bulk sediment input into waterways), and anthropogenic catchment disturbance leading to instream
sedimentation. Trout are present downstream of the distribution of each species, and instream sedimentation is an
ongoing issue, particularly for Galaxias sp. 9. Increased protection of the small, global distribution of each of these
species is required, as is careful conservation management to reduce the extinction risk.
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Additional aquatic fauna was collected during this survey, consisting of five native and two alien fish species, one species
of freshwater shrimp, three species of native freshwater crayfish and at least one species of native burrowing crayfish.
This fauna was composed of native species usually found at lower elevations in the catchment and extending a short
distance into the study area (Short-finned Eel, Broad-finned Galaxias, Common Galaxias, Australian Smelt, Yabby and
Freshwater Shrimp), and species found in mid to upper elevations (River Blackfish, a burrowing crayfish, Central
Highlands Spiny Crayfish and Gippsland Spiny Crayfish, and the alien species Brown Trout and Rainbow Trout). In
general, upland species were more widespread than lowland taxa.
Significantly, the Baw Baw National Park appears to be unique amongst sub-alpine to alpine areas on mainland southeastern Australia because our survey results indicate that the waterways lack fish, and notably alien trout are absent. If
true, these aquatic systems would provide a scarce, natural, predator-free refuge, particularly for upland galaxiids.
Instream sedimentation (silt and fine and coarse sand smothering the substrate), including smothering of riparian zones,
was evident at many locations in both catchments, although more common in the La Trobe system. The sediment
appeared to be derived from poorly maintained and drained roads and tracks, and from disturbed sites such as timber
harvesting coupes and areas burnt by wildfire. Structural aquatic habitat (rock, timber debris, interstitial spaces) were
reduced or absent at these sites, and infilling of pools was evident. Instream sedimentation impacts might have affected
the distribution and abundance of some aquatic species, particularly River Blackfish. This benthic species prefers
streams containing timber debris, and its eggs are laid on the substrate and can be smothered and killed by sediment.
Our recommendations for the conservation management of Galaxias sp. 8 and Galaxias sp. 9 include:
To stabilise known populations

Re-define the upstream and downstream extent of each species at the annual period of lowest stream flow to
accurately delimit the area of each population.

Monitor population abundance and recruitment annually to determine population health and trends, and to
detect and remove predators (trout) before they become established. This needs to be done annually to detect
any rapid population decline or predator presence before they breed and become established and major loss in
galaxiid abundance occurs.

Assess the location and type of instream barriers (if present) downstream of each population, including their
effectiveness at preventing the movement of trout upstream in higher flows.
o If a barrier is not present, translocate a subset of individuals immediately to a suitable captive or wild
destination
o
If a barrier is only partially effective, modify it to improve its effectiveness in preventing trout movement
upstream, or install a new vertical concrete barrier, as has occurred for other threatened galaxiid
populations.

Mitigate sediment input point sources from existing forestry tracks.

Close and rehabilitate redundant forestry tracks near the streams, removing stream crossings.

Provide more effective vegetative buffer zones along waterways, drainage lines and filter strips, in timber
harvesting coupes to prevent sediment transport into waterways during intense rainfall events.
To reduce the overall extinction threat

Carry out additional surveys in Rintoul Creek and unsampled western tributaries for the presence of Galaxias
sp. 9.

Assess nearby catchments to confirm potential translocations sites for establishment of additional populations of
each species.

Undertake translocations to establish new populations in the wild.

Avoid new roading crossing streams or drainage lines in key areas for these species.

Establish a protocol to monitor populations regularly during drought and immediately post-fire, and for ex situ
temporary captive maintenance if required.
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Introduction
Conservation management of threatened fauna in timber harvesting areas of state forest is currently through the
exclusion of harvesting from designated zones, based on species records (Lumsden et al. 2012). However, to be fully
effective the conservation management for a threatened taxon should consider its overall distribution at the landscape
scale, independent of land tenure. This then removes any bias in the perceived importance of an area, which can
eventuate from a focus on a given land tenure type or specific areas within a landscape.
In response to the Victorian Government’s Timber Industry Action Plan, released in 2011, a project was initiated to
develop an effective landscape approach to the management of threatened fauna species that provides opportunities for
sustainable timber production while managing biodiversity conservation (Lumsden et al. 2012). A key objective of the
project is to improve information about threatened fauna in the forest landscapes of eastern Victoria to inform the
management of threatened species across the public land estate. The research component of the project aims to
address this objective by undertaking surveys in the Central Highlands Regional Forest Agreement (CHRFA) area
(including all public land in state forests, parks and reserves) to provide new data on the distribution and habitat use of
priority threatened fauna (Lumsden et al. 2012).
While they do not constitute a major landscape component based on their area of occupancy, aquatic systems represent
a different biome to terrestrial environments. Running waters, in particular, are an important and ubiquitous component of
forested catchments. Rivers, smaller streams and drainage lines extend from lower elevations to ridgelines, bisecting the
landscape into drainage or catchment units and support important vegetation communities (e.g. riparian zones) and
aquatic organisms (Boulton and Brock 1999). The aquatic ecosystem relies on biological catchment processes, and in
small upland streams in forested catchments, a major pathway of energy into the aquatic environment is via allocthonous
organic matter (mainly leaves) (Wallace et al. 1997, Reid et al. 2008). Inputs of terrestrial insects from riparian vegetation
are also important for some species of fish (e.g. some galaxiids) (Cadwallader 1980).
A number of native fish and freshwater crayfish that occur in the Central Highlands RFA area are threatened at a state
and national level, e.g. Barred Galaxias (Galaxias fuscus), Macquarie Perch (Macquarie australasica), Australian
Grayling (Prototroctes maraena), Curve-tail Burrowing Cray (Engaeus curvisuturus) and Dandenong Burrowing Cray
(Engaeus urostrictus). Following a prioritisation process using six criteria to identify high-priority species (see Lumsden et
al. 2012), the majority of these were not selected for assessment in the research component of the project, except two
species of newly discovered upland galaxiids.
Upland galaxiids are small (< 130 mm in length) native freshwater fish that inhabit streams in south-eastern Australia,
from about 50 m to over 2000 m in elevation. Previously, this group was believed to be a single species, Mountain
Galaxias (Galaxias olidus), until it was recently identified as a cryptic species complex composed of 15 species, 12 of
which are new (Raadik 2011). Upland galaxiids are a common inhabitant of freshwater rivers and streams in forested
catchments of lowland, foothill and mountainous landscapes, often being the only native freshwater fish in areas above
700 m elevation (Raadik 2011). They do not migrate and therefore spend their entire life in freshwater, and their
distribution and abundance has been severely impacted by the introduction and establishment of alien Brown Trout
Salmo trutta and Rainbow Trout (Oncorhynchus mykiss) (Raadik 2011, Ayres et al. 2012), both of which are known to
severely impact on a number of species of galaxiids worldwide (McDowall 2006).
Seven of the 12 species of upland galaxiids known from Victoria are found in the coastal Gippsland region. Of these, six
are considered threatened (e.g. Dargo Galaxias, Galaxias sp. 6: Raadik and Nicol 2012), each being known mostly from
a single, short section of narrow headwater stream (Raadik 2011). These new species, in the process of being formally
described, have been nominated for listing under the Victorian Flora and Fauna Guarantee Act 1988 and are currently
being considered for listing by the Scientific Advisory Committee.
Two of the threatened upland galaxiids, Tapered Galaxias (Galaxias sp. 8) and West Gippsland Galaxias (Galaxias sp.
9), which are considered to be critically endangered (DSE 2013), were selected as priority species for assessment as
they are known from the headwaters of Stoney Creek (Thomson catchment) and Rintoul Creek (La Trobe catchment)
respectively. Although these locations are just outside of the Central Highlands RFA area, they are close to waterways
inside the area, and in the same river catchments. As these waterways are nearby and connected to each other, it was
considered highly likely that the two taxa may be more widespread in the portions of the Thomson and La Trobe river
catchments which form part of the Central Highlands RFA area. This assumption was supported by museum specimens,
indicating that Galaxias sp. 9 was historically more widespread in the La Trobe River catchment (Raadik 2011), a record
of an unidentified upland galaxiid (Galaxias sp.) observed on the Baw Baw Plateau in 1974 (Raadik 2001), and recent
anecdotal reports of galaxiids on the plateau (Greg Hollis, pers. comm. 2002, 2012; Stuart Galloway pers. comm. 2012).
The overall objective of this project was to significantly improve knowledge of the current distribution and associated
habitat of Galaxias sp. 8 and Galaxias sp. 9 in the Central Highlands RFA area.
Arthur Rylah Institute for Environmental Research Technical Report Series No. 248
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Specific aims were to:
 confirm their presence in the Thomson and La Trobe river catchments
 search for new locations
 collect demographic and general habitat information
 identify threats at each location, including wildfire and timber harvesting history.
To increase the value of this project and improve the broader aquatic biodiversity knowledge, data was also collected on
other fish and selected decapod crustacean (freshwater and burrowing crayfish, and freshwater shrimps) encountered at
the sampling sites for primary target taxa.
In this report we present the results of the field surveys for Galaxias sp. 8 and Galaxias sp. 9 that targeted the above
aims, including data on other fish and decapod crustacean encountered, in the Thomson River and La Trobe River
catchments.
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Methods
Site selection
Primary sampling sites were the locations at which upland galaxiids had previously been recorded — Stoney Creek,
Rintoul Creek, and the east branch of Tanjil River (Raadik 2011). An additional 250 potential sampling sites were initially
selected at higher elevations in the upper Thomson and La Trobe river catchments, spread throughout Baw Baw
National Park and adjoining state forests. These were selected from topographic survey maps and the digital map
coverage (including stream layer) in the Magellan program Vantage Point®. The initial selection was based on areas
considered highly likely to harbour upland galaxiids (e.g. areas upstream of instream barriers such as waterfalls or steep
instream gradients), in both catchment areas. Another consideration for site selection was distance from vehicle access,
as remote sites take more time to reach, reducing the overall number of sites which can be sampled. This therefore
reduced sites to those accessible by vehicle or those which could be reached within approximately one hour by foot from
a nearby track.
The list of potential sites was then refined by eliminating those where existing species records (Raadik et al. 2001,
Lieschke et al. 2013a,b; additional data sourced from the Victorian Biodiversity Atlas) did not include galaxiids, or
included trout (Figure 1). It was assumed that these sites had been sampled in a manner that would have detected
galaxiids, that galaxiids would have been part of the target fauna, and that enough sampling effort had been expended
which would have recorded galaxiids had they been present. Furthermore, trout are highly predatory and a key
threatening process for upland, non-migratory galaxiids, galaxiids typically being eliminated from streams as trout invade
(McDowall 2006). Potential sites were therefore also eliminated if they were found to be downstream of sites previously
found to contain trout, on the assumption that trout were still present at those sites, were highly likely to be present
farther downstream, and would have eliminated any galaxiids from those stream reaches. Overall, approximately 140
potential sampling sites remained after these eliminations.
The list of potential sampling sites was further refined during field surveys, as some sites could not be reached because
of access difficulties. During these surveys we also found additional sites that met our selection criteria and were located
on access tracks not recorded on topographic maps.
Aquatic fauna sampling
Although upland galaxiids were the primary fauna targeted during sampling, data was also collected on other fish and
decapod crustacean (freshwater and burrowing crayfish, freshwater shrimps) encountered during sampling at each
location.
At each survey site the aquatic fauna was sampled by single-pass electrofishing using a portable 24-volt Smith-Root®
LR20B backpack electrofishing unit. Electrofisher output ranged from 700–900 volts, at a frequency of 110 Hz and 25–
45% duty cycle, depending on water electrical conductivity levels and stream depth. Electrofishing was undertaken
during daylight hours, with the operator, wearing polarised sunglasses, walking instream along the entire length of the
survey site, sampling all habitat types in an upstream direction, stunning and retrieving all fauna encountered, while an
assistant followed with a dip net and bucket to collect captured fauna and retrieve any missed by the operator.
The target survey distance in the small streams to be sampled was a minimum 50 m in length, although this varied at
some sites (range 5–265 m) depending on stream width and accessible habitat. Survey distance was measured by the
assistant with a stringline, while average stream width, and maximum and average water depth were estimated. All fauna
collected (i.e. fish and decapod crustacea) was identified, counted and measured for length and weight, or preserved for
later identification in a laboratory. Additional aquatic animals that were seen but not captured were counted and recorded
to the taxonomic rank to which they could be confidently assigned (e.g. family, genus or species).
A visual search was also made along the banks at each survey site for secondary evidence of the presence of native
burrowing crayfish (Engaeus spp.), as only a small number of species occur in the stream, with many species found in
burrows in the riparian zone (Horwitz 1990). The most noticeable sign of burrowing crayfish was the presence of obvious
and distinctive soil-pellet ‘chimneys’ at burrow openings, although searches were also made for crayfish exoskeletons.
In addition to electrofishing, 1–3 unbaited, rectangular bait traps for fish were set in pools for a 14-hour period overnight.
Traps were set at dusk and retrieved the next morning. Unlike electrofishing, which is an active sampling technique, bait
traps relied on fauna moving into them, and have been used successfully as an adjunct to electrofishing to capture
smaller fish species (MDBC 2004). They were used as an additional, although passive, capture technique to target
upland galaxiids, and were only deployed for a single night at each of three locations in the east branch of Tanjil River,
within the Mount Baw Baw Alpine Resort.
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Figure 1. Pre-2012 fish sampling sites in the Thomson and La Trobe catchments (grey circles), including known upland galaxiid locations.
Fish were identified using the keys and species descriptions in McDowall (1996) and Raadik (2011), burrowing crayfish
(genus Engaeus), freshwater shrimps (genus Paratya) and yabbies (genus Cherax) using Horwitz (1990, 1995), and
spiny freshwater crayfish (genus Euastacus) using Morgan (1986).
In situ measurement of specific water quality parameters was made at the time of fauna sampling at each survey site.
Electrical conductivity (at 25°C), water temperature, turbidity and dissolved oxygen where recorded using a TPS 90-FLT
water quality meter. Water pH was recorded using a colorimetric test kit rather than the water quality meter, as this
provided a more accurate reading in water with low electrical conductivity (< 200 EC).
The reproductive condition of captured upland galaxiids was determined by inspecting the degree of gonad development
through the body wall and categorising the reproductive stage against descriptors previously developed for another
upland galaxiid species (Stoessel et al. 2012).
General observations were made at each site, where relevant, of general habitat association of upland galaxiids,
potential threats to the instream environment (e.g. sedimentation), and instream habitat characteristics such as substrate
type and composition. These also included a general visual inspection of active or potential sources of sedimentation into
the waterway.
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Results
Field surveys commenced in February 2012 and were completed by mid-May 2012, with 120 sites in the mid to upper
reaches of the Thomson (35 sites) and La Trobe (85 sites) catchments above 300 m in elevation (range 130–1520 m)
sampled for aquatic fauna (Figure 2, Appendix 1). These constitute approximately 80% of the potential sampling sites
selected as highly likely to harbour upland galaxiids.
Locations details are in Appendix 1, a summary of collection data is provided in Appendix 2, and water quality data and
other site characteristics are listed in Appendix 3. All data will be entered on the Victorian Biodiversity Atlas, managed by
the Department of Environment and Primary Industries.
Sites in the La Trobe catchment ranged in altitude from 250 m to 980 m, and those in the Thomson catchment from 840
m to 1185 m (Appendix 1). Ten sites — five in each river catchment — were found to be dry and therefore could not be
sampled for in-stream fauna (Figure 3). However the visual search for secondary evidence of native burrowing crayfish
(Engaeus spp.), was still carried out at these sites, with evidence of their presence found at one site (TR-12-035, a
tributary of the Latrobe River; Appendix 2).
An additional site, although not completely dry, was too shallow and overgrown with alpine heath vegetation and also
could not be sampled for in-stream fauna (site TR-12-009, a tributary of West Tanjil Creek, Baw Baw Plateau; Appendix
2). Of the 109 sites which were sampled by electrofishing, 16 lacked fish and decapod crustacea (10 sites in the
Thomson catchment and 6 sites in the La Trobe catchment) (Figure 4; Appendix 2). Most of these were in upper
headwater reaches.
More than two-thirds (n = 73) of sampled sites lacked fish (Figure 5; Appendix 2), and these were also mainly in
headwater reaches, with the majority located in the La Trobe catchment. Seven native species (including the two target
upland galaxias) and two alien fish species were collected, along with four species of native freshwater crayfish and one
species of freshwater shrimp (Table 1; see sections 4.1 to 4.3 for more detail). Streams at all sites ranged in width from
0.2 m to 15.0 m, although the majority were less than 2.0 m wide (median 1.1 m), and average depth varied from 5 cm to
70 cm. Survey reach length averaged approximately 55 m (Appendix 3).
Table 1. Common and scientific names of aquatic fauna collected in this study.
Scientific name
Scientific name
Common name
Family Anguillidae
Anguilla australis
Short-finned Eel
Family Percichthyidae
Gadopsis marmoratus
River Blackfish
Family Galaxiidae
Galaxias brevipinnis
Broad-finned Galaxias
Galaxias maculatus
Common Galaxias
Galaxias sp. 8A
Tapered Galaxias
Galaxias sp.
West Gippsland Galaxias
FISH
Native species
Family Retropinnidae
9A
Retropinna semoni
Australian smelt
Oncorhynchus mykiss
Rainbow Trout
Salmo trutta
Brown Trout
Cherax destructor
Common Yabby
Engaeus sp.
Burrowing Crayfish
Euastacus kershawi
Gippsland Spiny Crayfish
Euastacus woiwuru
Central Highland Spiny Crayfish
Paratya australiensis
Freshwater Shrimp
Alien species
Family Salmonidae
DECAPOD CRUSTACEA
Family Parastacidae
Family Atyidae
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Figure 2. Location of sites surveyed for aquatic fauna in the Thomson and La Trobe River catchments (black circles), February–May
2012, including sites at which Galaxias sp. 8 and Galaxias sp. 9 were recorded.
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Figure 3. Location of sites surveyed in the Thomson and La Trobe catchments found to be dry (red dots), February–May 2012.
Note some dots represent more than one site.
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Figure 4. Location of sites surveyed in the Thomson and La Trobe catchments at which aquatic fauna were not found,
February–May 2012 (includes dry sites from Figure 3). Note: some dots represent more than one site.
Arthur Rylah Institute for Environmental Research Technical Report Series No. 248
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Figure 5. Survey sites in the Thomson and La Trobe catchments at which fish were not found, February–May 2012.
Note: some dots represent more than one site
Upland galaxiids
Galaxias sp. 8 and Galaxias sp. 9 were confirmed as still extant, being collected from their previously known locations
(compare Figure 1 and Figure 2), and from other nearby sites in the same streams (Table 2). Together, both species
were recorded from 4% of sites visited.
No galaxiids were found on the Baw Baw Plateau (compare Figure 1 with Figure 2), despite recent anecdotal evidence
suggesting their presence in streams in that area (Greg Hollis, pers. comm. 2012; Mark Turra pers. comm. 2012).
Table 2. Survey sites at which upland galaxiids were recorded, including date of capture and numbers
recorded (= caught + seen). See Appendices 1–3 for more details.
Site
Stream
Location
Date
Species
Number
TR-12-117
Stoney Ck
Stoney No. 5 Track
1/05/2012
Galaxias sp. 8
42
TR-12-140
Stoney Ck
Stoney No. 4 Track
4/05/2012
Galaxias sp. 8
9
TR-12-112
Rintoul Ck
C12 Track
30/04/2012
Galaxias sp. 9
2
TR-12-116
Rintoul Ck
R10 Track
1/05/2012
Galaxias sp. 9
2
TR-12-118
Rintoul Ck
R7 Track
1/05/2012
Galaxias sp. 9
6
Galaxias sp. 8 (Tapered Galaxias)
Survey results
Galaxias sp. 8 (Figure 6) was recorded from its previously only known location in Stoney Creek (Stoney No. 5 Track, site
TR-12-117) and was also recorded for the first time at the ford on Stoney No. 4 Track (site TR-12-140), approximately
6.7 km downstream (Table 2; Figures 2, 7 and 8, Appendix 2).
Figure 6. Galaxias sp. 8, Stoney Creek at Stoney No. 5 Track (1 May 2012). Left: 75 mm long
gravid female. Right: Dorsal view of individuals from the same site. (Images: T.A. Raadik).
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Figure 7. Location of collection sites for Galaxias sp. 8 in the Stoney Creek system, Thomson River Catchment.
Previous sampling sites are shown in grey.
Galaxias sp. 8 was not recorded elsewhere in the Thomson and La Trobe river catchments, nor from farther
downstream in the Stoney Creek catchment. It was not collected at Stoney No. 3 Track (site TR-12-119),
approximately 7.8 km downstream from Stoney No. 4 Track, where Brown Trout were present, nor in a
tributary that joined downstream of Stoney No. 3 Track (site TR-12-161) (Appendix 2). It was also absent
from all sites sampled nearby in the Glenmaggie Creek catchment (TR-12-157, -158 and -159), and from
farther north in the headwaters of Mt Useful Creek (site TR-12-160) (Appendix 2).
Figure 8. Stoney Creek. Left: Upstream of the ford on Stoney No. 5 Track, 1 May 2012. Note
the gravel mound to the right and patches of in-stream gravel. Right: At the ford on Stoney
No. 4 Track, 4 May 2012. (Images: T.A. Raadik).
Population abundance (density of individuals) was highest at Stoney No. 5 Track (0.2 fish/m2) where 42 fish
were seen or captured in a 100 m reach of stream, and lowest at Stoney No. 4 Track where only nine
individuals were collected from a 165 m reach (0.01 fish/m2) (Tables 2 and 3). The biomass of Galaxias sp.
8 differed similarly between these sites (Table 3).
The smallest individual collected was 49 mm in length, which was most likely a juvenile from a spawning in
2011. The largest individuals were 84 mm long (Table 3, Figure 8). The average length of individuals at
Stoney No. 5 Track was approximately 66 mm, being on average shorter than those at Stoney No. 4 Track.
The relationship between individual length and weight, useful for future comparisons of fish condition, is
shown in Figure 9. Of the 40 fish collected (i.e. excluding those only seen), 31 could be sexed, with a male
(49 mm in length) the smallest mature fish. The gonads of the majority (71%) of these fish were in mature
stage of development, although five males were more advanced, with ripe gonads (milt extruded by gentle
pressure on the body wall). Three females were less well developed, with gonads in a maturing stage of
development.
Table 3. Length and weight data (mean; median; range) for Galaxias sp. 8 collected from
Stoney Creek in 2012, including density and biomass estimates (LCF – length to caudal
fork).
Site Code
Location
Length
(mm LCF)
Weight (g)
Density
(fish.m-2)
Biomass
(g. m-2)
TR-12-117
Stoney No. 5
Track
66.1; 68.5; 49–84
2.6; 2.4; 0.8–5.4
0.20
0.50
TR-12-140
Stoney No. 4
Track
71.3; 70.0; 60–84
3.3; 3.1; 1.9–5.4
0.01
0.04
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Based on a visual assessment of instream habitat and fish capture location at each site at the time of
sampling, individuals of Galaxias sp. 8 were located mainly around or among cobbles on the stream bed in
shallow (0.15–0.2 m), gently flowing riffle or glide areas. They were almost absent from still water areas
adjacent to banks or deep pools, and were not observed swimming before or during sampling. The water at
both sites was clear, and instream habitat was primarily rock (boulders and cobbles), with smaller amounts
of timber debris (logs and branches), and a very small amount of overhanging vegetation or undercut banks.
At both sites, although much more prominent at Stoney No. 5 Track, there were large amounts of finer
substrate particles (pebble, gravel and coarse sand), blanketing extensive areas of the substrate (e.g.
between cobbles), or mounded on the stream bank, indicating relatively recent sediment input into the
stream.
6
5.5
5
4.5
Weight (g)
4
3.5
3
2.5
2
1.5
1
0.5
0
45
50
55
60
65
70
75
80
85
90
Length (mm LCF)
Figure 9. Plot of length and weight for 40 individuals of Galaxias sp. 9 collected from
Stoney Creek in May 2012.
Wildfire and timber harvesting history
The Stoney Creek catchment experienced one moderately widespread and one widespread (in terms of
catchment area covered) wildfire events in the period 1990–2011 (Figure 10). The upper portion of the
catchment, upstream from (and including) Stoney No. 4 Track was burnt in 1991, and the most severe fire
occurred relatively recently, burning across the entire catchment in 2007.
Overall, timber harvesting activity over the past 50 years has occurred over an extensive area of the Stoney
Creek catchment, extending from the ridges on the edge of the catchment downhill to, and along, the main
channel in many areas (Figure 11). In particular, forest adjacent to Stoney No. 4 and No. 5 tracks has been
harvested.
More recently (1990–2011), timber harvesting has been restricted to the upper portion of the catchment
(Figure 12), mainly to the western ridgeline (compare Figure 11 and 12), and in many areas harvesting
coupes have been located adjacent to tributary streams. During this period, the amount of forest harvested
during a given season has been very small compared to the total area of the Stoney Creek catchment.
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Figure 10. Wildfire history in the Stoney Creek catchment, 1990–2011. (Data sourced from DSE Spatial Datamart).
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Figure 11. Timber harvesting history in the Stoney Creek catchment, 1990–2011. (Data sourced from DSE Spatial Datamart).
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Figure 12. Timber harvesting history in the Stoney Creek catchment, 1960–2011. (Data sourced from DSE Spatial Datamart).
Galaxias sp. 9 (West Gippsland Galaxias)
Survey results
Galaxias sp. 9 (Figure 13) was re-collected from its previously known location on Rintoul Creek, east branch, (C12 Track,
site TR-12-112) (Table 2, Figures 2, 14, 15) and was recorded for the first time at the fords on R10 and R7 tracks (sites
TR-12-116 and 118 respectively) (Table 2, Figures 2, 14–16), approximately 1.9 km (stream distance) farther
downstream and 2.0 km upstream respectively (Appendix 2).
The species was not recorded from elsewhere in the Thomson and La Trobe river catchments, and in particular was
absent from two additional sites farther downstream in the Rintoul Creek catchment (Figure 2): R15 (Scorese Bridge)
Track on Rintoul Creek east branch (site TR-12-115) (Figures 2, 16; Appendix 2), approximately 4 km (stream distance)
farther downstream; and, in a side tributary of Rintoul Creek (site TR-12-142) (Appendix 2). They were also absent from
all sites sampled relatively nearby in the Eaglehawk and Jacobs/Neander creek catchments (sites TR-12-116, 141 and
143) (Figure 2, Appendix 2).
Figure 13. Galaxias sp. 9 from Rintoul Creek, R10 Track (1 May 2012). Left: 65 mm long gravid female. Right:
Dorsal view of individuals. (Images: T.A. Raadik).
Figure 14. Rintoul Creek, east branch: Left: Downstream of C12 Track, 30 April 2012. Right:
Just downstream of R10 Track, 1 May 2012. (Images: T.A. Raadik).
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Figure 15. Location of collection sites for Galaxias sp. 9 in the Rintoul Creek system, La Trobe River Catchment.
Population abundance (density of individuals) was very low at all sites (Table 4), with very few fish recorded (Table 2).
The highest abundance was recorded at R7 Track (0.05 fish/m2) where 6 fish were seen or captured in a 100 m reach of
stream; only two fish were captured at each of the other two sites (Tables 2 and 4). The biomass of Galaxias sp. 9
similarly differed between these sites, with the lowest biomass at C12 Track (Table 4).
Table 4. Length and weight data (mean; median; range) for Galaxias sp. 9 collected from Rintoul
Creek, east branch, in 2012, including density and biomass estimates.
Density (fish/m2)
Biomass (g/m2)
2.6; 2.6; 2.3–3.0
0.004
0.01
64.0; 64.0; 63–65
2.25; 2.25; 2.2–2.3
0.01
0.03
74.7; 69.5; 62–97
5.0; 3.3; 2.4–11.5
0.05
0.23
Site Code
Location
Length (mm LCF)*
TR-12-112
C12 Track
66.5; 66.5; 66–67
TR-12-116
R10 Track
TR-12-118
R7 Track
Weight (g)
* length to caudal fork
No recruitment of fish from the last spawning season (2011) was detected; a fish 62 mm in length was the smallest
individual collected, representing an older, sexually mature adult. The largest individual collected was 97 mm long (Table
4), and the average length of individuals ranged from 64.0 mm to 74.7 mm (Table 4). All eight fish collected were sexed,
and comprised 7 males and one female. The gonads of six of the seven males were in a mature stage of development,
and one male and the single female were in a ‘maturing’ stage of development (data not shown).
Figure 16. Rintoul Creek, east branch: Left: Upstream of R7 Track, 1 May 2012. A silt load is
evident in the channel, infilling a pool (arrow). Right: Upstream of R15 Track, 1 May 2012.
(Images: T.A. Raadik).
Based on a visual assessment of instream habitat and fish capture location at each site at the time of sampling,
individuals of Galaxias sp. 9 were mainly in very shallow (< 0.2 m in depth), gently flowing riffle areas, among
cobbles/pebbles, or in small to medium-sized timber debris on the stream bed. An exception to this was the largest adult,
collected from under a log in a deep (c. 0.6 m), and heavily shaded pool upstream of R7 Track. No fish were observed
swimming before or during sampling, and all were collected from areas of cover; many fish at R7 Track came from under
timber on the ford (Figure 17, left image). The water at all sites was clear, and instream habitat was primarily rock (mainly
gravel and a few cobbles), with moderate amounts of timber debris (smaller branches and small to medium sized logs),
and overhanging vegetation or undercut banks.
All sites had extensive silt and fine sand deposits blanketing the stream bed, and deposits of sand/pebble and silt on the
stream banks. This indicates relatively recent, extensive, sediment input into the stream, with some point sources from
poorly maintained track crossings and roads (Figures 17–19). A large amount of silt was present around the ford on R7
Track (Figure 17), artificially building up the level of the ford and extensively blanketing the substrate in the pools farther
upstream. The only exposed rock substrate was small cobbles, present only on the ford in the flow channel where the
flow had scoured the silt downstream.
Following overnight rain, a tributary of Rintoul Creek (TR-12-142; Appendices 1 and 2) became turbid due to sediment
input from the adjacent Rintoul Creek Road and upstream pine plantation (Figure 18, right image). This indicates
waterborne sediment infiltration through the vegetated buffer zone around the stream.
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Figure 17. Rintoul Creek, east branch. Left: Sediment and erosion at ford on R7 Track
(1 May 2012). The ford has become artificially elevated by sediment build-up in the stream.
Right: Poorly maintained and eroding log causeway at C12 Track, 30 April 2012. (Images:
T.A. Raadik).
Figure 18. Rintoul Creek. Left: East branch, landslip and erosion area off C12 Track into
Rintoul Creek, upstream of C12 Track causeway. Right: Turbid water in a tributary off
Rintouls Creek Road (14 May 2012). (Images: T.A. Raadik).
Figure 19. Rintoul Creek, east branch, at C12 Track, 30 April 2012. Left: Stream channel
filled in by sediment downstream of ford. Note the sediment accumulations within the
channel which have become vegetated (arrows). Right: Pool filled in by sediment
immediately downstream of an eroding log causeway on C12 Track. No fish or crayfish
were present in the pool. (Images: T.A. Raadik).
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Wildfire and timber harvesting history
The upper portion of the Rintoul Creek catchment has experienced two small and one moderately widespread (in terms
of catchment area covered) wildfires in the period 1992–2011 (Figure 20). Of these, the most severe fire occurred
relatively recently, burning across the very upper portion of the catchment in 2007. Smaller areas in this section of the
catchment had been burnt in 1996, and a small area of the catchment of Rintoul Creek west branch was burnt in 2006.
The present distribution of Galaxias sp. 9 is within the area burnt in 2007.
Timber harvesting has been conducted in the Rintoul Creek catchment since the mid 1940s, and a large portion of the
forested catchment in the west and east branches of the system has been harvested since that time (Figure 21).
Extensive areas have been harvested from ridgelines downhill to, and along, the main channel. Although the logging
history, indicated in Figure 21, shows unlogged buffer strips along watercourses, these may not have been present
everywhere, as streamside buffer zones only came into use well after the 1950s.
More recently (1990–2011), timber harvesting has been restricted to the headwaters of the catchment (Figure 22), mainly
to the north-western and western ridgeline (compare Figure 21 and 22). During this period the amount of forest
harvested during a given season has been very small compared to the total area of the Rintoul Creek catchment.
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Figure 20. Wildfire history in the Rintoul Creek catchment, 1992–2011. (Data sourced from DSE Spatial Datamart).
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Figure 21. Timber harvesting history in the Rintoul Creek catchment, 1944–2011. (Data sourced from DSE Spatial Datamart).
1944-2011
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Figure 22. Timber harvesting history in the Rintoul Creek catchment, 1990–2011. (Data sourced from DSE Spatial
Datamart).
Other aquatic fauna
A range of other aquatic fauna were also collected at sampling sites (see Table 1; Appendix 2). This consisted of species
usually found at lower elevations in the catchment and extending a short distance into the study area, and species
commonly found at mid to upper elevations in forested catchments.
Lowland native species
Short-finned Eel (Anguilla australis), a migratory species, was recorded from two sites in Stoney Creek in the Thomson
catchment and from eight sites in the La Trobe catchment, at elevations between 340–445 m and 150–320 m
respectively. All sites were downstream of major instream barriers, except for two sites in the La Trobe catchment, one
near Neerim East (Stanley Vale Ck; TR-12-069) and one on a tributary of Tanjil River (east branch), upstream of Blue
Rock Lake (Lady Manner Sutton Ck; TR-12-025) (Appendix 2).
Broadfinned Galaxias (Galaxias brevipinnis), a migratory species, was collected at three sites on Rintoul Creek in the La
Trobe River catchment, at elevations between 150–230 m (sites TR-12-11, 115 and 116) (Appendix 2).
Common Galaxias (Galaxias maculatus), a migratory species, was recorded from one site on Rintoul Creek (La Trobe
catchment), with three individuals captured at R15 Track (site TR-12-115) at an elevation of 150 m (Appendix 2).
Australian Smelt (Retropinna semoni), a species which is now considered an un-resolved cryptic species complex
(Hammer et al. 2007), and which is partially known to migrate (Crook et al. 2008), was also only recorded from this site.
One Yabby (Cherax destructor) was recorded from a site on Starvation Creek (TR-12-068) at an elevation of 170 m (La
Trobe catchment) (Appendix 1). Freshwater shrimp (Paratya australiensis) were recorded from nine sites in the La Trobe
catchment and six sites in the Thomson catchment, at elevations between 150–315 m and 230–445 m respectively
(Appendix 2).
Mid to upland species
River Blackfish (Gadopsis marmoratus), a native, non-migratory species, was only recorded in the La Trobe catchment,
from nine sites spread across the catchment at elevations between 200–520 m (Figures 23 (left) and 24; Appendix 2).
Usually six or less individuals were found at a site, except at Jacobs Creek (TR-12-113) where 19 fish were collected,
and at Good Hope Creek (TR-12-024) where 24 fish were found.
Figure 23. Common native aquatic fauna in the upper Thomson and La Trobe catchments. Left: River
Blackfish Gadopsis marmoratus, Icy Creek, 10 February 2012. Right: Central Highlands Spiny
Crayfish Euastacus woiwuru, Tanjil River (east branch), The Morass, Baw Baw Plateau, 16 February
2012. (Images: T.A. Raadik).
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Figure 24. Distribution of River Blackfish recorded in the Thomson and La Trobe catchments, February–May 2012.
Native burrowing crayfish (Engaeus spp.) were collected by electrofishing at a small number of sites, but were also
identified as present on the basis of fresh soil-pellet ‘chimneys’ at the entrance to burrows (Figure 25, top row; Figure 26)
along stream banks or in marshy areas. Occasionally soil pellets were spread from the borrow entrance in a fan shape
(Figure 25, bottom row), or were absent. Fresh soil pellets indicate recent crayfish activity, although crayfish can be
dormant underground at some times of the year (M. Nichol, pers. comm.). In forested catchments, burrows were usually
located among leaf litter in moist areas on the bank, often next to logs or tree ferns, but were also found under shrubs or
in the open among grasses or moss in alpine areas.
Figure 25. Native burrowing crayfish (Engaeus spp.) burrow entrance. Top row, with soilpellet ‘chimney’ at opening: (left) Bell Clear Ck, 15 February 2012; (right) Tanjil River
(east branch), at The Morass, Baw Baw Plateau, 16 February, 2012. Bottom row, with soil
fan at burrow entrance: (left) Village Trail, Mt. Baw Baw Alpine Resort, 7 February 2012;
(right) Long Creek, Tanjil Bren Road, 8 February 2012. (Images: T.A. Raadik).
Burrowing crayfish were distributed widely across the La Trobe catchment (52 sites between elevations of 130–1220 m),
but were more prevalent in headwater reaches. They were more restricted in the Thomson catchment (5 sites, altitudinal
range of 710–1515 m) (Figure 26; Appendix 2), and to higher elevations.
The native Central Highlands Spiny Crayfish (Euastacus woiwuru) (Figure 23) and Gippsland Spiny Crayfish (Euastacus
kershawi) were relatively widespread and recorded from both catchments (Figure 27), although more common in the La
Trobe catchment. Of these, the Central Highlands Spiny Crayfish was more widespread, being found at 51 sites at
elevations between 275–1515 m and 445–1220 m in the La Trobe and Thomson catchments respectively (Appendix 2).
In contrast, the Gippsland Spiny Crayfish was less widespread (16 sites), particularly in the Thomson catchment (2
sites), and was found at lower elevations: 150–700 m in the La Trobe catchment and 340–350 m in the Thomson
catchment (Appendix 2).
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Figure 26. Distribution of burrowing crayfish (Engaeus spp.) recorded in the Thomson and La Trobe catchments, February–May 2012.
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Figure 27. Distribution of spiny crayfish (Euastacus spp.) recorded in the Thomson and La Trobe catchment,s February–May 2012.
Brown Trout (Salmo trutta) and Rainbow Trout (Oncorhynchus mykiss) (Figure 28), alien species which actively prey on
galaxiids (McDowall 2006), were relatively widespread in the mid to upper portion of the La Trobe catchment, although
restricted in the upper reaches of the Thomson catchment (Figure 29). Rainbow Trout were restricted in distribution
(three sites between 440 m and 520 m elevation), and only found at two sites in the La Trobe catchment and at a single
site in the Thomson catchment (Figure 29; Appendix 2). In contrast, Brown Trout were recorded at 25 sites, 18 of which
were in the La Trobe catchment (200–925 m) and at seven sites in the Thomson catchment (230–1085 m) (Figure 29,
Appendix 2). Trout were not recorded on the Baw Baw Plateau (Figure 29).
Figure 28. Alien salmonids in the upper Thomson and La Trobe catchments (Icy Creek,
10 February 2012). Left: Brown Trout (Salmo trutta). Right: Rainbow Trout
(Oncorhynchus mykiss). (Images: T.A. Raadik).
Instream and riparian sedimentation
Large amounts of organic silt and fine and coarse sand were prevalent at the majority of sites in state forest in the La
Trobe and Thomson catchments (i.e. outside Baw Baw National Park). Sediment often extensively blanketed the stream
bed, covering the substrate, and frequently formed large mounds along stream banks, extending laterally into the riparian
zone (Figure 30). In particular, sediment smothered rock and timber on the stream bed, effectively filling interstitial
spaces between rocks and infilling pools, leading to a uniform, compacted and homogenous stream bed lacking
structural habitat for aquatic fauna.
Active sources of this sediment into waterways, evident in both catchments, were vegetation disturbance and poorly
maintained or drained roads and tracks (Figure 31). Sediment can infiltrate waterways after rain, transported in run-off
through areas lacking filter vegetation or through insubstantial buffer zones that are unable to fully intercept the sediment
load. Both examples of such sediment (silt and sand) transport were witnessed during the field surveys after short,
intense rainfall.
Sediment entry into waterways via roads and tracks at some sites was observed usually via a point source (e.g. direct
draining from a stream crossing), but was usually more diffuse from timber harvesting coupes next to small streams. At
some sites sediment was observed penetrating the riparian zone and reaching the stream along coupe margins. The
persistence of instream sedimentation was also evident in areas in which timber harvesting had ceased a long time ago,
e.g. Ada River Sawmills Historical Area.
Signs of diffuse, bulk transport of sediment into waterways following wildfire were not evident from the general
observations made at sampling sites. This may be because vegetation quickly covered areas denuded by fire, and
because there had been an instream redistribution of sediment since the input.
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Figure 29. Distribution of Brown Trout (Salmo trutta) and Rainbow Trout (Oncorhynchus mykiss) recorded in the Thomson and
La Trobe catchments, February–May 2012.
Figure 30. Effect of sedimentation on the aquatic and riparian environment in the Thomson
and La Trobe catchments (clockwise from top left):
Build-up of fine sediment in Long Creek, Tanjil Bren Road (8 February 2012).
Smothering of bank and bed by coarse sand and silt, La Trobe River, upstream of Turner
Road (17 May 2012).
Streambed of Tanjil River, west branch (off Downey Road) smothered by coarse sand
(9 February 2012).
Silt and fine sand smothering bank and bed of a tributary of Whitelaw Creek, near Loop
Track (14 February 2012).
Streambed of Little Ada River filled in with sand, Ada River Mills Historic Area.
Kennedy Creek cutting through severe silt/sand deposition, Kennedy’s Creek Track (22
March 2012).
(Images: T.A. Raadik).
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Figure 31. Examples of sources of sediment to watercourse in the Thomson and La Trobe
catchments (clockwise from top left):
Eroding log bridge and dirt track on Good Hope Creek Track, Good Hope Creek (9 February
2012).
Eroding track (Federal Short Cut Road) draining into headwaters of Little Ada River
(17 May 2012).
Erosion point from bridge on Misery Creek Road directly into Starvation Creek (19 March 2012).
Extensive soil disturbance on steep slope, harvesting coupe, Tanjil River (east branch), north of
Tanjil Bren (9 February 2012).
Drainage line (indicated by arrow), lacking filter vegetation, draining from a timber harvesting
coupe, upper Thomson River catchment (14 February 2012).
Erosion point draining from Upper Thomson Road directly into a stream; (18 May 2012).
(Images: T.A. Raadik).
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Discussion
This project provides new data on Galaxias sp. 8 and Galaxias sp. 9, and aquatic biodiversity data from relatively poorly
known mid to upland forested areas in the Thomson and La Trobe catchments. This information will be broadly valuable,
particularly for biodiversity conservation and monitoring the impacts of climate change. These data complement existing
broader aquatic fauna data sets (e.g. Raadik 2001, Lieschke et al. 2013a,b) and, together with data from smaller projects
collated in the Victorian Biodiversity Atlas, contribute to benchmarking the status and condition of aquatic fauna in
Victoria.
The 120 survey sites were spread across each catchment, although concentrated more at higher elevations because of
the smaller amount of previous survey effort in this area compared to lower in the catchments, and a greater density of
stream network at these higher altitudes. A major area which was not thoroughly covered was the Baw Baw Plateau in
the Baw Baw National Park, where many remote streams drain the north and east sides (Thomson catchment), and a
portion of the south-east corner draining into the La Trobe catchment, not previously sampled. Additional survey effort in
the following areas would help to further define aquatic biodiversity values, particularly in relation to upland galaxiids:

La Trobe catchment — Rintoul Creek west branch, and headwater reaches of the Tyers River west branch

Thomson catchment — headwater reaches of the Aberfeldy River system, Deep and Lammers creek systems just
east of Walhalla, and headwaters of south-west tributaries of the Thomson River which drain Baw Baw Plateau.
Upland galaxiids
Galaxias sp. 8 and Galaxias sp. 9 were confirmed as present but restricted to the original single stream where they were
each previously found, within a forested catchment in state forest. Although they were each collected from additional
sites in their respective streams, this project has confirmed that the distribution of Galaxias sp. 8 is confined to a short
section of Stoney Creek, and Galaxias sp. 9 to a short section of the east branch of Rintoul Creek, both relatively narrow
(< 4.m wide), slowly flowing freshwater streams within state forest.
No additional populations of known or potentially new species of upland galaxiids were located elsewhere in the
sampling areas of the mid to upper Thomson and La Trobe catchments. In particular, the presence of an upland galaxiid
on the Baw Baw Plateau could not be confirmed. There are largely anecdotal records of galaxiids in Tanjil River (east
branch), West Tanjil Creek, a tributary of the Tyers River (west branch), and an unspecified upper tributary in the
Thomson catchment on the north-east slope of the plateau. The survey results, from approximately 80% of the sites
considered highly likely to harbour upland galaxiids, provide a high level of confidence that upland galaxiids are rare in
terms of distribution in the forested catchments of the Thomson and La Trobe river systems. They also highlight the
importance of the single known populations of Galaxias sp. 8 and Galaxias sp. 9 for the continued conservation of each
species, and how significant additional populations of each taxon in different streams, or of other upland galaxiid species,
would be if discovered.
Further assessment for upland galaxiids in the remaining remote and unsampled portions of the Thomson and La Trobe
catchments listed above, particularly the Baw Baw Plateau, may be helped by the use of environmental DNA (eDNA)
monitoring. This emerging technique aims to detect the presence of aquatic taxa by the presence of their DNA in water
(Darling and Blum 2007, Ficetola et al. 2008, Thomsen et al. 2012), and may be particularly useful for rare species. By
screening water samples taken from specific points in the catchment for the DNA of target taxa, sampling effort can then
be directed to portions of the catchment from which a positive DNA signature is detected, thereby increasing the chances
of locating small and isolated populations.
Locating additional individuals downstream from their original collection sites during this project increased the known
distribution of each taxon. However, this only approximately defined their downstream extent, at least to the particular
track crossing at which they were sampled; their distribution may extend farther downstream, probably to where they
meet the upstream distribution of predatory trout. The range extension for each species did not greatly increase the
overall geographical spread of each taxon: Galaxias sp. 8 is restricted to approximately the uppermost 11 km of Stoney
Creek, and Galaxias sp. 9 to the uppermost 6 km of Rintoul Creek. These estimates assume there is sufficient water,
habitable by fish, in the upper reaches of each catchment where the streams become third-order systems. The upstream
and downstream distribution of each species should be further defined, particularly during summer, in order to accurately
define the overall distribution of each species.
Historical distributional data is generally lacking, except for Galaxias sp. 9, which was previously also present (now
extinct) in Jeeralang Creek (Raadik 2011), almost directly south and across the La Trobe River from its confluence with
Rintoul Creek. This indicates that this taxon was historically more widespread in the lower La Trobe catchment, and
Arthur Rylah Institute for Environmental Research Technical Report Series No. 248
35
possibly occupied larger stream systems. A broader distribution can also be inferred for the biologically similar Galaxias
sp. 8.
Trout are present downstream of the distribution of Galaxias sp. 8 and Galaxias sp. 9 (Raadik et al. 2001, Lieschke et al.
2013a,b, and this survey), and it is likely that their presence has restricted the galaxiids to their current locations. Trout
can severely fragment non-migratory galaxiid populations (Tilzey 1976, Townsend and Crowl 1991, Crowl et al. 1992,
Closs and Lake 1996, McDowall 2006), which usually become confined to short headwater reaches of tributary streams,
often upstream of an instream barrier which prevents farther upstream colonisation by trout (Tilzey 1976, Raadik et al.
1996, Raadik 2011).
Within its restricted range Galaxias sp. 8 appeared to be reasonably abundant, although the density of individuals at
Stoney No. 5 Track (0.2 fish/m2), when compared to previous data, was half that for the same stream reach in November
1998, and only 22% of the density recorded in February 2002 (Raadik et al. 2001; Raadik 2011). Conversely, Galaxias
sp. 9 was rare; only two individuals were recorded from C12 Track, and the density of fish (> 0.01 fish/m2) was only 1.5–
1.7% of the densities found in December 1998 and February 2002 (Raadik et al. 2001; Raadik 2011). Density estimates
therefore demonstrate a large reduction in the number of fish at the sites sampled for both species. If these sites are
representative of conditions in the rest of each system, this suggests a considerable reduction in overall population
abundance has occurred for both species in the last 13 years.
The length range of Galaxias sp. 8 captured in Stoney Creek indicated the presence of fish presumed to have hatched in
the previous year. In contrast, no Galaxias sp. 9 from the previous (2011) spawning season were among the very few
fish collected in Rintoul Creek, suggesting recruitment failure for at least one season. Both sexes were present in both
systems, although only a single female was present among the eight fish collected from Rintoul Creek. Individuals of
both species were found to be reproductively developing, with the majority at a mature stage of gonad development,
suggesting a winter spawning period. Galaxias sp. 8 appeared to be slightly more advanced, with some males already in
a running ripe condition.
The aquatic and riparian environments in Stoney Creek and Rintoul Creek showed evidence of relatively recent and
extensive sediment input. The stream bed in each system was blanketed by smaller substrate components (e.g. pebble,
gravel, sand and silt) and deposits were also evident on the stream banks, extending into the riparian zone. This
sediment reduced the structural habitat on the stream bed preferred by > 1 year old galaxiids (cobbles and larger
boulders), and filled interstitial spaces in the stream bed, which are important for aquatic macroinvertebrates.
Sedimentation can degrade ecological condition in streams, and in particular reduce the diversity and abundance of
benthic macroinvertebrates (Doeg and Koehn 1994, Harrison et al. 2007), which are a food source for galaxiids. In
addition, a reduction of available rocks on the stream bed by sediment may reduce the spawning success of demersal
egg laying fish, ultimately affecting population size. Other species of upland galaxiids, Galaxias olidus and G. fuscus, are
known to prefer nest sites on cobbles and boulders (O’Connor and Koehn 1991, Stoessel et al. 2012) and Galaxias sp. 8
and Galaxias sp. 9 follow a similar strategy (Raadik unpublished data). Instream sedimentation may therefore play a
major role in the observed reductions in the galaxiid population in Stoney and Rintoul creeks.
Sediment input into the streams in both catchments appears to be via multiple sources. The bulk transport of large
amounts of sediment into streams can occur during intense rainfall events following wildfire which causes the temporary
reduction or loss of vegetative cover that stabilises soil, making soil easily eroded (Lyon and O’Connor 2008). Both
catchments have experienced fire: the upper portion of the Stoney Creek catchment was burnt in 1991, and the entire
catchment, including the upper portion of Rintoul Creek catchment, was burnt in 2007. It is strongly suspected that postfire erosion from these steep catchments is responsible for the bulk transport of sediment load into each stream, which is
slowly being flushed from the catchments.
In addition, active point sources of sediment input from roading are evident in both catchments. The majority of unsealed
forest tracks in both catchments had signs of recent erosion on slopes leading down to stream crossings, with many
lacking cross-drains so that run-off was directed into the watercourse. This was particularly prevalent in the Rintoul Creek
catchment, which has a more developed track network and consequently more stream crossings and therefore more
point sources of sediment input. Effective surface drainage from tracks to control run-off and to prevent it reaching
erosive speeds is therefore lacking in critical areas in both catchments. Track management requires improvement, with
installation of appropriately spaced (depending on grade and soil structure) cross drains to intercept run-off and to redirect it across the track surface into fringing vegetation. This is particularly important close to stream crossings, with the
drains carefully directed into vegetated buffer zones able to contain sediment flowing from the track. These should also
be able to operate effectively during intense rainfall events.
Furthermore, at least one recently constructed track crossing in the Rintoul Creek catchment (C12 Track) consisted of
compacted soil on top of logs placed directly into the stream bed. The soil was eroding directly into the stream and the
timber was blocking streamflow and catching debris. This structure, including the poorly maintained tracks leading to it,
was a major source of sediment input, and will erode further and cause bank erosion on the upstream side during higher
flow events.
Arthur Rylah Institute for Environmental Research Technical Report Series No. 248
36
Sediment transport into Stoney and Rintoul creeks through buffer zones around current or recent timber harvesting
coupes adjacent to water courses was not investigated. Given the degree to which fine sediment was found to be
transported through poorly functioning buffer zones around coupes elsewhere in the Thomson and La Trobe catchments
(see 3.3 above), these may be an additional source of sediment to each system.
Finally, the long-term impact of drought on the aquatic environments of both systems is unknown but is suspected to
have reduced population abundance, at least temporarily. This is likely to have occurred via a reduction in wetted habitat
that can support fish because of lowered water levels, poor water quality and, in some areas, the complete loss of water.
Observations on other upland galaxiids suggest they can be relatively persistent and resilient (Raadik, unpublished data).
Small, isolated populations can persist in refuge habitats and recover rapidly following the end of drought, driven by
strong recruitment from one or more spawning seasons (Raadik, unpublished data). Consequently, if recruitment is
restricted (e.g. lack of spawning substrate or poor larval survival), the rate of natural population recovery will be slower.
Based on the results of this project, Galaxias sp. 8 and Galaxias sp. 9 are at high risk of extinction because of the
substantial decline in historical distribution of both species and their current very small range, each in the headwaters of
a single stream that is prone to impacts from stochastic events such as drought, post-fire impacts (ash and bulk sediment
input), sediment input from anthropogenic catchment disturbance, and the ongoing threat of trout invasion. Populations
of both species have also declined considerably since 1998. Although this might have been a drought response within
natural bounds, but the resilience of the remaining population of either species could have been critically reduced,
particularly when coupled with existing potential threatening processes such as instream sedimentation.
Increased protection of the small, global distribution of each of these species is required, as is careful conservation
management to reduce the extinction risk. Based on this new information, the previous threatened status of Galaxias sp.
8 and Galaxias sp. 9 as Critically Endangered (DSE 2013) is upheld based on assessment against IUCN threatened
species criteria (IUCN 2012).
Of the two, Galaxias sp. 9 is currently considered under greater threat of extinction, as it has undergone a dramatic
population decline since 1998 and few individuals were located, the size of which indicate a lack of successful
recruitment for at least the previous season.
Conservation management recommendations
The future conservation management of Galaxias sp. 8 and Galaxias sp. 9 needs to include the following actions.
To stabilise known populations

Re-define the upstream and downstream extent of each species at the annual period of lowest stream flow
to accurately delimit the area of each population.

Monitor population abundance and recruitment annually to determine population health and trends, and to
detect and remove predators (trout) before they become established. This needs to be done annually to
detect any rapid population decline or predator presence before they breed and become established and
major loss in galaxiid abundance occurs.

Assess the location and type of instream barriers (if present) downstream of each population, including
their effectiveness at preventing the movement of trout upstream in higher flows.
o If a barrier is not present, translocate a subset of individuals immediately to a suitable captive or wild
destination
o
If a barrier is only partially effective, modify it to improve its effectiveness in preventing trout movement
upstream, or install a new vertical concrete barrier, as has occurred for other threatened galaxiid
populations.

Mitigate sediment input point sources from existing forestry tracks.

Close and rehabilitate redundant forestry tracks near the streams, removing stream crossings.

Provide more effective vegetative buffer zones along waterways, drainage lines and filter strips, in timber
harvesting coupes to prevent sediment transport into waterways during intense rainfall events.
To reduce the overall extinction threat

Carry out additional surveys in Rintoul Creek and unsampled western tributaries for the presence of Galaxias
sp. 9.

Assess nearby catchments to confirm potential translocations sites for establishment of additional populations of
each species.

Undertake translocations to establish new populations in the wild.

Avoid new roading crossing streams or drainage lines in key areas for these species.

Establish a protocol to monitor populations regularly during drought and immediately post-fire, and for ex situ
temporary captive maintenance if required.
Arthur Rylah Institute for Environmental Research Technical Report Series No. 248
37
Other aquatic fauna
Native burrowing crayfish of the genus Engaeus were found to be distributed widely across the study area, and in
particular, were abundant at high elevations on the Baw Baw Plateau in areas covered by snow during winter. While not
identified, as they were not a priority taxon and many records were based only on the presence of soil pellet ‘chimneys’,
six species could be present in the mid to upper La Trobe and Thomson catchments (Horwitz 1990). One species, the
Curve-tail Burrowing Crayfish (Engaeus curvisuturus) is rare and threatened (DSE 2009).1 It is known from only three
locations, two of which are in the upper La Trobe River catchment including the Baw Baw Plateau (Horwitz 1990).
Three additional species are also known from the upper La Trobe catchment: Tubercle Burrowing Crayfish (Engaeus
tuberculatus), Gippsland Burrowing Crayfish (Engaeus hemicirratulus), and Granular Burrowing Crayfish (Engaeus
cunicularius) (Horwitz 1990). Only E. hemicirratulus has been recorded previously from the Baw Baw Plateau. Targeted
sampling for the threatened E. curvisuturus is needed across its range from the upper Yarra River system to the La
Trobe catchment to more accurately define its distribution. Identification of the burrowing crayfish on the Baw Baw
Plateau is also required to improve our knowledge of their biodiversity and distribution.
Central Highlands Spiny Crayfish (Euastacus woiwuru) was also recorded extensively in the La Trobe and Thomson
catchments, and was widespread and abundant at locations sampled on the Baw Baw Plateau. With the Alpine Spiny
Crayfish (E. crassus), this species is one of only two freshwater spiny crayfish in Victoria that are regularly recorded from
locations covered by snow during winter (Morgan 1986, 1997), and is found in streams that freeze over during that time.
River Blackfish was found to have a wide distribution in the mid to upper La Trobe catchment, although found at very few
locations and in low abundance. This species lays adhesive, demersal eggs, inside timber (Jackson 1978), which, along
with larvae and juvenile fish, can be killed by sedimentation (Doeg and Koehn 1994). High levels of instream
sedimentation in the upper La Trobe River system may have reduced the overall abundance of this species. Further
monitoring of the stocks of River Blackfish in the mid to upper reaches of the La Trobe River system, including targeted
surveys and comparison with previous survey data, is needed to determine the status of this species and to define
population trends.
Brown Trout was the most widespread alien salmonid in the Thomson and La Trobe catchments, but importantly was
absent from the upper reaches of many smaller streams, and in particular, from the Baw Baw Plateau. Trout are
widespread in Victoria (VBA 2013) and trout (predator) free environments in the headwater reaches of small streams in
upland areas can be scarce (Ayres et al. 2012, Raadik unpublished data). This is particularly true for most sub-alpine
and alpine areas (e.g. Mount Buller – Mount Stirling, Mount Buffalo, Mount Hotham and Falls Creek), where many
streams contain Brown Trout or Rainbow Trout (VBA 2013), and also more widely across the Australian Alps, Brown
Trout having colonised streams almost to the summit of Mount Kosciusko (Green 2002, Raadik and Kuiter 2002, Green
2008). Their absence from the Baw Baw Plateau, which is probably due to the steep gradients and the number of natural
barriers present on the streams on the edges of the plateau, makes these aquatic environments unique and provides a
scarce, natural, predator-free refuge for upland galaxiids in particular.
Approximately half of the sites sampled for aquatic fauna lacked fish, the majority of these being small streams, although
many larger streams draining the Baw Baw Plateau were also fishless. The significance of this is unknown as data on
other fishless streams in Victoria have not been compiled or analysed. Data on zero captures could be lacking or
incomplete for some areas because collectors might not have counted a zero result as valuable and therefore may not
have retained these records or placed them on databases.
Many streams in the Thomson and La Trobe catchments are degraded by sediment slugs that smother the stream
substrate, reducing bed topography and structural habitat for aquatic fauna. This was particularly evident in the upper
reaches of the La Trobe River system, much of which appeared to be derived from recent and historical anthropogenic
catchment disturbance, including run-off from poorly maintained forest tracks. The loss or reduction in aquatic
macrohabitat and microhabitat in many of these streams is likely to have had a negative impact on the resident aquatic
communities through changes in community structure, alterations to species distributions, and changes in abundances.
However, this is difficult to quantify because of a lack of detailed baseline data, and a targeted study would be needed to
determine whether this is the case. Some species or faunal groups may be more persistent and resilient to disturbance
than others (e.g. some active burrows of Engaeus were constructed vertically through deep layers of silt and sand in
riparian zones affected by sedimentation), but others may be more sensitive (e.g. the apparent decline in River Blackfish
abundance and distribution). Preventing sediment from entering waterways in the La Trobe and Thomson catchments
would improve the condition of their aquatic ecosystems.
1
Note that Engaeus hemicirratulus, a widespread and abundant species, is incorrectly listed as threatened in DSE (2009).
Arthur Rylah Institute for Environmental Research Technical Report Series No. 248
38
Conclusion
This project has confirmed the rarity of two recently discovered, non-migratory native freshwater fish (Galaxias sp. 8 and
Galaxias sp. 9) and provides important information on their distribution, abundance, status and threats. This provides
new data to assist with managing biodiversity conservation in timber production areas. The new data also further
supports the conservation status of each species as critically endangered. For such narrow-range endemic species, this
could not have been achieved without the extensive, targeted field sampling undertaken during this project, which now
provides information that is also valuable for the development of a recovery plan and future conservation management.
In addition, intensive sampling has also provided supplementary aquatic biodiversity data, including qualitative
assessment of threats, from relatively poorly known mid to upland areas in the catchments. This data will be particularly
valuable for biodiversity conservation, current catchment management, and monitoring of future impacts from climate
change.
Arthur Rylah Institute for Environmental Research Technical Report Series No. 248
39
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Arthur Rylah Institute for Environmental Research Technical Report Series No. 248
41
Appendix 1 Location of sampling sites
Details of 120 sites sampled in upper Thomson River (25) and La Trobe River (26) basins, February–May 2012.
Basin
No.
Site
Waterbody
Latitude
Longitude
Altitude
(m)
26
TR-12-001
Hope Ck
–37.85164
146.24863
950
6/02/2012
26
TR-12-002
Hope Ck
–37.85496
146.25371
920
6/02/2012
26
TR-12-003
Faith Ck
–37.86599
146.25557
800
6/02/2012
26
TR-12-004
Long Ck
–37.87175
146.26614
860
6/02/2012
26
TR-12-005
Barnies Ck
–37.84307
146.27417
1510
6/02/2012
26
TR-12-006
Tyers R
–37.84204
146.27575
1520
6/02/2012
26
TR-12-007
Tyers R
–37.84371
146.27777
1500
6/02/2012
26
TR-12-008
Tanjil R
–37.842
146.26825
1480
6/02/2012
26
TR-12-009
West Tanjil Ck
–37.83205
146.27393
1481
7/02/2012
26
TR-12-010
West Tanjil Ck
–37.82904
146.28093
1480
7/02/2012
26
TR-12-011
Tyers R
–37.8356
146.28015
1460
7/02/2012
26
TR-12-012
Tanjil R
–37.84068
146.26702
1475
7/02/2012
26
TR-12-013
Tyers R
–37.87935
146.27541
780
7/02/2012
26
TR-12-014
Christmas Ck
–37.389505
146.28586
720
7/02/2012
26
TR-12-015
Growler Ck
–37.90678
146.29599
780
7/02/2012
26
TR-12-016
Faith Ck
–37.86941
146.24106
575
7/02/2012
26
TR-12-017
Hope Ck
–37.86359
146.23547
575
7/02/2012
26
TR-12-018
-
–37.83173
146.27408
1490
7/02/2012
26
TR-12-019
Tanjil R
–37.83888
146.26531
1460
8/02/2012
26
TR-12-020
Rum Ck
–37.87802
146.37889
660
8/02/2012
26
TR-12-021
Tyers R
–37.90064
146.35526
920
8/02/2012
26
TR-12-022
Tyers R
–37.90595
146.25411
380
8/02/2012
26
TR-12-023
Long Ck
–37.8817
146.24457
530
8/02/2012
26
TR-12-024
Good Hope Ck
–37.99527
146.248
270
9/02/2012
26
TR-12-025
Lady Manor Sutton Ck
–37.95192
146.21524
320
9/02/2012
26
TR-12-026
Tanjil R
–37.79869
146.19915
960
9/02/2012
26
TR-12-027
Toorongo R
–37.77909
146.10495
980
9/02/2012
26
TR-12-028
Mundic Ck
–37.78877
146.11566
1000
9/02/2012
26
TR-12-029
Tea Tree Ck
–37.99606
146.31222
270
9/02/2012
26
TR-12-030
Tea Tree Ck
–37.00079
146.31247
250
9/02/2012
29
TR-12-031
Falls Ck
–37.78995
146.12617
1020
9/02/2012
26
TR-12-032
Mundic Ck
–37.7821
146.11256
980
9/02/2012
26
TR-12-033
Regnans Ck
–37.83292
146.15328
740
10/02/2012
26
TR-12-034
Icy Ck
–37.86604
146.12267
520
10/02/2012
Arthur Rylah Institute for Environmental Research Technical Report Series No. 248
42
Date
Basin
No.
Site
Waterbody
Latitude
Longitude
Altitude
(m)
Date
26
TR-12-035
Deep Ck
–37.87232
145.97288
440
10/02/2012
25
TR-12-036
Dry Ck
–37.63472
146.34049
920
13/02/2012
25
TR-12-037
Red Jacket Ck
–37.61622
146.30266
720
13/02/2012
25
TR-12-038
Ross Ck
–37.61674
146.30338
710
13/02/2012
25
TR-12-039
Red Jacket Ck
–37.60194
146.28953
840
13/02/2012
25
TR-12-040
Poole Gully
–37.66355
146.22683
750
13/02/2012
25
TR-12-041
Poole Gully
–37.66214
146.24397
25
TR-12-042
Ferntree Ck
–37.61734
146.22938
880
13/02/2012
25
TR-12-043
Matlock Ck
–37.62519
146.17599
1210
14/02/2012
25
TR-12-044
Matlock Ck
–37.6681
146.15747
730
14/02/2012
25
TR-12-045
Thomson R
–37.68965
146.16289
1020
14/02/2012
29
TR-12-046
Woods Ck
–37.69341
146.13914
1070
14/02/2012
25
TR-12-047
Thomson R
–37.7287
146.1704
990
14/02/2012
25
TR-12-048
Whitelaw Ck Middle Br.
–37.75452
146.24457
1080
14/02/2012
25
TR-12-049
Whitelaw Ck
–37.77216
146.25209
1220
14/02/2012
25
TR-12-050
Whitelaw Ck
–37.7632
146.2486
1140
14/02/2012
25
TR-12-051
Thomson R
–37.74597
146.21427
1170
14/02/2012
25
TR-12-052
Thomson R
–37.74344
146.19915
1080
14/02/2012
25
TR-12-053
Matlock Ck
–37.65352
146.1403
1035
15/02/2012
25
TR-12-054
North Cascade Ck
–37.81166
146.32234
1140
15/02/2012
25
TR-12-055
Bell Clear Ck
–37.78307
146.2834
1140
15/02/2012
25
TR-12-056
Bell Clear Ck
–37.76947
146.2857
1020
15/02/2012
25
TR-12-057
Thomson R
–37.74749
146.21787
1180
15/02/2012
25
TR-12-058
Thomson R
–37.75997
146.17586
1070
15/02/2012
25
TR-12-059
Swift Ck
–37.8013
146.31126
1200
15/02/2012
26
TR-12-060
Tanjil R
–37.82409
146.25267
1325
16/02/2012
25
TR-12-061
Tanjil R
–37.82608
146.25487
1515
16/02/2012
25
TR-12-062
Aqueduct
–37.78587
146.20795
1185
16/02/2012
25
TR-12-063
Thomson R
–37.77518
146.20895
1085
16/02/2012
26
TR-12-064
Big Ck
–37.85752
145.83254
350
17/02/2012
26
TR-12-065
Pioneer Ck
–37.89881
145.79192
650
17/02/2012
26
TR-12-066
La Trobe R
–37.88001
145.78006
400
17/02/2012
26
TR-12-067
Dead Horse Ck
-38.01929
146.02126
200
19/03/2012
26
TR-12-068
Starvation Ck
-38.038
146.06756
170
19/03/2012
26
TR-12-069
Stanley Vale Ck
–37.98206
146.03191
300
19/03/2012
26
TR-12-070
Wild Bull Ck
–37.97229
146.10725
209
19/03/2012
26
TR-12-071
Hawthorn Ck
–37.92949
146.06862
285
19/03/2012
26
TR-12-072
Mundic Ck
–37.810662
146.10008
930
20/03/2012
26
TR-12-073
Mundic Ck
–37.81328
146.12457
1000
20/03/2012
13/02/2012
Arthur Rylah Institute for Environmental Research Technical Report Series No. 248
43
Basin
No.
Site
Waterbody
Latitude
Longitude
Altitude
(m)
26
TR-12-074
Walkers Ck
–37.81191
146.14222
1010
20/03/2012
26
TR-12-075
Toorongo R
–37.782178
146.09301
870
20/03/2012
26
TR-12-076
Toorongo R
–37.76613
146.08179
925
20/04/2012
26
TR-12-077
Toorongo R
–37.782259
1446.06688
7900
20/03/2012
26
TR-12-078
Icy Ck
–37.78329
146.05273
830
20/03/2012
26
TR-12-079
Carter Ck
–37.80441
146.03274
630
20/03/2012
26
TR-12-080
Cascade Ck
–37.83573
146.01078
480
20/03/2012
26
TR-12-081
Tanjil R
–37.82142
146.2719
1395
21/03/2012
26
TR-12-082
Tanjil R
–37.81959
146.27011
1360
21/03/2012
26
TR-12-083
West Tanjil Ck
–37.8197
146.27015
1365
21/03/2012
26
TR-12-084
West Tanjil Ck
–37.82519
146.27356
1425
21/03/2012
26
TR-12-085
Pennyweight Ck
–37.8858
146.08207
440
21/03/2012
26
TR-12-086
Kennedys Ck
–37.8013
146.00737
480
22/03/2012
26
TR-12-087
Loch R
–37.80402
145.98636
365
22/03/2012
26
TR-12-088
Bennet Ck
–37.78181
146.00662
680
22/03/2012
26
TR-12-089
Skerry Ck
–37.77436
145.99089
810
22/03/2012
26
TR-12-090
Skerry Ck
–37.78775
145.97241
460
22/03/2012
26
TR-12-091
Loch R
–37.79343
145.94445
490
22/03/2012
26
TR-12-092
Litaize Ck
–37.81149
145.95981
505
22/03/2012
26
TR-12-093
Litaize Ck
–37.81797
145.95113
615
22/03/2012
26
TR-12-094
Russell Ck
–37.83665
145.96489
385
22/03/2012
26
TR-12-095
Bennie Ck
–37.87163
145.93976
275
22/03/2012
26
TR-12-096
Lavery Ck
–37.88994
145.87025
370
23/03/2012
26
TR-12-097
Lavery Ck
–37.90248
145.88673
415
23/03/2012
26
TR-12-098
Jacky Ck
–37.90675
145.81136
715
23/03/2012
25
TR-12-099
Jordan R
–37.64027
146.19424
940
13/02/2012
26
TR-12-111
Rintoul Ck
-38.03589
146.46931
230
30/04/2012
26
TR-12-112
Rintoul Ck
-38.0357
146.46897
235
30/04/2012
26
TR-12-113
Jacobs Ck
–37.99567
146.39866
315
30/04/2012
26
TR-12-114
Hotel Ck
–37.94715
146.37912
455
30/04/2012
26
TR-12-115
Rintoul Ck
-38.06436
146.48416
150
1/05/2012
26
TR-12-116
Rintoul Ck
-38.04325
146.47945
195
1/05/2012
25
TR-12-117
Stoney Ck
–37.9029
146.54254
445
1/05/2012
26
TR-12-118
Rintoul Ck
-38.03085
146.45094
275
1/05/2012
25
TR-12-119
Stoney Ck
–37.93733
146.6119
230
1/05/2012
25
TR-12-140
Stoney Ck
–37.94179
146.56247
340
4/05/2012
26
TR-12-141
Eaglehawk Ck
-38.10383
146.52275
130
4/05/2012
26
TR-12-142
Rintoul Ck
-38.11462
146.47562
135
14/05/2012
26
TR-12-143
Iseppis Ck
-38.0301
146.53044
240
14/05/2012
Arthur Rylah Institute for Environmental Research Technical Report Series No. 248
44
Date
Basin
No.
Site
Waterbody
Latitude
Longitude
Altitude
(m)
25
TR-12-157
Glenmaggie Ck
–37.85819
146.62653
380
15/06/2012
25
TR-12-158
Glenmaggie Ck
–37.83545
146.6281
420
16/05/2012
25
TR-12-159
Springs Ck
–37.75801
146.56293
745
16/05/2012
25
TR-12-160
Mt Useful Ck
–37.69543
146.52286
740
16/05/2012
25
TR-12-161
Stoney Ck
–37.94263
146.59918
350
17/05/2012
26
TR-12-162
Ada R
–37.81854
145.80905
690
17/05/2012
26
TR-12-163
Little Ada R
–37.82651
145.85049
700
18/05/2012
26
TR-12-164
Ada R
–37.83578
145.84077
650
18/05/2012
Arthur Rylah Institute for Environmental Research Technical Report Series No. 248
45
Date
Appendix 2 Summary of survey results
Summary of aquatic fauna (fish and decapod crustacea) sampled at each survey site in the upper Thomson River and La
Trobe River catchments, February–May 2012.
Refer to Appendix 1 for site locations and Table 1 for species common names. (# – indicates presence based on
secondary evidence of soil-pellet ‘chimney’ at burrow entrance).
Site
Waterbody
Scientific Name
Number
TR-12-001
Hope Creek
Euastacus woiwuru
4
TR-12-002
Hope Creek
no fauna
TR-12-003
Faith Creek
Euastacus woiwuru
1
TR-12-004
Long Creek
Engaeus sp.
observed#
Euastacus woiwuru
3
TR-12-005
Barnies Creek
no fauna
TR-12-006
Tyers River
no fauna
TR-12-007
Tyers River
no fauna
TR-12-008
Tanjil River
no fauna
TR-12-009
West Tanjil Creek
almost dry
TR-12-010
West Tanjil Creek
Engaeus sp.
observed#
TR-12-011
Tyers River
Engaeus sp.
observed#
TR-12-012
Tanjil River
Euastacus woiwuru
observed
TR-12-013
Tyers River
Euastacus woiwuru
4
TR-12-014
Christmas Creek
Euastacus woiwuru
4
TR-12-015
Growler Creek
Engaeus sp.
observed#
Euastacus woiwuru
4
Engaeus sp.
observed#
Euastacus woiwuru
observed
Engaeus sp.
observed#
Euastacus woiwuru
observed
Engaeus sp.
observed#
TR-12-016
TR-12-017
Faith Creek
Hope Creek
TR-12-018
TR-12-019
Tanjil River
Euastacus woiwuru
observed
TR-12-020
Rum Creek
Euastacus woiwuru
5
TR-12-021
Tyers River
Euastacus woiwuru
8
TR-12-022
Tyers River
Euastacus kershawi
3
Gadopsis marmoratus
3
Salmo trutta
11
Engaeus sp.
observed#
Euastacus woiwuru
observed
Gadopsis marmoratus
33
Paratya australiensis
observed
Salmo trutta
1
TR-12-023
TR-12-024
Long Creek
Good Hope Creek
Arthur Rylah Institute for Environmental Research Technical Report Series No. 248
46
Site
Waterbody
Scientific Name
Number
TR-12-025
Lady Manor Sutton Creek
Anguilla australis
1
Euastacus kershawi
1
Engaeus sp.
observed#
Euastacus woiwuru
7
Engaeus sp.
observed#
Euastacus woiwuru
1
Engaeus sp.
observed#
Euastacus woiwuru
observed
TR-12-026
TR-12-027
TR-12-028
Tanjil River
Toorongo River
Mundic Creek
TR-12-029
Tea Tree Creek
dry
TR-12-030
Tea Tree Creek
dry
TR-12-031
Falls Creek
Engaeus sp.
TR-12-032
Mundic Creek
dry
TR-12-033
Regnans Creek
Euastacus woiwuru
observed
TR-12-034
Icy Creek
Euastacus woiwuru
1
Gadopsis marmoratus
5
Oncorhynchus mykiss
1
Salmo trutta
9
TR-12-035
Deep Creek
observed#
dry
Engaeus sp.
observed#
TR-12-036
Dry Creek
dry
TR-12-037
Red Jacket Creek
Engaeus sp.
observed#
Salmo trutta
11
Engaeus sp.
observed#
Salmo trutta
9
TR-12-038
Ross Creek
TR-12-039
Red Jacket Creek
dry
TR-12-040
Poole Gully
Euastacus woiwuru
1
Salmo trutta
1
TR-12-041
Poole Gully
dry
TR-12-042
Ferntree Creek
no fauna
TR-12-043
Matlock Creek
no fauna
TR-12-044
Matlock Creek
Oncorhynchus mykiss
9
Salmo trutta
18
TR-12-045
Thomson River
dry
TR-12-046
Woods Creek
Cherax destructor
10
Paratya australiensis
observed
Salmo trutta
8
TR-12-047
Thomson River
no fauna
TR-12-048
Whitelaw Creek Middle Branch
Euastacus woiwuru
3
TR-12-049
Whitelaw Creek
Engaeus sp.
observed#
Euastacus woiwuru
2
Arthur Rylah Institute for Environmental Research Technical Report Series No. 248
47
Site
Waterbody
Scientific Name
Number
TR-12-050
Whitelaw Creek
Engaeus sp.
observed#
Euastacus woiwuru
7
TR-12-051
Thomson River
no fauna
TR-12-052
Thomson River
no fauna
TR-12-053
Matlock Creek
no fauna
TR-12-054
North Cascade Creek
Euastacus woiwuru
5
TR-12-055
Bell Clear Creek
Engaeus sp.
observed#
TR-12-056
Bell Clear Creek
Euastacus woiwuru
3
TR-12-057
Thomson River
no fauna
TR-12-058
Thomson River
Salmo trutta
TR-12-059
Swift Creek
No fauna
TR-12-060
Tanjil River
Engaeus sp.
observed#
Euastacus woiwuru
observed
Engaeus sp.
observed#
Euastacus woiwuru
6
TR-12-061
Tanjil River
2
TR-12-062
Aqueduct
dry
TR-12-063
Thomson River
Euastacus woiwuru
2
Salmo trutta
21
Engaeus sp.
observed#
Euastacus woiwuru
4
Gadopsis marmoratus
3
Salmo trutta
6
Engaeus sp.
observed#
Euastacus woiwuru
9
Engaeus sp.
observed#
Euastacus woiwuru
observed
Gadopsis marmoratus
2
Salmo trutta
2
Engaeus sp.
observed#
Euastacus kershawi
observed
Gadopsis marmoratus
3
Salmo trutta
9
Cherax destructor
1
Engaeus sp.
2
Anguilla australis
1
Engaeus sp.
observed#
Engaeus sp.
observed#
Euastacus kershawi
1
Paratya australiensis
observed
Salmo trutta
8
TR-12-064
TR-12-065
TR-12-066
TR-12-067
TR-12-068
TR-12-069
TR-12-070
Big Creek
Pioneer Creek
La Trobe River
Dead Horse Creek
Starvation Creek
Stanley Vale Creek
Wild Bull Creek
Arthur Rylah Institute for Environmental Research Technical Report Series No. 248
48
Site
Waterbody
Scientific Name
Number
TR-12-071
Hawthorn Creek
Engaeus sp.
observed#
Euastacus kershawi
3
Salmo trutta
6
Engaeus sp.
observed#
Euastacus woiwuru
7
TR-12-072
Mundic Creek
TR-12-073
Mundic Creek
Euastacus woiwuru
1
TR-12-074
Walkers Creek
Euastacus woiwuru
1
TR-12-075
Toorongo River
Euastacus woiwuru
2
TR-12-076
Toorongo River
Euastacus woiwuru
1
Salmo trutta
10
Engaeus sp.
observed#
Salmo trutta
1
TR-12-077
Toorongo River
TR-12-078
Icy Creek
Euastacus woiwuru
observed
TR-12-079
Carter Creek
Engaeus sp.
observed#
TR-12-080
Cascade Creek
Engaeus sp.
observed#
Euastacus woiwuru
1
observed#
TR-12-081
Tanjil River
Engaeus sp.
TR-12-082
Tanjil River
no fauna
TR-12-083
West Tanjil Creek
Euastacus woiwuru
observed
TR-12-084
West Tanjil Creek
Engaeus sp.
observed#
TR-12-085
Pennyweight Creek
Oncorhynchus mykiss
3
Salmo trutta
5
Engaeus sp.
observed#
Euastacus woiwuru
1
Salmo trutta
2
TR-12-086
Kennedys Creek
TR-12-087
Loch River
dry
TR-12-088
Bennet Creek
Engaeus sp.
observed#
Euastacus woiwuru
observed
TR-12-089
Skerry Creek
Engaeus sp.
observed#
TR-12-090
Skerry Creek
Engaeus sp.
observed#
Euastacus woiwuru
1
Salmo trutta
11
Engaeus sp.
observed#
Euastacus woiwuru
6
Gadopsis marmoratus
2
Salmo trutta
10
Engaeus sp.
observed#
Euastacus woiwuru
3
TR-12-091
TR-12-092
Loch River
Litaize Creek
Arthur Rylah Institute for Environmental Research Technical Report Series No. 248
49
Site
Waterbody
Scientific Name
Number
TR-12-093
Litaize Creek
Engaeus sp.
observed#
TR-12-094
Russell Creek
Engaeus sp.
observed#
Euastacus woiwuru
2
Salmo trutta
6
Engaeus sp.
observed#
Euastacus kershawi
3
Euastacus woiwuru
1
Gadopsis marmoratus
2
Salmo trutta
12
TR-12-095
Bennie Creek
TR-12-096
Lavery Creek
Engaeus sp.
observed#
TR-12-097
Lavery Creek
Engaeus sp.
observed#
Euastacus woiwuru
4
Engaeus sp.
observed#
Euastacus woiwuru
6
TR-12-098
Jacky Creek
TR-12-099
Jordan River
no fauna
TR-12-111
Rintoul Creek
Anguilla australis
5
Engaeus sp.
2
Euastacus kershawi
5
Galaxias brevipinnis
2
Paratya australiensis
observed
Anguilla australis
observed
Engaeus sp.
observed#
Euastacus kershawi
observed
Galaxias sp. 9
2
Paratya australiensis
observed
Engaeus sp.
observed#
Euastacus kershawi
4
Gadopsis marmoratus
13
Paratya australiensis
observed
Salmo trutta
1
Engaeus sp.
observed#
Euastacus kershawi
observed
Anguilla australis
observed
Engaeus sp.
observed#
Euastacus kershawi
9
Galaxias brevipinnis
2
Galaxias maculatus
3
Paratya australiensis
observed
Retropinna semoni
11
TR-12-112
TR-12-113
TR-12-114
TR-12-115
Rintoul Creek
Jacobs Creek
Hotel Creek
Rintoul Creek
Arthur Rylah Institute for Environmental Research Technical Report Series No. 248
50
Site
Waterbody
Scientific Name
Number
TR-12-116
Rintoul Creek
Anguilla australis
observed
Engaeus sp.
observed#
Euastacus kershawi
3
Galaxias brevipinnis
3
Galaxias sp. 9
2
Paratya australiensis
observed
Anguilla australis
observed
Euastacus woiwuru
2
Galaxias sp. 8
33
Paratya australiensis
observed
Anguilla australis
observed
Engaeus sp.
1
Euastacus kershawi
2
Galaxias sp. 9
4
Paratya australiensis
observed
Paratya australiensis
observed
Salmo trutta
1
Anguilla australis
observed
Euastacus kershawi
2
Galaxias brevipinnis
2
Galaxias sp. 8
8
Paratya australiensis
observed
TR-12-117
TR-12-118
TR-12-119
TR-12-140
Stoney Creek
Rintoul Creek
Stoney Creek
Stoney Creek
TR-12-141
Eaglehawk Creek
Engaeus sp.
2
TR-12-142
Rintoul Creek
Engaeus sp.
3
TR-12-143
Iseppis Creek
Anguilla australis
1
Paratya australiensis
observed
Galaxias brevipinnis
17
Paratya australiensis
observed
Galaxias brevipinnis
37
Paratya australiensis
observed
2
TR-12-157
TR-12-158
Glenmaggie Creek
Glenmaggie Creek
TR-12-159
Springs Creek
Euastacus woiwuru
TR-12-160
Mt Useful Creek
no fauna
TR-12-161
Stoney Creek
Euastacus kershawi
2
Paratya australiensis
observed
Engaeus sp.
observed#
Euastacus woiwuru
9
Engaeus sp.
observed#
Euastacus kershawi
3
Salmo trutta
9
Engaeus sp.
observed#
Euastacus woiwuru
17
TR-12-162
TR-12-163
TR-12-164
Ada River
Little Ada River
Ada River
Arthur Rylah Institute for Environmental Research Technical Report Series No. 248
51
Appendix 3 Summary of site characteristics
Summary of survey details and site and water quality characteristics at sites in the upper Thomson River and La Trobe
River catchments during February to May, 2012 (excludes dry sites). Note site code has been shortened ('TR-12-'
removed). See Appendix 1 for site locations.
(EC – water electrical conductivity at 25°C, expressed in EC units; DO – dissolved oxygen).
Site
Waterbody
Code
Survey
Ave.
Max.
Ave.
Length
Width
Depth
Depth
(m)
(m)
(m)
(m)
EC
Water
DO
DO
temp
mg/L
%Sat.
pH
Turbidity
(NTU)
o
C
001
Hope Ck
50
0.8
0.15
0.05
50.4
11.8
8.7
85
8.6
<5.0
002
Hope Ck
45
1.3
0.6
0.15
19
10.1
9.2
85
8.5
<5.0
003
Faith Ck
50
1
5
0.1
26.5
12.3
8.5
85
8.3
<5.0
004
Long Ck
50
1.2
0.4
0.1
32.5
11.8
9.2
80
8
<5.0
005
Barnies Ck
5
0.3
0.01
0.005
006
Tyers R
10
1
0.3
0.1
007
Tyers R
30
0.6
0.2
0.01
008
Tanjil R
0.5
0.2
0.05
010
West Tanjil Ck
30
0.6
0.3
0.05
10.3
9.6
11.5
101.9
8.5
0
011
Tyers R
50
11.9
10.1
9.1
81
7.6
0
012
Tanjil R
10
013
Tyers R
50
12
014
Christmas Ck
25
015
Growler Ck
50
016
Faith Ck
017
Hope Ck
018
-
019
0.8
0.5
0.2
15
1.5
0.5
19.1
11.6
10.4
96
7.6
10
0.7
0.4
22.9
11.3
10.7
98
7.6
8.7
1.1
0.4
0.2
35.8
11
10.4
98
7.8
<5.0
55
3
0.3
0.07
35
6
0.5
0.15
Tanjil R
60
1
0.7
0.15
14.9
8.6
10.6
92
7.8
<5.0
020
Rum Ck
20
1.8
0.6
0.1
21.5
11.8
10.4
97
7.6
0
021
Tyers R
50
4
1
0.2
18.7
10.3
10.2
92
7.6
0
022
Tyers R
55
14
0.4
0.15
21.5
13.2
8.7
84
7.9
<5.0
023
Long Ck
50
1.4
0.3
0.1
024
Good Hope Ck
50
3
1
0.4
210
15.3
4.7
48.5
7.1
5
025
Lady Manor
Sutton Ck
50
3
1.25
0.4
335
15.8
7.1
72
7.1
15
026
Tanjil R
55
7
1
0.3
17.9
11.3
9.7
92
8.2
0
027
Toorongo R
50
0.6
0.4
0.08
25.6
13.6
7.3
71
7.8
<5.0
028
Mundic Ck
30
0.15
0.05
031
Falls Ck
033
Regnans Ck
50
0.5
0.3
0.1
034
Icy Ck
50
8
0.6
0.15
36.2
14
9.3
88
7.8
<5.0
Arthur Rylah Institute for Environmental Research Technical Report Series No. 248
52
Site
Waterbody
Code
Survey
Ave.
Max.
Ave.
Length
Width
Depth
Depth
(m)
(m)
(m)
(m)
EC
Water
DO
DO
temp
mg/L
%Sat.
pH
Turbidity
(NTU)
o
C
037
Red Jacket Ck
25
0.7
0.15
0.05
46
13.5
9
85.5
8.7
0
038
Ross Ck
45
0.5
0.1
0.05
46
13.5
9
85.5
8.7
0
040
Poole Gully
50
0.8
0.3
0.1
39.6
12.7
9.5
91.3
8
042
Ferntree Ck
60
1
043
Matlock Ck
30
044
Matlock Ck
50
5
0.3
0.1
27.4
11.4
10.2
92
7.8
0
046
Woods Ck
25
1.5
0.3
0.1
47
17.1
5.8
70
7.7
5
047
Thomson R
50
0.4
0.2
0.05
048
Whitelaw Ck
Middle Branch
45
1.5
0.6
0.15
19.6
12.1
10.2
97
8.7
5
049
Whitelaw Ck
35
0.8
0.15
0.05
16.8
12.3
8.8
80
8.6
0
050
Whitelaw Ck
30
5
0.7
0.15
17.7
11.8
8.3
76.6
8.2
5
051
Thomson R
10
0.3
0.4
0.2
052
Thomson R
50
1.5
0.4
0.1
053
Matlock Ck
70
1
0.3
0.08
18
12
8.9
90.9
8.8
5
054
North Cascade
Ck
50
7
0.7
0.2
10.3
13.3
9.9
99
8.7
5
055
Bell Clear Ck
35
2.2
0.6
0.15
16.4
10.8
10.1
91
8.1
5
056
Bell Clear Ck
50
1
0.15
0.05
26.3
12.9
9.7
90
7.6
0
057
Thomson R
30
0.4
0.6
0.2
25.5
16.1
6
65
7.3
5
058
Thomson R
059
Swift Ck
15
0.3
0.3
0.05
060
Tanjil R
1.1
1.2
0.7
061
Tanjil R
063
Thomson R
50
4.5
0.5
0.15
16.1
11.5
9.6
96
7.9
0
064
Big Ck
45
1.4
0.3
0.1
56.8
15
8.2
83
7.8
5
065
Pioneer Ck
50
1.7
0.4
0.1
35.3
13
9.9
94.5
8.1
5
066
La Trobe R
35
2
0.3
0.1
50.1
14.5
7.7
76
7.7
5
067
Dead Horse Ck
60
0.7
0.4
0.1
554
15.5
7.5
73.8
7.6
0
068
Starvation Ck
50
0.5
0.4
0.2
1153
15.3
6.3
64
6.7
5
069
Stanley Vale
Ck
50
0.7
0.5
0.15
470
15.1
77.8
7.4
5
070
Wild Bull Ck
80
0.7
0.5
0.2
353
15.7
8.5
85
7.2
5
071
Hawthorn Ck
70
0.9
0.7
0.3
170.9
15.1
8.2
70
6.8
5
072
Mundic Ck
70
1.8
1.1
0.3
25
10.5
7.8
85
6.5
0
073
Mundic Ck
10
0.4
0.5
0.1
19.9
9.8
8.7
77
6.18
0
074
Walkers Ck
50
0.4
0.3
0.1
21.6
11.6
9.9
96
6.7
0
075
Toorongo R
50
0.9
1.2
0.3
31.6
11.4
9.6
95
6.2
5
076
Toorongo R
50
0.7
1.5
0.2
20.5
11
9.5
86.2
6.3
0
78
Arthur Rylah Institute for Environmental Research Technical Report Series No. 248
53
<5.0
Site
Waterbody
Code
Survey
Ave.
Max.
Ave.
Length
Width
Depth
Depth
(m)
(m)
(m)
(m)
077
Toorongo R
50
0.4
0.4
0.1
078
Icy Ck
30
0.6
0.3
0.07
079
Carter Ck
15
0.25
0.1
0.02
080
Cascade Ck
50
0.4
0.4
0.1
081
Tanjil R
082
Tanjil R
35
5
1
0.3
083
West Tanjil Ck
40
4
0.7
0.2
084
West Tanjil Ck
60
0.4
0.6
0.3
085
Pennyweight
Ck
60
2.2
0.8
086
Kennedys Ck
50
0.4
088
Bennet Ck
50
089
Skerry Ck
090
EC
Water
DO
DO
temp
mg/L
%Sat.
pH
Turbidity
(NTU)
o
C
22.9
13.4
9.4
98
6.8
0
112.7
14.7
9
97
6.9
20
0.2
37.4
13.2
10.8
103
6.7
14
0.3
0.08
50.2
11.1
9.7
87
6.9
20
0.3
0.25
0.08
33.7
10.1
10.5
92
6.9
0
12
0.2
0.04
0.02
Skerry Ck
60
0.4
0.4
0.1
37.5
11.3
10.1
90
6.9
0
091
Loch R
60
1.4
0.4
0.15
49.6
12.3
9.1
85
6.8
5
092
Litaize Ck
40
0.3
0.3
0.1
0.3
12.8
9.5
92
7.3
0
093
Litaize Ck
50
0.5
0.4
0.1
45.1
12.3
9.2
87
7
0
094
Russell Ck
50
45.6
12.7
9.2
88
7.1
5
095
Bennie Ck
50
1.2
0.7
0.25
44.7
12.8
8.7
82
6.8
0
096
Lavery Ck
35
0.5
0.25
0.05
097
Lavery Ck
50
0.3
0.15
0.05
69.9
11.7
8.5
83
7.15
10
098
Jacky Ck
35
0.6
0.3
0.08
37.1
9.7
9.8
87
5.8
0
099
Jordan R
30
0.3
111
Rintoul Ck
265
1.6
0.7
0.15
260
9.9
8.3
76
6.5
0
112
Rintoul Ck
100
1.3
0.7
0.2
113
Jacobs Ck
50
202
11.3
7.9
73
6
10
114
Hotel Ck
50
115
Rintoul Ck
125
116
Rintoul Ck
117
1.2
0.4
0.1
249
10.5
9.1
83.4
6
5
2
0.5
0.2
243
9.9
10.3
92.6
6.5
5
80
2.1
0.8
0.2
252
9.8
11.3
98
6.5
0
Stoney Ck
100
2.1
0.8
0.15
111.7
11.4
9.3
90
6.5
0
118
Rintoul Ck
100
1.1
0.6
0.15
285
10
8.8
79
6
0
119
Stoney Ck
35
6
1.5
0.4
160.7
11.9
10.3
96
6.5
0
140
Stoney Ck
165
3.8
0.6
0.2
135
9.9
10.7
97
6.5
0
141
Eaglehawk Ck
65
0.4
0.3
0.04
1380
11.1
10.9
100
7
500
142
Rintoul Ck
70
1
0.4
0.15
690
11.3
11.4
104
6.5
400
143
Iseppis Ck
70
1.3
0.5
0.2
360
10.3
11.3
100
7.5
10
157
Glenmaggie Ck
150
3.5
0.8
0.25
110.5
7.8
11.1
95
6
0
158
Glenmaggie Ck
120
3
0.7
0.2
116.1
7.8
10.9
91
6
0
Arthur Rylah Institute for Environmental Research Technical Report Series No. 248
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Site
Waterbody
Code
Survey
Ave.
Max.
Ave.
Length
Width
Depth
Depth
(m)
(m)
(m)
(m)
EC
Water
DO
DO
temp
mg/L
%Sat.
pH
Turbidity
(NTU)
o
C
159
Springs Ck
80
1.8
1.2
0.25
38.2
7.8
11.5
87
6.5
0
160
Mt Useful Ck
55
1.8
1.1
0.15
39.5
8.6
11.5
98
6.5
0
161
Stoney Ck
190
1.3
0.4
0.1
268
7.7
7.9
64.7
6.5
0
162
Ada R
50
1.1
0.3
0.1
30.9
8.2
11.6
98.9
6
0
163
Little Ada R
60
2
0.6
0.2
28.7
6.9
11.5
94
5.5
0
164
Ada R
65
2.3
0.6
0.25
31.1
7.2
11.5
99
6
0
Arthur Rylah Institute for Environmental Research Technical Report Series No. 248
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Arthur Rylah Institute for Environmental Research Technical Report Series No. 248
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