hardey resource: aquatic ecosystem surveys€¦ · pre- & post-wet 2010 sampling final report...
TRANSCRIPT
API MANAGEMENT PTY. LTD.
PRE- & POST-WET 2010 SAMPLING
FINAL REPORT
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Wetland Research & Management
January 2011
Hardey Aquatic Surveys: 2010 Wetland Research & Management
ii
Study Team
Project Management: Jess Delaney and Andrew Storey
Field work: Jess Delaney, Isaac Cook, Caroline Lever (API)
Macroinvertebrate identification: Adam Harman, Isaac Cook, Ness Rosenow and Jess
Delaney
Microinvertebrate identification: Russ Shiel, University of Adelaide
Report: Jess Delaney and Isaac Cook
Reviewed by: Andrew Storey
Recommended Reference Format
WRM (2011) Hardey Resource: Aquatic Ecosystem Surveys. Unpublished DRAFT report by
Wetland Research & Management to API Management Pty. Ltd. January 2011.
Acknowledgements
This report was written by Wetland Research and Management (WRM) for API Management
Pty. Ltd (API). WRM would like to acknowledge Michelle Carey for efficient overall
management on behalf of API. Caroline Lever is thanked for assistance with field logistics,
and for help during both field trips. Her assistance is greatly appreciated. Fish photographs
were provided by Dr Mark Allen and the dragonfly picture was provided by Dr Jan Taylor.
The draft report was reviewed by Caroline Lever (API).
Disclaimer
This document was based on the best information available at the time of writing. While
Wetland Research & Management (WRM) has attempted to ensure that all information
contained within this document is accurate, WRM does not warrant or assume any legal
liability or responsibility to any third party for the accuracy, completeness, or usefulness of
any information supplied. The views and opinions expressed within are those of WRM and
do not necessarily represent API policy. No part of this publication may be reproduced in
any form, stored in any retrieval system or transmitted by any means electronic,
mechanical, photocopying, recording or otherwise, without the prior written permission of
API and WRM.
This document has been printed on ‘Reflex Green Recycled Paper’.
Frontispiece (top to bottom): Hardey River at Kazput Pool (site HR5) (photo by Jess Delaney/WRM,
Jan 2010); view from the Hardey Resource (photo by Jess Delaney/WRM, Jan2010); and, the Pilbara
Tiger dragonfly (photo by Jan Taylor).
Hardey Aquatic Surveys: 2010 Wetland Research & Management
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CONTENTS
1 INTRODUCTION .................................................................................................................................................... 1
1.1 Background .............................................................................................................. 1
1.2 Study objectives ...................................................................................................... 1
2 METHODS ............................................................................................................................................................... 3
2.1 Study area ................................................................................................................ 3
2.1.1 Climate .................................................................................................................................................. 3
2.2 Sites and sampling design ..................................................................................... 4
2.3 Water quality ............................................................................................................ 7
2.4 Microinvertebrates ................................................................................................... 9
2.5 Hyporheic fauna ...................................................................................................... 9
2.6 Macroinvertebrates ............................................................................................... 10
2.7 Fish .......................................................................................................................... 10
3 RESULTS AND DISCUSSION .......................................................................................................................... 12
3.1 Water quality .......................................................................................................... 12
3.1.1 Physico-chemistry ............................................................................................................................. 12
3.2 Microinvertebrates ................................................................................................. 18
3.2.1 Taxonomic composition and species richness.............................................................................. 18
3.2.2 Conservation significance of microinvertebrates .......................................................................... 19
3.3 Hyporheic fauna .................................................................................................... 21
3.3.1 Taxonomic composition and species richness.............................................................................. 21
3.3.2 Hyporheos taxa .................................................................................................................................. 22
3.4 Macroinvertebrates ............................................................................................... 23
3.4.1 Taxonomic composition and species richness.............................................................................. 23
3.4.2 Conservation significance of macroinvertebrates ......................................................................... 25
3.4.3 Functional feeding groups ................................................................................................................ 26
3.5 Fish .......................................................................................................................... 28
3.5.1 Species richness ............................................................................................................................... 28
3.5.2 Conservation significance of fish fauna ......................................................................................... 28
3.5.3 Length Frequency Analysis.............................................................................................................. 29
4 CONCLUSIONS ................................................................................................................................................... 37
4.1 Water quality .......................................................................................................... 37
4.2 Microinvertebrate fauna ....................................................................................... 38
4.3 Hyporheic fauna .................................................................................................... 38
4.4 Macroinvertebrate fauna ...................................................................................... 39
4.5 Fish .......................................................................................................................... 39
5 RECOMMENDATIONS ....................................................................................................................................... 41
6 REFERENCES ..................................................................................................................................................... 42
APPENDICES ................................................................................................................................................................ 46
Appendix 1. Site photographs ........................................................................................ 47
Appendix 2. ANZECC/ARMCANZ (2000) trigger values for the protection of aquatic systems in tropical northern Australia .............................................................. 49
Appendix 3. Water quality data from January and May 2010. .................................. 51
Appendix 4. Microinvertebrate data from January and May 2010. .................................. 53
Appendix 5. Hyporheic fauna recorded from the Hardey and Beasley rivers in January and
May 2010. ............................................................................................................................ 57
Appendix 6. Macroinvertebrate data from January and May 2010. ................................... 59
Hardey Aquatic Surveys: 2010 Wetland Research & Management
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LIST OF TABLES, FIGURES & PLATES
TABLES TABLE 1. AQUATIC SAMPLE SITES, THEIR GPS LOCATION AND TYPE (POTENTIAL IMPACT OR REFERENCE). .......................... 5 TABLE 2. ALL WATER QUALITY PARAMETERS MEASURED. ............................................................................................... 8 TABLE 3. COMPOSITION OF MICROINVERTEBRATE FAUNA RECORDED FROM THE STUDY AREA IN JANUARY AND MAY 2010. . 18 TABLE 4. COMPOSITION OF MICROINVERTEBRATE FAUNA RECORDED FROM THE HARDEY RIVER AND BEASLEY RIVER DURING
THE CURRENT STUDY. ..................................................................................................................................... 18 TABLE 5. COMPOSITION OF MACROINVERTEBRATES RECORDED FROM THE STUDY AREA IN JANUARY AND MAY 2010. ........ 23 TABLE 6. COMPOSITION OF MACROINVERTEBRATES RECORDED FROM THE HARDEY AND BEASLEY RIVERS DURING THE
CURRENT STUDY. ............................................................................................................................................ 24 TABLE 7. LIST OF FISH SPECIES RECORDED FROM EACH SITE. � INDICATES PRESENCE IN JANUARY, * INDICATES PRESENCE IN
MAY 2010. .................................................................................................................................................... 29
FIGURES FIGURE 1. LOCATION OF THE HARDEY RESOURCE IN THE PILBARA REGION OF W.A., SHOWING THE HARDEY AND BEASLEY
RIVER SYSTEMS. ............................................................................................................................................... 2 FIGURE 2. RAINFALL AT THE AIRSTRIP GAUGING STATION ON THE HARDEY RIVER, SHOWING AVERAGE TOTAL MONTHLY
RAINFALL (LEFT) AND TOTAL ANNUAL RAINFALL (RIGHT). ....................................................................................... 4 FIGURE 3. TOTAL MONTHLY RAINFALL (MM) AND TOTAL MONTHLY STREAMFLOW VOLUME (ML) DATA FOR THE MT SAMSON
GAUGING STATION ON THE HARDEY RIVER. ......................................................................................................... 4 FIGURE 4. PLOT SHOWING RAINFALL IN FEBRUARY, MARCH AND APRIL OF 2010 RECORDED FROM THE HARDEY RIVER
AIRSTRIP STATION, COMPARED WITH AVERAGE HISTORIC RAINFALL DURING THESE MONTHS. ..................................... 5 FIGURE 5. LOCATION OF THE HARDEY RIVER POTENTIAL IMPACT SITES AND THE BEASLEY RIVER REFERENCE SITES WITH
RESPECT TO THE HARDEY RESOURCE. ................................................................................................................ 6 FIGURE 6. DISSOLVED OXYGEN (%) LEVELS RECORDED IN JANUARY AND MAY 2010. .................................................... 12 FIGURE 7. ELECTRICAL CONDUCTIVITY (µS/CM) RECORDED IN JANUARY AND MAY 2010. ................................................ 13 FIGURE 8. TOTAL NITROGEN (LEFT) AND TOTAL PHOSPHORUS LEVELS (RIGHT) RECORDED IN JANUARY AND MAY 2010. ..... 15 FIGURE 9. CONCENTRATIONS OF COPPER (LEFT) AND ZINC (RIGHT), RECORDED FROM THE STUDY AREA IN JANUARY AND MAY
2010. ........................................................................................................................................................... 16 FIGURE 10. MICROINVERTEBRATE TAXA RICHNESS. .................................................................................................... 19 FIGURE 11. CONSERVATION CATEGORY OF MICROINVERTEBRATE TAXA RECORDED FROM THE BEASLEY RIVER (LEFT) AND
HARDEY RIVER (RIGHT). .................................................................................................................................. 20 FIGURE 12. PROPORTION OF SPECIES FROM EACH HYPORHEIC CLASSIFICATION CATEGORY. ........................................... 21 FIGURE 13. NUMBER OF OCCURRENCES OF TAXA CONSIDERED HYPORHEOS RECORDED FROM EACH RIVER SYSTEM. ......... 21 FIGURE 14. MACROINVERTEBRATE TAXA RICHNESS RECORDED FROM EACH SITE ON EACH SAMPLING OCCASION. ............... 24 FIGURE 15. CONSERVATION CATEGORY OF MACROINVERTEBRATE TAXA RECORDED FROM THE BEASLEY RIVER (LEFT) AND
HARDEY RIVER (RIGHT). .................................................................................................................................. 25 FIGURE 16. PIE-CHARTS SHOWING THE PROPORTION OF MACROINVERTEBRATE TAXA FROM EACH FUNCTIONAL FEEDING
GROUP RECORDED FROM THE HARDEY RIVER (LEFT) AND BEASLEY RIVER (RIGHT). .............................................. 27 FIGURE 17. LENGTH-FREQUENCY PLOTS FOR WESTERN RAINBOWFISH FROM SELECTED SITES ON THE HARDEY AND BEASLEY
RIVERS. ......................................................................................................................................................... 30 FIGURE 18. LENGTH-FREQUENCY PLOT FOR HYRTL’S TANDAN CATFISH COLLECTED FROM BR1 ON THE BEASLEY RIVER.... 31 FIGURE 19. LENGTH-FREQUENCY PLOTS OF SPANGLED PERCH FROM ALL SITES SAMPLED IN JANUARY AND MAY 2010. ..... 32 FIGURE 20. LENGTH-FREQUENCY PLOT FOR FORTESCUE GRUNTER FROM HR5. ............................................................ 33 FIGURE 21. LENGTH-FREQUENCY PLOTS OF BONY BREAM FROM SELECTED SITES. ......................................................... 34 FIGURE 22. LENGTH-FREQUENCY PLOTS FOR FLATHEAD GOBY FROM SELECTED SITES ON THE HARDEY AND BEASLEY
RIVERS. ......................................................................................................................................................... 35 FIGURE 23. LENGTH-FREQUENCY PLOTS FOR BARRED GRUNTER FROM SELECTED SITES ON THE HARDEY AND BEASLEY
RIVERS. ......................................................................................................................................................... 36
PLATES
PLATE 1. USING THE PORTABLE WTW FIELD METERS TO RECORD IN SITU WATER QUALITY SUCH AS PH, EC, DO, AND WATER
TEMPERATURE. ................................................................................................................................................ 7 PLATE 2. USING THE 250 µM MESH NET TO SELECTIVELY SAMPLE THE AQUATIC MACROINVERTEBRATES AT BR2. .............. 10 PLATE 3. THE AUSTRALIAN ENDEMIC CLADOCERA, MOINA CF MICRURA (PHOTO BY RUSS SHIEL) ..................................... 19 PLATE 4. STYGAL AMPHIPOD ?NEDSIA SP., COLLECTED FROM THE HYPORHEIC ZONE AT BR2 ON THE BEASLEY RIVER
(PHOTO BY RUSS SHIEL). ................................................................................................................................ 22 PLATE 5. THE PILBARA TIGER, ICTINOGOMPHUS DOBSONI (PHOTO TAKEN AND PROVIDED BY DR JAN TAYLOR/WA INSECT
STUDY SOCIETY). ........................................................................................................................................... 26 PLATE 6. WESTERN RAINBOWFISH MELANOTAENIA AUSTRALIS (LEFT) AND SPANGLED PERCH LEIOPOTHERAPON UNICOLOR
(RIGHT) (PHOTOS TAKEN AND PROVIDED BY MARK ALLEN ©). .............................................................................. 29 PLATE 7. HYRTL’S TANDAN, NEOSILURIS HYRTLII (PHOTO TAKEN AND PROVIDED BY MARK ALLEN ©). ............................... 29
Hardey Aquatic Surveys: 2010 Wetland Research & Management
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1 INTRODUCTION
1.1 Background
API Management Pty. Ltd. (API) plan to develop the Hardey Resource Area, located
approximately 50 km west north-west of Paraburdoo in the Pilbara region of Western
Australia (see Figure 1). The Hardey Bedded Iron Deposit is a potential extension to API’s
West Pilbara Iron Ore Project (WPIOP) Stage 1 development. The resource covers an area of
approximately 75 hectares and is hosted within the Dales Gorge Member of the Brockman
Iron Formation.
A number of ephemeral drainage lines traverse the Hardey Resource Area. Although no
major creeklines are associated with the Hardey Resource Area, the Hardey River lies
approximately 1.5 km to the south. Current mine plans are not complete, however,
dewatering and/or discharge operations may be necessary. Therefore, API contracted WRM
to undertake an aquatic survey of significant pools in the area to establish baseline
conditions, determine the distribution and conservation status of aquatic fauna which may
be present in or near the Hardey Resource Area, and provide data for a Public
Environmental Review (PER). Given the imminent commencement of this operation,
baseline data were required in the short term. ANZECC/ARMCANZ (2000) recommend at
least three years baseline data are required to establish local trigger levels for assessing
changes in aquatic fauna. At least two years of monthly data are recommended for
developing local trigger values for water quality data. This is usually not logistically possible,
so at least three years biannual data are recommended as a compromise.
1.2 Study objectives
The aims of this project were to collect data which would:
� identify ecological values and conservation significance of the aquatic ecosystems in
the immediate vicinity of the Hardey Resource Area,
� allow future impact assessment, and
� allow monitoring of changes in water quality and aquatic fauna over the life of the
project.
Sampling of aquatic fauna (fish, macroinvertebrates, microinvertebrates, hyporheic fauna)
and water quality were undertaken in the vicinity of the Hardey Resource as well as from
reference (control) sites.
Hardey Aquatic Surveys: 2010 Wetland Research & Management
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Figure 1. Location of the Hardey Resource in the Pilbara Region of W.A., showing the Hardey and Beasley river systems.
Hardey Aquatic Surveys: 2010 Wetland Research & Management
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2 METHODS
2.1 Study area
The Hardey River is a major tributary of the Ashburton River in the Pilbara Region of
Western Australia. It flows in a westerly direction for approximately 217 km from Mount
Tom Price in the Hamersley Range until it meets the Ashburton River near Hardey Junction.
Tributaries of the Hardey River include the Beasley River and Hope Creek. Although much of
the length of the Hardey River is ephemeral, there are permanent pools located in the
vicinity of the Hardey Resource Area. Such permanent pools have high environmental
significance in the Pilbara owing to the fact that they are rare because of the aridity of the
region. Halse et al. (2002) suggested that systems with permanent pools in the Pilbara
provide an important “source of animals for colonisation of newly flooded pools and
maintenance of populations of invertebrate species at the regional level”.
The Beasley River arises in the Hamersley Range north west of Tom Price and flows south-
west for around 105 km into the Hardey River. This river is also mostly ephemeral, although
permanent pools do exist north-west of the Hardey Resource Area.
2.1.1 Climate
The climate of the Pilbara is semi-arid, with relatively dry winters and hot summers. Most
rainfall occurs during the summer months and is associated with cyclonic events; when
flooding frequently occurs along creeks and rivers (Gardiner 2003). Due to the nature of
cyclonic events and thunderstorms, total annual rainfall in the region is highly unpredictable
and individual storms can contribute several hundred millimetres of rain at one time.
Average annual pan evaporation in the Pilbara is ten times greater than rainfall (Stoddart
1997).
Average annual rainfall recorded from gauging stations in the vicinity of the Hardey
Resource range from 356.31 mm at Mt Samson (Station # 505026) to 374.84 mm at Airstrip
(Station # 005059). The length of record differs for these stations, with Mt Samson
extending from 1973 to 1998, and Airstrip from 1989 to current. The Mt Samson gauging
station is located on the Hardey River approx. 18 km west of Tom Price and the Airstrip
station is located approx. 6.5 km upstream of the Mt Samson station. As with other areas in
the Pilbara, most rainfall in the vicinity of the Hardey River falls during the summer,
between January and March (Figure 2). Very little rain falls between July and November
(Figure 2). Over the period of record at Airstrip, total annual rainfall has ranged from 135.20
mm in 2003 to 711.40 mm in 2006 (Figure 2).
Consequently, streamflow is also highly seasonal and variable. Flows occur as a direct
response to rainfall, with peak flows tending to occur within 24 hours of a rainfall event and
continuing for several days. Figure 3 shows the relationship between rainfall and
streamflow for the Mt Samson gauging station on Hardey River, with streamflow volumes
generally being highest following large rainfall events.
Hardey Aquatic Surveys: 2010 Wetland Research & Management
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0
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Hardey River rainfall - airstrip
Figure 2. Rainfall at the Airstrip gauging station on the Hardey River, showing average total monthly rainfall (left) and total annual rainfall (right).
0
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Hardey River Mt Samson Gauging Station
Rainfall Streamflow
Figure 3. Total monthly rainfall (mm) and total monthly streamflow volume (ML) data for the Mt Samson gauging station on the Hardey River.
2.2 Sites and sampling design
The ideal study design would include replicate pools within the area of potential impact
(within the Hardey Resource Area itself and downstream Hardey River), as well as replicate
pools on systems outside the area of potential impact (reference or control sites). However,
the current study was limited by the absence of pools within the Hardey Resource Area
itself, as well as regionally low surface water due to the below-average seasonal rainfall. A
total of five permanent pools were located for sampling, including two potential impact
sites on the Hardey River and three reference sites on the Beasley River (Figure 4 and Table
1). Site photographs are provided in Appendix 1.
Hardey Aquatic Surveys: 2010 Wetland Research & Management
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Table 1. Aquatic sample sites, their GPS location and type (potential impact or reference).
River Site Pool name Type Latitude Longitude
Beasley River
BR1 Reference 22°52’31 S 117°07’05 E
BR2 Reference 22°52’42 S 117°06’30 E
BR3 Woongarra Pool Reference 22°52’55 S 117°06’11 E
Hardey River
HR5 Kazput Pool Potential impact 22°58’32 S 117°11’40 E
HR6 Potential impact 22°58’37 S 117°11’18 E
It was proposed that sampling be conducted in the late dry season (i.e. Jan 2010) and the
late-wet (i.e. April 2010). Dry season sampling is important as it identifies aquatic fauna
utilising permanent pools as vital refuges. In addition, any impacts are likely to be more
severe in the dry season under recessional flows due to a lack of dilution of any possible
contaminants. Sampling in both seasons
increases the ability to collect all species
and allows for seasonal variations in
breeding times of different species.
However, due to the lack of rain, there
wasn’t really a wet season in this area in
2010. Monthly rainfall at the Airstrip
gauging station on the Hardey River was
well below the average during February,
March and April 2010 (Figure 5). There
was no rain in February, and only 15.4
mm and 1.6 mm recorded in March and
April, respectively (Figure 5). Therefore,
post-wet season sampling was much
reduced in 2010. Two sampling rounds
were conducted, the first in January 2010 and the second in May 2010 in order to obtain as
much baseline data as possible and show the system in a naturally stressed condition due to
the low rainfall. This is an important issue to quantify, as natural variability may be greater
than any potential future mine-related effects.
0
20
40
60
80
100
120
February March April
Ra
infa
ll (m
m)
2010 rainfall Average rainfall
Figure 4. Plot showing rainfall in February, March and April of 2010 recorded from the Hardey River airstrip station, compared with average historic rainfall during these months.
Hardey Aquatic Surveys: 2010 Wetland Research & Management
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Figure 5. Location of the Hardey River potential impact sites and the Beasley River reference sites with respect to the Hardey resource.
Hardey Aquatic Surveys: 2010 Wetland Research & Management
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2.3 Water quality
At each site a number of water quality variables were recorded in situ using portable WTW
field meters, including pH, electrical
conductivity (µS/cm), dissolved
oxygen (% and mg/L), and water
temperature (°C) (Plate 1).
Undisturbed water samples were
taken for laboratory analyses of ionic
composition, nutrients and dissolved
metals. Samples collected for
nutrients and metals were filtered
through 0.45 µm Millipore
nitrocellulose filters. All water
samples were kept cool in an esky
while in the field, and frozen as soon
as possible for subsequent transport
to the laboratory. All laboratory
analyses were conducted by the
Natural Resources Chemistry
Laboratory, Chemistry Centre, WA (a
NATA accredited laboratory). Table 2 shows all water quality variables measured.
Water quality data were compared against ANZECC/ARMCANZ (2000) water quality
guidelines. ANZECC/ARMCANZ (2000) provides trigger values for a range of water quality
parameters for the protection of aquatic ecosystems. These trigger values may be adopted
in the absence of adequate site-specific data. ANZECC/ARMCANZ (2000) recommends
different levels of species protection applied to different levels of ecosystem condition. The
99% value is applied to high conservation/ecological value ecosystems, the 95% value to
slightly to moderately disturbed ecosystems and the 90% or 80% values to highly disturbed
ecosystems. In the ANZECC/ARMCANZ (2000) water quality management framework, the
decision about the ecosystem condition is typically a joint one between stakeholders. Based
on the observed condition of rivers in the vicinity of the Hardey Resource, it is suggested
that either the 99% or possibly the 95% values are applied. When applying trigger values
(TVs), ANZECC/ARMCANZ (2000) state the following:
“Trigger values are concentrations that, if exceeded, would indicate a
potential environmental problem, and so ‘trigger’ a management response,
e.g. further investigation and subsequent refinement of the guidelines
according to local conditions.” (Section 2.1.4); and
“Exceedances of the trigger values are an ‘early warning’ mechanism to alert
managers of a potential problem. They are not intended to be an instrument
to assess ‘compliance’ and should not be used in this capacity.” (Section 7.4.4)
Plate 1. Using the portable WTW field meters to record in situ water quality such as pH, Ec, DO, and water temperature.
Hardey Aquatic Surveys: 2010 Wetland Research & Management
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Table 2. All water quality parameters measured.
Parameter Units Parameter Units
pH pH units Aluminium (Al) mg/L
Electrical conductivity µS/cm Arsenic (As) mg/L
Dissolved oxygen % saturation Boron (B) mg/L
Dissolved oxygen mg/L Barium (Ba) mg/L
Water temp °C Cadmium (Cd) mg/L
Cobalt (Co) mg/L
Sodium (Na) mg/L Chromium (Cr) mg/L
Potassium (K) mg/L Copper (Cu) mg/L
Calcium (Ca) mg/L Iron (Fe) mg/L
Magnesium (Mg) mg/L Manganese (Mn) mg/L
Chloride (Cl) mg/L Molybdenum (Mo) mg/L
CO3 mg/L Nickel (Ni) mg/L
HCO3 mg/L Lead (Pb) mg/L
SO4 mg/L Selenium (Se) mg/L
Alkalinity mg/L Uranium (U) mg/L
Hardness mg/L Vanadium (V) mg/L
Nitrate (NO3) mg/L Zinc (Zn) mg/L
Ammonium (NH3) mg/L
Total Nitrogen (total N) mg/L
Total Phosphorus (total P) mg/L
Hence, TVs should not be used in a ‘pass-fail’ approach to water quality management. Their
main purpose is to inform managers and regulators that changes in water quality are
occurring and may need to be investigated. In the case of baseline data collection, the
guidelines may be used to establish background levels relative to TVs, and show where
certain elements may be naturally elevated (i.e. due to geological features). This allows
future discrimination of mine effects from natural enrichment. Where background levels
are elevated, then it is desirable to establish site-specific TVs.
The guidelines recommend, that where an appropriate default TV does not exist, or the
default TV is consistently lower than natural background concentrations, natural
background data should be used to derive the TV. In these instances, the 80th
percentile
(and 20th
percentile in the case of variables that require an upper and lower guidelines, e.g.
pH) of a baseline dataset should be used. This value is then compared to the median value
of the subject water (i.e. the dewatering water) (for further details see Sections 3.3.2.4 and
7.4.4 of ANZECC/ARMCANZ 2000). It is also recommended that TV are based on at least two
years of monthly monitoring data, although it is now acknowledged that this is not always
possible in remote regions, therefore at least three years of biannual data at replicate sites
will provide indicative data.
Hardey Aquatic Surveys: 2010 Wetland Research & Management
9
2.4 Microinvertebrates
Microinvertebrate samples were collected from each site by gentle sweeping over an
approximate 15 m distance with a 53 µm mesh pond net. Care was taken not to disturb the
benthos (bottom sediments). Samples were preserved in 70% ethanol and sent to Dr Russ
Shiel of Adelaide University for processing. Dr Shiel is a world authority on microfauna, with
extensive experience in fauna survey and impact assessment across Australasia.
Microinvertebrate samples were processed by identifying the first 200-300 individuals
encountered in an agitated sample decanted into a 125 mm2 gridded plastic tray, with the
tray then scanned for additional missed taxa also taken to species, and recorded as
‘present’. Specimens were identified to the lowest taxon possible, i.e. species or
morphotypes. Where specific names could not be assigned, vouchers were established.
These vouchers are held by Dr Shiel at Adelaide University, Adelaide, Australia.
2.5 Hyporheic fauna
At each site, hyporheic sampling was conducted by digging a hole approximately 20 cm deep
and 40 cm diameter in alluvial gravels in the dry streambed adjacent to the waters edge.
The hole was allowed to infiltrate with water from the surrounding alluvium, and then the
water column was swept with a modified 53 µm mesh plankton net immediately after the
hole had filled, and again after approx. 30 minutes, after other sampling at the site had been
conducted. Hyporheic sampling was not conducted at Kazput Pool on the Hardey River
(HR5) as the substrate at this site was clay/silt rather than gravel and not conducive to
hyporheic sampling.
Samples were preserved in 70% ethanol and returned to the laboratory for processing. Any
hyporheic fauna present was removed from samples by sorting under a low power
dissecting microscope. Specimens were sent to appropriate taxonomic experts for
identification and confirmation of their status as hyporheic fauna.
Chironomidae (non-biting midges) were sent to Dr Don Edward (The University of Western
Australia), and Copepoda and Ostracoda to Dr Russ Shiel (Adelaide University).
All taxa recorded from hyporheic samples were classified using Boulton’s (2001) categories;
• stygobite – obligate groundwater species, with special adaptations to survive
such conditions
• permanent hyporheos stygophiles - epigean1 species which can occur in both
surface- and groundwaters, but is a permanent inhabitant of the hyporheos
• occasional hyporheos stygophiles – use the hyporheic zone seasonally or during
early life history stages
1 Epigean – living or occurring on or near the surface of the ground.
Hardey Aquatic Surveys: 2010 Wetland Research & Management
10
• stygoxene (species that appear rarely and apparently at random in groundwater
habitats, there by accident or seeking refuge during spates or drought; not
specialised for groundwater habitat).
2.6 Macroinvertebrates
Macroinvertebrate sampling was conducted with a 250 µm mesh FBA pond net to
selectively collect the macroinvertebrate
fauna. As many habitats as possible were
sampled to maximise the number of
species collected, including trailing riparian
vegetation, macrophyte beds, woody
debris, open water column and benthic
sediments. Each sample was then washed
through a 250 µm sieve to remove fine
sediment, leaf litter and other debris (Plate
2). Samples were then preserved in 70%
ethanol.
In the laboratory, macroinvertebrates were
removed from samples by sorting under a
low power dissecting microscope.
Collected specimens were then identified
to the lowest possible level (genus or species level) and enumerated to log10 scale
abundance classes (i.e. 1 = 1 - 10 individuals, 2 = 11 - 100 individuals, 3 = 101-1000
individuals, 4 = >1000). In-house expertise was used to identify invertebrate taxa using
available published keys and through reference to the established voucher collections held
by WRM. External specialist taxonomic expertise was sub-contracted to assist with
Chironomidae (non-biting midges) (Dr Don Edward, The University of Western Australia).
2.7 Fish
Fish fauna were sampled using a variety of methods in order to maximise species richness
and effectively collect as many individuals as possible from each site. Fish sampling
methods included seine nets, gill nets and dip nets.
A beach seine (10 m net, with a 2 m drop and 6 mm mesh) was deployed in shallow areas
where there was little vegetation or large woody debris. Generally, two seines were
conducted at each site to maximise the number of individuals caught.
Gillnetting involved setting 10 m light-weight fine mesh gill nets with a 2 m drop (of varying
stretched mesh net size 13 mm and 19 mm) at each site. Nets were left for the duration of
sampling at that particular site.
Plate 2. Using the 250 µm mesh net to selectively
sample the aquatic macroinvertebrates at BR2.
Hardey Aquatic Surveys: 2010 Wetland Research & Management
11
All fish were identified in the field, measured and then released alive. Fish nomenclature
followed that of Allen et al. (2002). Measuring the fish captured provided information on
the size structure, breeding and recruitment of the fish population.
Hardey Aquatic Surveys: 2010 Wetland Research & Management
12
3 RESULTS AND DISCUSSION
3.1 Water quality
As mentioned previously, water quality data were compared against ANZECC/ARMCANZ
(2000) water quality guidelines. The default trigger values for physical and chemical
stressors applicable to tropical northern Australia are provided in Appendix 2.
3.1.1 Physico-chemistry
Dissolved oxygen (DO)
In January, daytime dissolved oxygen (DO) levels ranged from 37.5% at BR3 to 77.2% at BR1
(Figure 6 and Appendix 3). In May, DO levels ranged from 44.5% at HR5 to 161.7% at BR2
(Figure 6 and Appendix 3). DO values were generally within ANZECC/ARMCANZ (2000)
guidelines, however, a number of
sites recorded DO levels either
above or below guidelines (Appendix
3). Super-saturated daytime DO
levels (<100%) were recorded from a
number of sites in May, including
BR1, BR2 and BR3 (Appendix 3).
These sites all supported dense
macrophyte growth which would be
producing high levels of oxygen
through photosynthesis during the
day (Wilcock and Nagels 2001).
Although ‘high’ DO levels would not
be thought to cause environmental
concern per se, it is likely that sites
with high daytime DO (<120%) may go into oxygen stress at night. These sites likely become
anoxic overnight as respiration by plants, algae and fauna deplete DO (Wilcock and Nagels
2001). Super-saturated DO can also lead to fish bubble disease. One site in particular, BR2
in May 2010, recorded exceptionally high daytime DO levels (161.7%). In most cases, the
‘low’ DO levels (<90%) were unlikely to be low enough to have an ecological impact. DO
concentrations less than ~20% typically represent environmental conditions of ‘stress’ to
resident aquatic fauna, particularly fish with high metabolic demand for oxygen. Whilst no
DO values this low were recorded during the current study, one site recorded particularly
low DO (site BR3 in January 2010, 37.5%).
pH
Most river systems in Western Australia (including those in the Pilbara e.g. Robe, Harding
and lower Fortescue at Millstream) have a natural pH range circum-neutral. In the absence
of baseline data, ANZECC/ARMCANZ (2000) guidelines recommend average pH should be
between 6 and 8 in lowland rivers of tropical northern Australia. The pH values recorded
0
30
60
90
120
150
180
BR1 BR2 BR3 HR5 HR6
Beasley River Hardey River
DO
%
January May ANZECC Upper
Site
ANZECC Lower Point of Ecological Stress
Figure 6. Dissolved oxygen (%) levels recorded in January and May 2010.
Hardey Aquatic Surveys: 2010 Wetland Research & Management
13
during the current study were generally higher than these guidelines and were circum-
neutral to basic. pH ranged from 7.53 (HR5) to 8.89 (HR6) during January 2010, and from
7.66 (HR5) to 8.8 (BR1) in May 2010 (Appendix 3). The circum-neutral to slightly basic pH
characteristic of the sites sampled along the Hardey and Beasley rivers is natural and likely
due to surrounding geology. Although outside of the ANZECC guidelines, it is unlikely that
the slightly basic pH would adversely affect the aquatic biota. Similarly basic pH has
previously been reported from other systems in the East Pilbara (Johnson and Wright 2003,
Streamtec 2004, Jess Delaney, WRM, pers. obs.).
Electrical conductivity (Ec)
Water quality from sites sampled during the current study ranged from fresh through to
brackish, as classified by the DoE (2003)2 (Appendix 3). During January 2010, electrical
conductivity ranged from 1417 µS/cm (HR5) to 1792 µS/cm (HR6), and in May 2010 from
1242 µS/cm (HR5) to 1672 µS/cm (HR6). All conductivity values were above
ANZECC/ARMCANZ
(2000) guidelines for
the protection of
aquatic ecosystems.
There is a general
acceptance that when
conductivity is less
than 1500 µS/cm,
freshwater ecosystems
experience little
ecological stress (Hart
et al. 1991, Horrigan et
al. 2005). With the
exception of HR5, all
sites recorded brackish
Ec in excess of this
value, in either January or May of 2010 (Figure 7). Therefore, it is likely that the aquatic
biota currently supported by these permanent pools are already adapted to the brackish
conditions, and likely comprise the more salt-tolerant remnants after the more sensitive
species have been eliminated. The groups most sensitive to increasing salinity are the
structurally simple, often soft-bodied animals such as hydra, insect larvae and molluscs
(Hart et al. 1991, Nielson et al. 2003). Any future increases in the electrical conductivity of
these waters will likely result in a change in faunal composition.
Ionic composition
2 Fresh defined as < 1500 µS/cm, Brackish = 1500 – 4500 µS/cm, Saline = 4500 – 50,000 µS/cm,
Hypersaline > 50,000 µS/cm (DoE 2003). Classifications were presented as TDS (mg/L) in DoE (2003)
so a conversion factor of 0.68 was used to convert to conductivity µS/cm as recommended by
ANZECC/ARMCANZ (2000).
0
500
1000
1500
2000
2500
BR1 BR2 BR3 HR5 HR6
Beasley River Hardey River
Ele
ctri
cal
con
du
ctiv
ity
(µ
S/
cm)
January May ANZECC trigger Point of Ecological Stress
Figure 7. Electrical conductivity (µS/cm) recorded in January and May 2010.
Hardey Aquatic Surveys: 2010 Wetland Research & Management
14
Alkalinity refers to the capacity of water to neutralise acid and is an expression of buffering
capacity. It essentially relates to the amount of bases3 in water which buffer against sudden
changes in pH (McDonald and Wood 1993, Riethmuller et al. 2001, Lawson 2002). Bases are
able to buffer water by absorbing hydrogen ions when the water is acidic and releasing
them when the water becomes basic (Lawson 2002). Therefore, alkalinity is important for
aquatic fauna as it can protect against rapid pH changes (Riethmuller et al. 2001). Alkalinity
of less than 20 mg/L is considered low; waters would be poorly buffered and the removal of
carbon dioxide during photosynthesis would result in rapidly rising pH (Sawyer and McCarty
1978, Romaire 1985, Lawson 2002). If alkalinity is naturally low (< 20 mg/L) there can be no
greater than a 25% reduction in alkalinity. In the current study, alkalinity was high at all
sites (Appendix 3). Alkalinity ranged from 365 mg/L at BR3 to 520 mg/L at HR6 in January,
and 440 mg/L at BR2 to 560 mg/L at HR6 in May (Appendix 3). This suggests that the
buffering capacity of all sites in the study is high.
The ionic composition of waters is determined by rain-borne salts (i.e. wind-blown dusts)
and geology (e.g. weathering of soils) of the catchment (DeDeckker and Williams 1986).
However, the composition over the warmer months, will be altered by evapo-concentration
and precipitation of less soluble salts, such as calcium carbonate and magnesium sulphate
(Hart and McKelvie 1986). The ionic composition of inland waters in Australia is known to
vary widely, but the proportions of calcium, magnesium and bicarbonate are often enriched
compared to seawater (DeDeckker and Williams 1986).
The composition of major ions at all sites was dominated by sodium and hydrogen
bicarbonate (Na+>Mg
2+>Ca
2+>K
+; HCO3
->Cl
->SO4
2->CO3
-) (Appendix 3). There was no
difference in the dominance of major ions between sampling period or system (Appendix 3).
Nutrients
Nutrient enrichment in aquatic systems can lead to increased algal growth and
cyanobacterial blooms (ANZECC/ARMCANZ 2000), which may become more apparent as
water levels recede, nutrients are evapo-concentrated, and water temperature increases.
Such nuisance blooms can result in adverse impacts to the aquatic ecosystem through toxic
effects, reductions in dissolved oxygen and changes in biodiversity (ANZECC/ARMCANZ
2000). Highly eutrophic waters tend to support high abundances of pollution-tolerant
species, but few rare taxa, and overall, a less complex community structure. During the
current study, all sites recorded elevated levels of total nitrogen and total phosphorus, with
the exception of BR2 (total P in January and May) and HR5 (total P in January) (Figure 8 and
Appendix 3). The levels of nitrogen and phosphorus were variable between sites and
seasons (Figure 8). Total nitrogen levels ranged from 0.22 mg/l at BR2 to 13 mg/l at BR3 in
January, and from 0.2 mg/l at BR2 to 0.69 mg/l at BR3 in May. The high total nitrogen levels
recorded during the current study could perhaps be attributed to pastoral operations in the
area and unrestricted cattle access to the rivers. Cattle were observed in and around most
sites during both sampling occasions.
3 Bases are ions which release hydroxyl ions (OH-) when dissolved in water. Generally these bases
are principally bicarbonate and carbonate ions (Lawson 2002).
Hardey Aquatic Surveys: 2010 Wetland Research & Management
15
During January, total phosphorus ranged from 0.01 mg/l at both BR2 and HR5 to 0.83 mg/l
at BR3. Total phosphorus recorded in May varied between 0.01mg/l at BR2 to 0.04mg/l at
BR3 (Figure 8).
0
0.2
0.4
0.6
0.8
1
BR1 BR2 BR3 HR5 HR6
Beasley River Hardey River
To
tal
nit
rog
en
(m
g/
L)
13 mg/L
0
0.02
0.04
0.06
0.08
0.1
BR1 BR2 BR3 HR5 HR6
Beasley River Hardey River
To
tal
ph
osp
ho
rus
(mg
/L
)
0.83 mg/L
January May ANZECC Trigger
Figure 8. Total nitrogen (left) and total phosphorus levels (right) recorded in January and May 2010.
It should be noted that spot measurements of nutrients are not necessarily indicative of
total nutrient loads.
Metals
Elevated bioavailable metal concentrations are known to adversely impact aquatic biota;
especially populations of metal-sensitive groups such as crustaceans (e.g. Hynes 1960).
Therefore, concentrations of heavy metals were compared to ANZECC/ARMCANZ guidelines
(2000) for the protection of 99% of species. Metal levels were generally low; however,
boron, copper and zinc exceeded ANZECC/ARMCANZ (2000) guidelines for the protection of
99% of species at some sites (Figure 9 and Appendix 3).
Concentrations of boron in excess of the ANZECC/ARMCANZ (2000) 99% trigger values were
recorded from all sites during both sampling events (Appendix 3). All values recorded in
May also exceeded the 95% trigger value. Boron is an essential element for some aquatic
biota, and is used in plants for a variety of metabolic processes, growth, membrane
structure and function, and the maintenance of cell walls (Lovatt 1985, Maier and Knight
1991, Takano et al. 2009), in frogs for early embryonic development (Fort 1998, Fort 1999),
and is required for reproduction in some fish species (Eckhert 1998, Rowe et al. 1998).
Therefore, boron is relatively non-toxic to aquatic systems, and those with moderate
concentrations (1-2 mg/L) are unlikely to experience direct effects (Maier and Knight 1991).
The boron concentrations recorded during the current study were in excess of these
‘moderate’ concentrations. At high levels boron can become toxic, particularly to rooted
macrophytes. In a study examining the toxicity of boron to Myriophyllum alterniflourum,
Nobel et al. (1983) reported that growth was inhibited at 2.0 mg/L (boric acid). Aquatic
macroinvertebrates are considered more tolerant than aquatic macrophytes (Maier and
Knight 1991), while early life stages of fish have been found to be sensitive to high boron
levels.
Hardey Aquatic Surveys: 2010 Wetland Research & Management
16
Elevated concentrations of copper were recorded from BR1, BR3 and HR6 in January, and
HR5 in May (Figure 9 and Appendix 3). Copper can be highly toxic in aquatic environments
and can adversely affect algae, invertebrates, fish, amphibians and water birds (Horne and
Dunson 1995). Acute toxic effects to algae and cyanobacteria include reductions in
photosynthesis and growth, loss of photosynthetic pigments, disruption of potassium
regulation, and mortality. Highly sensitive algae may even be affected by free Cu at low
(parts per billion) concentrations in freshwater. Copper toxicity in amphibians impacts the
juvenile stages (tadpoles and embryos) and includes mortality and sodium loss (Owen 1981,
Horne and Dunson 1995). Copper bioconcentrates in the organs of fish and molluscs (Owen
1981) and birds can experience reduced growth rates, lowered egg production, and
developmental abnormalities. Elevated copper levels have been shown to lead to
reductions in overall macroinvertebrate richness, particularly in sensitive ‘EPT’
(Ephemeroptera, Plecoptera and Trichoptera) taxa (Malmqvist and Hoffsten 1999).
All sites recorded elevated levels of zinc on both sampling occasions (Figure 9 and Appendix
3). Considerably high zinc concentrations were recorded from BR1 and HR6 in May, with
values exceeding the ANZECC/ARMCANZ (2000) guidelines by up to 16 times (Figure 9). At
these concentrations, zinc can become toxic to aquatic organisms, particularly crustaceans
and molluscs.
0
0.001
0.002
0.003
BR1 BR2 BR3 HR5 HR6
Beasley River Hardey River
Co
pp
er
(mg
/L
)
0
0.01
0.02
0.03
0.04
BR1 BR2 BR3 HR5 HR6
Beasley River Hardey River
Zin
c (m
g/
L)
January May ANZECC 99% Trigger
Figure 9. Concentrations of copper (left) and zinc (right), recorded from the study area in January and May 2010.
Given that elevated levels of zinc and copper have previously been recorded from
waterbodies in the East Pilbara region (Streamtec 2004, Jess Delaney, WRM, unpub. dat.),
including sites that are not downstream of mine-sites, the high metal levels recorded during
the current study were considered due to local geology. A number of heavy metals occur
naturally in sediment, including mercury, cadmium, copper and zinc, and the concentration
of such metals can build up over time through natural processes. Generally boron is
freshwater systems in derived from the natural weathering of sediments or sedimentary
rocks or soils. These data provide a good baseline to determine future changes, and to
document current (pre-development) condition of the receiving environment.
Even though elevated, it is unknown what proportion of the measured dissolved metals was
labile (bio-available) or unavailable through complexing (i.e. with dissolved organic carbon;
e.g. tannin). The bioavailability of trace metals is affected by a number of factors including,
water hardness (Stephenson and Mackie 1989), alkalinity, salinity (Jackson et al. 2000), pH
Hardey Aquatic Surveys: 2010 Wetland Research & Management
17
(Jackson et al. 2000) as well as what chemical form the metal is in (Sander et al. 2007). Zinc
is an essential micronutrient, whereas cadmium is extremely toxic, but when they occur in
the same environment there is potential for the two metals to compete for the same
biological binding sites. In a study of the complexation of Cd and Zn in alpine lakes in New
Zealand, Sander et al. (2007) found that despite cadmium being recorded in much lower
total concentrations than copper and zinc, it exhibited the highest toxicity for aquatic
organisms.
ANZECC/ARMCANZ (2000) recommends the use of techniques such as DGTs (Diffuse
Gradients in Thin Films; see Box 1) as a speciation measurement to provide a better
estimate of the bio-available metal concentration if the dissolved metal concentrations
exceed the guideline trigger values. It is possible that the current complexing capacity of the
receiving water renders the observed levels of dissolved metals non-labile (i.e. non-
bioavailable). However, a small increase in concentration of a particular dissolved metal
may exceed the complexing capacity of the waters, resulting in labile concentrations, and
toxicity to biota. Therefore, even though background concentrations may be elevated, they
may not be toxic, but small additional increases due to development could result in toxicity.
Box 1. Diffuse Gradients in Thin Films (DGTs).
The DGT technique was first developed in 1994 as a time averaged, in situ speciation measurement
of heavy metals in waters. Since its introduction it has been validated in the field for the
determination of metals in fresh and seawater, and more recently in estuarine waters. The DGT
technique is based on a simple device, which accumulates metal ions in a well-defined manner from
solution. Soluble species diffuse through a diffusive layer of known thickness in which a
concentration gradient is maintained. Behind the diffusive layer is a binding layer in which reactive
metal species are bound. The mass of accumulated metal is measured following retrieval and is
used to calculate the average concentration of DGT labile metal species in the bulk solution over the
deployment time. As the device does not accumulate the major ions that cause interference with
the measurement, the measurement does not suffer the degree of interference associated with the
direct analysis of waters.
Hardey Aquatic Surveys: 2010 Wetland Research & Management
18
3.2 Microinvertebrates
3.2.1 Taxonomic composition and species richness
The microinvertebrate fauna recorded during the current study was highly diverse. A total
of 103 taxa were recorded from the five sites sampled on two occasions, with 75 taxa being
recorded in January, and 67 taxa in May 2010 (Table 3 and Appendix 4). A considerably
greater number of microinvertebrate taxa were collected from Beasley River sites (a total of
90 taxa) compared with Hardey River sites (51 taxa); although this may in part be due to the
additional site sampled on the Beasley River (three sites compared to two on the Hardey
River) (see Table 4 and Appendix 4). The microinvertebrate fauna comprised Protista
(Ciliophora & Rhizopoda), Rotifera (Bdelloidea & Monogonata), Cladocera (water fleas),
Copepoda (Cyclopoida) and Ostracoda (seed shrimp). In comparison to other pools in the
Pilbara sampled by the DEC, the Hardey and Beasley sites were more speciose, and
appeared to be richer in testates and rotifers, but comparable or slightly less speciose in
microcrustaceans (Dr Russ Shiel, University of Adelaide, pers. comm.).
The microinvertebrate fauna was typical of tropical systems reported elsewhere (e.g. Koste
and Shiel 1983, Tait et al. 1984, Smirnov and De Meester 1996, Segers et al. 2004). For
example, a greater number of Lecanidae taxa (15 taxa) were recorded than Brachionidae
taxa (8 taxa) within the Rotifera (Appendix 4). Brachionidae tend to dominate temperate
rotifer plankton, but is overshadowed by Lecanidae in tropical waters, as was the case here.
Within the Cladocera fauna, daphniids tend to predominate in temperate waters, with low
representation in the tropics. Only two daphniids were recorded during the current study
(Appendix 4). In tropical systems throughout the world, daphniids tend to be replaced by
sidids, moinids, and in the case of heavily vegetated or shallow waters, by chydorids, as seen
here (see Appendix 4).
Table 3. Composition of microinvertebrate fauna recorded from the study area in January and May 2010.
Microinvertebrate division Common name No. of taxa
Jan May
Protista Protists 13 15
Rotifera Rotifers 42 38
Cladocera Water fleas 10 5
Copepoda Copepods 7 6
Ostracoda Seed shrimp 3 3
Total number of taxa 75 67
Table 4. Composition of microinvertebrate fauna recorded from the Hardey River and Beasley River during the current study.
Microinvertebrate division Common name No. of taxa
Hardey Beasley
Protista Protists 12 19
Rotifera Rotifers 24 54
Cladocera Water fleas 5 8
Copepoda Copepods 7 7
Ostracoda Seed shrimp 3 2
Total number of taxa 51 90
Hardey Aquatic Surveys: 2010 Wetland Research & Management
19
Microinvertebrate taxa richness varied considerably between river and sampling occasion
(Figure 10). During
January 2010, the
greatest number of
microinvertebrate taxa
was recorded from BR3
(39 taxa), and the least
from HR6 (10 taxa). Due
to inadequate
preservation, however,
the sample taken from
HR6 in January had
deteriorated in quality,
with loss of some taxa.
This likely resulted in the
apparently lower taxa
from HR6 in January. During May 2010, the greatest number of taxa was recorded from
BR1, BR2 and HR5 (all recorded 33 taxa). Again, the least number of micro-invertebrate taxa
was recorded from HR6 (10 taxa). Generally, most sites recorded more microinvertebrate
taxa in May, with the exception of BR3 (Figure 10).
3.2.2 Conservation significance of microinvertebrates
The majority of microinvertebrate taxa recorded are common, ubiquitous species. Of the 51
microinvertebrate taxa collected from the Hardey
River, 39% were cosmopolitan, occurring widely
throughout the world, 2% were Australasian, and 2%
had a pan-tropical distribution (Figure 11). Over 50%
of taxa were indeterminate due to insufficient
information/taxonomy. One species, however, was
endemic to Australia. This was the Cladocera Moina
cf. micrura (Plate 3); recorded from HR5 in January.
Moina micrura has a cosmopolitan distribution, but
genetic studies of the Australian species separate it
from the common cosmopolitan species. Therefore,
this species was identified as Moina cf. micrura, and
was classified as an Australian endemic. This species
is known from across Australia, with a greater
number of records in the eastern states due to the
higher sampling intensity of microinvertebrate fauna
there.
During the current study, 90 taxa of
microinvertebrates were recorded from the Beasley
River. Of these, 50% had a cosmopolitan distribution and are known to occur widely
throughout the world, 3.5% had a pan-tropical distribution, and 3.5% were Australasian
0
10
20
30
40
BR1 BR2 BR3 HR5 HR6
Beasley River Hardey River
Mic
roin
vert
eb
rate
ta
xa r
ich
ne
ss
January May
Figure 10. Microinvertebrate taxa richness.
Plate 3. The Australian endemic cladocera, Moina cf micrura (photo by Russ Shiel)
Hardey Aquatic Surveys: 2010 Wetland Research & Management
20
(Figure 11). Of interest, however, was the collection of one species which is only known
from the Australian continent. This was the Cladocera Alona cf. rigidicaudis. This species
was collected from BR3 in January. Like the Moina endemic species, A. cf. rigidicaudis has
been collected across Australia, with a greater number of records from the eastern states.
Other microinvertebrate taxa of interest included one species which is rarely recorded
within Australia, the Rotifera Asplanchnopus hyalinus, and another which is cosmopolitan
but rare, the Rotifera Trichocerca cf. agnatha. The former species was recorded from BR2 in
January, and the latter from BR1 in May (Appendix 4).
BEASLEY RIVER
HARDEY RIVER
Australasian Australian endemic Cosmopolitan Pantropical Indeterminate
Figure 11. Conservation category of microinvertebrate taxa recorded from the Beasley River (left) and Hardey River (right).
Hardey Aquatic Surveys: 2010 Wetland Research & Management
21
3.3 Hyporheic fauna
3.3.1 Taxonomic composition and species richness
A total of 33 taxa were recorded from hyporheic samples collected during the current study
(Appendix 5). Of these taxa, the vast majority were
classified as stygoxene (67%) and do not have
specialised adaptations for groundwater habitats.
However, 15% of the taxa were classified as
occasional hyporheos stygophiles, 3% were
stygobites4, and 6% were possible hyporheic taxa
(Figure 12). No permanent hyporehic stygophiles
were recorded. Around 9% of taxa collected from
hyporheic samples were unknown due to insufficient
taxonomy and/or information (Figure 12).
Classifications followed those by Boulton (2001),
however, this type of analysis should be treated with
some caution as results are likely affected by
available information on life history, taxonomic
resolution, and interpretation of classification
categories.
The results from this study are similar to those
reported previously in the Pilbara (Halse et al. 2002,
Jess Delaney, WRM, pers. obs), in that <20% of taxa collected in hyporheic habitats were
entirely dependent on groundwater for their persistence as a species. Halse et al. (2002)
suggested that it is not surprising that the hyporheos is dominated by species with some
affinity for surface water, because the
hyporheos is an “ecotone between
productive, species-rich surface water
systems and nutrient-poor groundwater
systems with lower number of species per
sampling unit”.
Hyporheos fauna (including those classified
as possible hyporheic species) were recorded
from both river systems (Figure 13). A
greater number of occurrences of hyporheos
taxa were recorded from the Beasley River,
although this may be a reflection of the
greater sampling effort in this system (three
sites successfully sampled for hyporheos in the Beasley River compared with one site on the
Hardey River).
4 A stygobite is an aquatic animal that is restricted to groundwater and/or hyporheic environments
(i.e. stygofauna). They have adaptations to survive such conditions, including elongated appendages
and antennas, no eyes, and a lack of pigmentation.
Stygoxene Occasional stygophile
Stygobite Possible hyporheic
Unknown
Figure 12. Proportion of species from each hyporheic classification category.
0
2
4
6
8
10
Beasley River Hardey River
No
. o
f o
ccu
rre
nce
s o
f
hy
po
rhe
os
fau
na
Figure 13. Number of occurrences of taxa considered hyporheos recorded from each river system.
Hardey Aquatic Surveys: 2010 Wetland Research & Management
22
3.3.2 Hyporheos taxa
Species considered to be restricted to the hyporheos included the stygobitic amphipod
?Nedsia sp.; occasional stygophiles Mesocyclops cf. darwini (copepod), Microcyclops
varicans (copepod), Candonopsis tenuis (ostracod), Elmid beetle larvae Austrolimnius sp.,
and Hydraenid beetle Hydraena sp.; and, the possible hyporheos species Oligochaeta spp.
and dytiscid beetle Limbodessus sp.
The stygobitic amphipod collected from the Beasley River was identified as a Melitid, likely
to be a species of Nedsia (Plate 4). As is common with many groundwater animals (Strayer
1994), this species is likely a short range endemic. The ?Nedsia sp. amphipod was collected
from the hyporheic sample of BR2 during May 2010 (Appendix 5).
Plate 4. Stygal amphipod ?Nedsia sp., collected from the hyporheic zone at BR2 on the Beasley River (photo by Russ Shiel).
Both the copepod species collected from hyporheic samples were considered occasional
stygophiles. Mesocyclops cf. darwini have been recorded from surface waters, springs and
wells throughout the Pilbara (Holyńska and Brown 2002, Halse et al. 2002, DEC 2009). This
species was recorded from BR3 during the current study (Appendix 5). Microcyclops
varicans have also been collected from surface waters and groundwater (bores and
hyporheic environments) throughout the Pilbara (Martens and Rossetti 2002, Pesce et al.
1996, Halse et al. 2002, DEC 2009). During the current study, M. varicans was collected
from both the Beasley (BR2 and BR3) and Hardey rivers (HR6) (Appendix 5). Given that
Elmidae larvae Austrolimnius sp. and species of Hydraena have been commonly reported
from hyporheic habitats throughout the world (Boulton et al. 1997, del Rosario and Resh
2000, Olsen and Townsend 2003, Belaidi et al. 2004, Storey and Williams 2004), they were
classified as occasional stygophiles in the current study. Austrolimnius sp. larvae were
recorded from BR2, and Hydraena sp. from HR6 (Appendix 5). One other species was
classified as an occasional hyporheic stygophile, the ostracod Candonopsis tenuis. This
species is known from surface waters (Sommer et al. 2008, DEC 2009), bores (Karanovic and
Marmonier 2002), wells (Reeves et al. 2007, Schmidt et al. 2007), and springs (Halse et al.
2002) across the Pilbara. During the current study it was collected from the Beasley River
(BR1 and BR2).
Hardey Aquatic Surveys: 2010 Wetland Research & Management
23
3.4 Macroinvertebrates
3.4.1 Taxonomic composition and species richness
A total of 92 macroinvertebrate taxa were recorded from the five sites sampled in January
and May 2010 (Table 5 & Appendix 6). Of these, 58 were recorded in January and 71 were
recorded in May (Table 5 & Appendix 6). Similar to the microinvertebrate fauna, a greater
number of macroinvertebrate taxa were recorded from the Beasley River (80 taxa) than the
Hardey River (62 taxa) (Table 6). Again, this may be due, at least in part, to the additional
site sampled on the Beasley River. The macroinvertebrate fauna comprised Turbellaria (flat
worms), Cnidaria (freshwater hydra), Mollusca (snails and freshwater mussels), Oligochaeta
(aquatic segmented worms), Crustacea (side swimmers), Acarina (water mites),
Ephemeroptera (mayflies), Odonata (dragonflies and damselflies), Hemiptera (aquatic true
bugs), Coleoptera (aquatic beetles), Diptera (fly larvae), Trichoptera (caddisflies) and
Lepidoptera (moth larvae). This list also includes groups which could not be identified to
species level due to lack of suitable taxonomic keys (i.e. Diptera families, some families of
Coleoptera, etc), and some groups were not considered as macroinvertebrates and so not
taken further (i.e. micro-crustacea). Therefore, the total macroinvertebrate species richness
for these sites is likely greater.
Table 5. Composition of macroinvertebrates recorded from the study area in January and May 2010.
Macroinvertebrates No. of taxa
January May
Turbellaria (flat worms) 0 1+
Cnidaria (freshwater hydra) 1+ 1+
Mollusca (snails & bivalves) 3 3
Oligochaeta (aquatic worms) 1+ 1+
Crustacea (side swimmers) 1 0
Acarina (water mites) 1+ 2
Ephemeroptera (mayflies) 1 2
Odonata (dragonflies & damselflies) 8 9
Hemiptera (true bugs) 7 11
Coleoptera (aquatic beetles) 12 14
Diptera (two-winged flies) 20 26
Trichoptera (caddis-flies) 2 1
Lepidoptera (moths) 1 0
Total number of taxa 58 71
The taxonomic listing includes records of larval and pupal stages for groups such as Diptera
and Coleoptera. Current taxonomy is not sufficiently developed to allow identification of
larval and pupal stages of all members of these groups to species level. In many instances, it
is likely that these stages are the same species as the larval/adult stages recorded from the
same location. However, because this could not be definitively determined, they were
treated as separate taxa. In any case, different life stages often have different functional
roles in the ecosystem and therefore it is acceptable to treat them as separate taxa.
Hardey Aquatic Surveys: 2010 Wetland Research & Management
24
Table 6. Composition of macroinvertebrates recorded from the Hardey and Beasley rivers during the current study.
Macroinvertebrates No. of taxa
Hardey Beasley
Turbellaria (flat worms) 1+ 1+
Cnidaria (freshwater hydra) 1+ 1+
Mollusca (snails & bivalves) 2 3
Oligochaeta (aquatic worms) 1+ 1+
Crustacea (side swimmers) 1 0
Acarina (water mites) 2+ 2+
Ephemeroptera (mayflies) 1 2
Odonata (dragonflies & damselflies) 10 11
Hemiptera (true bugs) 8 13
Coleoptera (aquatic beetles) 12 15
Diptera (two-winged flies) 21 28
Trichoptera (caddis-flies) 2 2
Lepidoptera (moths) 0 1
Total number of taxa 62 80
The composition of macroinvertebrate taxa was typical of freshwater systems throughout
the world (Hynes 1970), and was dominated by Insecta (90% of taxa). Of the insects, the
majority were Diptera (36% of Insecta), closely followed by Coleoptera (25% of Insecta).
Molluscs only comprised 3% of the total fauna.
Of the 92 taxa, three were common and occurred in all samples (see Appendix 6). These
were Hydracarina spp., the dytiscid Necterosoma regulare and the ceratopogonid
Dasyheleinae. In contrast, a total of 34 taxa were uncommon and only recorded once (i.e.
from one sample; Appendix 6).
Macroinvertebrate taxa
richness varied between
site and sampling period
(Figure 14). In January,
the number of
macroinvertebrate taxa
recorded ranged from
22 at BR2 to 33 at both
BR1 and HR5 (Figure 14
and Appendix 6). In
May, the greatest
number of taxa was
recorded from BR3 (39
taxa), and the least from
HR6 (30 taxa; Figure 14).
Three of the five sites
recorded more
macroinvertebrate taxa in May than January (Figure 14).
0
10
20
30
40
BR1 BR2 BR3 HR5 HR6
Beasley River Hardey River
Ma
cro
inv
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eb
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ta
xa
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ess
January May
Figure 14. Macroinvertebrate taxa richness recorded from each site on each sampling occasion.
Hardey Aquatic Surveys: 2010 Wetland Research & Management
25
3.4.2 Conservation significance of macroinvertebrates
The majority of macroinvertebrate taxa recorded were common, ubiquitous species. Of the
80 macroinvertebrate taxa recorded from the Beasley River, 15% were Cosmopolitan,
occurring widely across the world, and 34% were Australasian with a distribution extending
across Australia, New Guinea and neighbouring islands, including those of Indonesia (Figure
15). Almost half (48%) were indeterminate due to insufficient taxonomy/information.
Species with restricted distributions were recorded in lower proportions; 2% were Northern
Australian species, and 1% was endemic to the Pilbara (Figure 15). Of the 62 taxa recorded
from the Hardey River, 45% were Indeterminate, 37% were Australasian, and 8% were
Cosmopolitan. A number of taxa were also recorded which had restricted distributions; 5%
were Northern Australian and 5% were Pilbara Endemic species (Figure 15).
BEASLEY RIVER
HARDEY RIVER
Australasian Indeterminate Cosmopolitan Northern Australian Pilbara Endemic
Figure 15. Conservation category of macroinvertebrate taxa recorded from the Beasley River (left) and Hardey River (right).
Of interest was the collection of species known only from the Pilbara region of Western
Australia, including the stygal amphipod ?Nedsia sp., beetle Tiporus tambreyi and the
dragonfly Ictinogomphus dobsoni. Only one Pilbara endemic species was recorded from the
Beasley River, while all three endemic species were found in the Hardey River.
The amphipod collected from the Hardey River HR6 in January was of stygal origin and
identified as a species of Nedsia (Family: Melitidae). Without DNA analysis it is not possible
to determine if it is the same species as that collected from the hyporheic zone at site BR2.
Given that stygal amphipods tend to be short range endemics, it was classified amongst the
macroinvertebrate fauna as a Pilbara endemic.
Although endemic to the Pilbara, Tiporus tambreyi appears to be commonly recorded and
widespread throughout its range. It is previously known from the Millstream area (ANIC
Database), Palm Pool in Millstream National Park (DEC 2009), Dales Gorge in Karijini
National Park (DEC 2009), the Upper Fortescue River, Weeli Wolli Creek, Coondiner Creek,
Kalgan Creek, and Bobswim Pool in Karijini NP (Jess Delaney, WRM, unpub. dat.). During the
current study this species was collected from BR1, BR2, BR3 and HR6 (Appendix 6). The
beetle Tiporus tambreyi is most abundant in the littoral zone at the edge of ponds, lakes,
Hardey Aquatic Surveys: 2010 Wetland Research & Management
26
billabongs and pools in intermittent streams. This wide range of habitats includes numerous
types of substrata, such as rock, pebbles,
gravel, sand, mud, silt, peat and other
organic debris.
The Pilbara Tiger dragonfly,
Ictinogomphus dobsoni (Plate 5), occurs
in permanent still or sluggish waters
(Watson 1991). This species is known
only from a few localities in the Pilbara
region of north-west Western Australia
(Watson 1991). It has been collected
previously from Gregory Gorge (ANIC
Database), Fortescue River on Millstream
Station (ANIC Database), Bobswim Pool,
Dales Gorge (DEC 2009), Fortescue Falls
in Karijini National Park (Adrian Pinder,
DEC, pers. comm.), and Weeli Wolli Creek
(Jess Delaney, WRM, unpub. dat.).
During the current study, I. dobsoni was
recorded from HR5.
3.4.3 Functional feeding groups
It is generally considered that the functional complexity and ‘health’ of an aquatic
ecosystem is reflected by the diversity of functional feeding groups5 present (groups that
reflect the obligate feeding mode of each species) (Cummins et al. 1995). As a result,
aquatic macroinvertebrates are often classified into functional feeding groups, which reflect
the mode of feeding by individual species. These groups include shredders, predators,
filterers, grazers and collectors. The functional composition (i.e. the proportions of these
groups) may be used to infer ecological health, whereby an ecologically healthy system has
a mix of the different groups present. Covich et al. (1999) suggested that if each functional
group is present in a system, ecological processes and energy flow are maintained.
All functional feeding groups were represented in both systems (Figure 16). Predators were
the dominant taxa from both the Hardey and Beasley rivers, followed by collectors (Figure
16). There were a high proportion of unknowns, reflecting a general lack of knowledge on
the biology of Pilbara aquatic macroinvertebrates.
5 Functional feeding groups: ‘shredders’ feed on coarse particulate matter (CPOM >1mm);
‘collector’s feed on fine particulate matter (FPOM < 1mm); ‘filterers’ filter suspended particles from
the water column and are often viewed as a subset of collectors; ‘grazers’ are those animals that
graze or scrape algae and diatoms attached to the substrate; ‘predators’ capture live prey.
Plate 5. The Pilbara Tiger, Ictinogomphus dobsoni (photo taken and provided by Dr Jan Taylor/WA Insect Study Society).
Hardey Aquatic Surveys: 2010 Wetland Research & Management
27
HARDEY RIVER
BEASLEY RIVER
Collectors/gatherers Shredders
Grazers/scrapers Predators
Filterers
Other/unknown
Figure 16. Pie-charts showing the proportion of macroinvertebrate taxa from each functional feeding group recorded from the Hardey River (left) and Beasley River (right).
Hardey Aquatic Surveys: 2010 Wetland Research & Management
28
3.5 Fish
3.5.1 Species richness
The fish fauna of the Pilbara is characterised by low species diversity yet high levels of
endemicity; over 42% of species recorded from the Pilbara are restricted to the region
(Unmack 2001, Allen et al. 2002). Masini (1988) found the relatively clear waters of
permanent and semi-permanent waterbodies supported the best developed fish
assemblages in the region. In a study of the biogeography of Australian fish fauna, Unmack
(2001) recognised ten distinct freshwater fish biogeographic provinces, of which the Pilbara
Province was one. This region was considered distinct because its fauna did not cluster with
other drainages in multivariate (parsimony and UPGMA) analysis of fish distribution
patterns (Unmack 2001).
Allen et al. (2002) suggested the sparse freshwater fish fauna of the Pilbara was due to its
aridity. The fish which inhabit the region are adapted to the extreme conditions and many
have strategies for surviving drought (Unmack 2001). For example, Australia’s most
widespread native fish, the spangled perch (Leiopotherapon unicolor), is thought to survive
drought by aestivating in wet mud or under moist litter in ephemeral waterbodies (Allen et
al. 2002). Although conclusive evidence is still required to validate this hypothesis,
anecdotal evidence does exist. This species is often found in large numbers shortly after
rain in locations which were previously dry and have no connection to permanent water.
Spangled perch can migrate in very shallow waters, and can be found in any temporary
water of the Pilbara following rainfall, including wheel ruts of vehicle tracks (Allen et al.
2002). They are known to tolerate extremes in the aquatic environment (Llewellyn 1973,
Beumer 1979, Glover 1982) and occupy a wide range of habitats (Bishop et al. 2001, Allen et
al. 2002). Spangled perch and western rainbowfish are the only species known from an area
in the Pilbara with little or no surface run-off in the Great Sandy Desert (Morgan and Gill
2004).
Seven of the twelve freshwater fish species known from the Pilbara were recorded during
the current study (Table 7). These were the western rainbowfish Melanotaenia australis
(Plate 7), spangled perch Leiopotherapon unicolor (Plate 7), Hyrtl’s tandan (eel-tailed catfish)
Neosiluris hyrtlii (Plate 7), Fortescue grunter Leiopotherapon aheneus, bony bream
Nematalosa erebi, flathead goby Glossogobius giurus and barred grunter Amniataba
percoides. Spangled perch and western rainbowfish were the most common species
recorded, and were found at all sites, while Hyrtl’s tandan was only recorded from BR1 and
HR5 (Table 7). The greatest number of fish species was recorded from BR1 and HR5 (seven
species; Table 7). All other sites recorded six species (Table 7).
3.5.2 Conservation significance of fish fauna
Generally, the fish recorded are common widespread species. However, the Fortescue
grunter, Leiopotherapon aheneus, has a restricted distribution within the Pilbara Region of
Western Australia. It is only known from the Fortescue, Robe and Ashburton river systems
(Allen et al. 2002), but is considered reasonably common within its range. This species is
currently listed as ‘Lower Risk Near Threatened’ on the IUCN Redlist of Threatened Species
Hardey Aquatic Surveys: 2010 Wetland Research & Management
29
(IUCN 2009) and as a Priority 4 Species on the DEC Priority Fauna List (DEC 2010). Priority 4
species are those in need of monitoring (DEC 2010). This species was recorded from all sites
on both the Hardey and Beasley rivers (Table 7).
Table 7. List of fish species recorded from each site. � indicates presence in January, * indicates presence in May 2010.
Beasley River Hardey River
BR1 BR2 BR3 HR5 HR6
Bony bream Nematalosa erebi � * � � � * �
Fortescue grunter Leiopotherapon aheneus � * � � � * � *
Spangled perch Leiopotherapon unicolor � * � * � * � * � *
Barred grunter Amniataba percoides � * � * � � * � *
Western rainbowfish Melanotaenia australis � * � * * � � *
Flathead goby Glossogobius giurus � * � * � � � *
Hyrtl’s tandan Neosiluris hyrtlii � �
Species richness 7 6 6 7 6
Plate 6. Western rainbowfish Melanotaenia australis (left) and spangled perch Leiopotherapon unicolor (right) (photos taken and provided by Mark Allen ©).
Plate 7. Hyrtl’s tandan, Neosiluris hyrtlii (photo taken and provided by Mark Allen ©).
3.5.3 Length Frequency Analysis
Breeding characteristics of fish species in the Pilbara, such as fecundity and the size at first
maturity, vary between river systems and rainfall zone. Beesley (2006) found life history
Hardey Aquatic Surveys: 2010 Wetland Research & Management
30
strategies of fish species in the Fortescue River lay between ‘opportunistic’ and ‘periodic’,
reflecting the seasonal yet unpredictable nature of rainfall in the region.
Western rainbowfish
Breeding in western rainbowfish (Melanotaenia australis) occurs throughout the year, with
multiple spawning bouts which take full advantage of the regions intermittent rainfall and
streamflow (Beesley 2006). Morgan et al. (2002) captured small juveniles on most sampling
occasions in the Fitzroy River. The size at first maturity varies between river systems, but
western rainbowfish generally attain a maximum size of 110 mm total length (TL) (Morgan
et al. 2002).
The length-frequency plots of western rainbowfish from most sites show a range of size-
classes, including new recruits (<30 mm), juveniles, sub-adults and adults (Figure 17). This
suggests good recruitment and some degree of population stability, with juveniles and
adults through all size classes present in the population. No western rainbowfish were
recorded from HR5 in May (Figure 17).
Hyrtl’s tandan (catfish)
Very little is known of the breeding ecology of Hyrtl’s tandan (Neosiluris hyrtlii). It is thought
that individuals may mature in their first year at a size of approximately 135 mm TL for both
sexes (Lake 1971, Bishop et al. 2001). Species of Neosilurus catfish usually attain a
maximum size of only 200 mm however, N. hyrtlii, along with N. ater, can reach up to 400
0
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HR6
Jan May
Figure 17. Length-frequency plots for western rainbowfish from selected sites on the Hardey and Beasley rivers.
Hardey Aquatic Surveys: 2010 Wetland Research & Management
31
mm TL (Lake 1971, Bishop et al. 2001). Breeding is thought to occur in the early wet season
(Morgan et al. 2002, Bishop et al. 2001), when initial flooding increases the area and
diversity of aquatic habitat available, while also initiating increases in plankton and other
foods (Bishop et al. 2001).
Very low numbers of Hyrtl’s tandan were recorded, with the species only being caught at
two sites, BR1 and HR5 (Table 7). Only one individual of approximately sub-adult size (99
mm) was recorded from the Hardey River at HR5. Five individuals were collected from BR1
which would be considered juveniles and sub-adults (Figure 18). The low number of Hyrtl’s
tandan catfish collected may be a reflection of sampling difficulty, as this species is a
bottom-dweller and would have plenty of places to hide from gill and seine nets in the
dense macrophyte growth characteristic of the Hardey and Beasley river sites. Due to the
elevated conductivity of the waters it was not possible to electrofish, however,
electrofishing in other Pilbara rivers routinely catches Hyrtyl’s catfish, when seine and gill
netting does not. Therefore, it is likely this species is more common than it appears in the
Hardey/Beasley system.
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Jan May
Figure 18. Length-frequency plot for Hyrtl’s tandan catfish collected from BR1 on the Beasley River.
Spangled perch
Breeding in spangled perch (Leiopotherapon unicolor) of the Pilbara occurs during the
summer wet season, between late November and March (Beesley 2006, Morgan et al.
2002). During this time, multiple spawning events are known to occur (Beesley 2006). In
the Fitzroy River, Morgan et al. (2002) collected mature specimens in summer and larvae at
the end of the wet season, indicating that spawning coincided with the flooding of the river.
Spangled perch mature in their first year at approx. 58 mm TL for males and 78 mm TL for
females. They reach a maximum size of 300 mm TL.
Juvenile spangled perch (<50 mm) were recorded from all sites in January, but none in May
(Figure 19). No large adults (>160 mm) were collected, however sexually mature individuals
(>70 mm) were evident at all sites. All sites recorded higher numbers of spangled perch in
January than in May (Figure 19).
Hardey Aquatic Surveys: 2010 Wetland Research & Management
32
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Jan May
Figure 19. Length-frequency plots of spangled perch from all sites sampled in January and May 2010.
Fortescue Grunter
Little is known about the biology of the Fortescue grunter, Leiopotherapon aheneus. Few
specimens were recorded from each site during the current study, with the exception of
HR5 on the Hardey River, which in January had very high numbers representing all size
classes between 41 mm and 100 mm (Figure 20). It is likely that these size classes cover the
range from juvenile to adult, suggesting good recruitment at this site.
Hardey Aquatic Surveys: 2010 Wetland Research & Management
33
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Jan May
Figure 20. Length-frequency plot for Fortescue grunter from HR5.
Bony bream
Breeding in bony bream (Nematalosa erebi) is independent of flooding. Reaching sexual
maturity at about 144 mm for males and 180 mm for females; they mature in their second
or third year (Puckridge and Walker 1990). In the Murray River, spawning is known to occur
over summer when water temperatures are 21-23 °C (Puckridge and Walker 1990).
Commonly 150 – 200 mm in length, bony bream can reach a maximum of 300 mm TL (Allen
et al 2002).
Bony bream were recorded at a range of size classes from sites BR1, BR2 and HR6 (Figure
21). Sexually mature individuals (>~130 mm SL) were recorded from all three sites (Figure
21). Juveniles and sub-adults were recorded in low numbers, with the majority being in the
larger size classes > 100 mm (Figure 21). Bony bream were not recorded in May from BR2
or HR6, but were taken from BR1 (Figure 21).
Flathead goby
The flathead goby (Glossogobius giurus) is found throughout northern Australia from the
Ashburton River (WA), to the Burdekin River in north Queensland (Merrick and Schmida
1984, Allen et al. 2002, Morgan et al. 2002). They are also found throughout the Indo-West
Pacific (Allen et al. 2002). Although this species is thought to have a marine larval stage
(Allen 1989, Herbert and Peeters 1995, Allen et al. 2002), Morgan et al. (2002) captured
larvae, juveniles and adults in the freshwaters of the Fitzroy River, suggesting they do breed
in freshwater. Similarly, juveniles have been collected from creeks above the Ord River dam
(AW Storey, unpub. dat.), which is a major barrier to fish passage. Little could be found on
the breeding biology of this species, but the maximum size is thought to be at least 200 mm
TL.
During the current study, flathead gobies were recorded from all sites during both sampling
periods (Table 7). Sites for which sufficient individuals were collected for length-frequency
analysis included BR1, BR2 and HR6 (Figure 22). A variety of size classes were found at BR1,
BR2 and HR6, ranging between 21 mm and 70 mm (Figure 22).
Hardey Aquatic Surveys: 2010 Wetland Research & Management
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Figure 21. Length-frequency plots of bony bream from selected sites.
Hardey Aquatic Surveys: 2010 Wetland Research & Management
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10
0-1
0
11
-20
21
-30
31
-40
41
-50
51
-60
61
-70
71
-80
81
-90
91
-10
0
Fre
qu
en
cy
Length (mm)
HR6
Jan May
Figure 22. Length-frequency plots for flathead goby from selected sites on the Hardey and Beasley rivers.
Barred grunter
The barred grunter (Amniataba percoides) is widely distributed in coastal drainages from
the Ashburton River in the Pilbara Region of Western Australia, around northern Australia,
south to the Burnett River in Queensland (Allen et al. 2002). Breeding is thought to take
place between August and March (Allen et al. 2002). Bishop et al. (2001) reported that
barred grunter spawn at the onset of the wet season and grow about 30 mm in six months.
Size at first maturity varies between sexes, with males being sexually mature at around 77
mm (SL) and females at 88 mm (Rowland 2001). This species is highly fecund (Allen et al.
2002), with females between 70 and 90 g spawning up to 77 000 demersal eggs (Merrick
and Schmida 1984, Hebert and Peeters 1995). The barred grunter attains a maximum size
of up to 200 mm (Rowland 2001).
Barred grunters were recorded at all sites (Table 7). Sites for which sufficient individuals
were collected for length-frequency analysis included BR1 and HR6 (Figure 23). A range of
size classes were recorded from these, including new recruits (<30 mm), juveniles, sub-
adults and adults (>70 mm; Figure 23). This suggests good recruitment of barred grunter at
these sites.
Hardey Aquatic Surveys: 2010 Wetland Research & Management
36
0
2
4
6
8
100
-10
11
-20
21
-30
31
-40
41
-50
51
-60
61
-70
71
-80
Fre
qu
en
cy
Length (mm)
BR1
0
2
4
6
8
10
0-1
0
11
-20
21
-30
31
-40
41
-50
51
-60
61
-70
71
-80
Fre
qu
en
cy
Length (mm)
HR6
Jan May
Figure 23. Length-frequency plots for barred grunter from selected sites on the Hardey and Beasley rivers.
Hardey Aquatic Surveys: 2010 Wetland Research & Management
37
4 CONCLUSIONS
4.1 Water quality
The main water quality findings were:
• Super-saturated DO levels (>100%) were recorded from all sites along the Beasley
River in May. These sites all supported dense macrophyte growth which would be
producing high levels of oxygen through photosynthesis during the day. However,
these sites likely become anoxic overnight as respiration by plants, algae and fauna
deplete DO. Super-saturated DO can also lead to fish bubble disease.
• The circum-neutral to slightly basic pH characteristic of the sites sampled along the
Hardey and Beasley rivers is natural and likely due to surrounding geology. Similarly
basic pH has previously been reported from other systems in the East Pilbara.
• Water quality from sites sampled during the current study ranged from fresh
through to brackish. There is a general acceptance that when conductivity is less
than 1500 µS/cm, freshwater ecosystems experience little ecological stress. As all
sites except HR5 recorded Ec in excess of this value, it is likely the aquatic biota
currently supported by these permanent pools are already adapted to the brackish
conditions and comprise the more salt-tolerant remnants after the more sensitive
species have been eliminated. Any future increases in the electrical conductivity of
these waters will likely result in a change in faunal composition.
• Alkalinity, and therefore the buffering capacity of waters, was high at all sites.
• Ionic composition was dominated by sodium and hydrogen bicarbonate. There was
no difference in the dominance of major ions between sampling period or system.
• All sites recorded elevated levels of either total nitrogen or total phosphorus. Total
nitrogen levels ranged from 0.22 mg/l at BR2 to 13 mg/l at BR3 in January, and from
0.2 mg/l at BR2 to 0.69 mg/l at BR3 in May. The high total nitrogen levels recorded
during the current study could perhaps be attributed to pastoral operations in the
area and unrestricted cattle access to the rivers. Total phosphorus ranged from 0.01
mg/L (at BR2 and HR5) to 0.83 mg/L at BR3.
• Dissolved copper concentrations in excess of the ANZECC/ARMCANZ (2000) 99%
trigger values were recorded from BR1, BR3 and HR6 in January, and HR5 in May. All
sites recorded elevated levels of zinc and boron on both sampling occasions. Given
that elevated levels of zinc and copper have previously been recorded from
waterbodies in the East Pilbara region, including sites that are not downstream of
mine-sites (i.e. other reference sites), the high metal levels recorded during the
current study were considered due to local geology. These data provide a good
baseline to determine future changes. The presence of elevated dissolved metal
levels indicate naturally enriched systems. However, the basic/alkaline conditions
likely prevent excessive mobilisation of available metals into solution. Increased
acidity (i.e. pH falling below 7) may progressively release available metals, and could
lead to toxicity issues.
Hardey Aquatic Surveys: 2010 Wetland Research & Management
38
4.2 Microinvertebrate fauna
The main microinvertebrate fauna findings were:
• The microinvertebrate fauna recorded during the current study was highly diverse.
In comparison to other pools in the Pilbara sampled by the DEC, the Hardey and
Beasley sites were more speciose, and appeared to be richer in testates and rotifers,
but comparable or slightly less speciose in microcrustaceans (Dr Russ Shiel,
University of Adelaide, pers. comm.). A total of 103 taxa were recorded, with 75
taxa being recorded in January, and 67 taxa in May 2010. A considerably greater
number of microinvertebrate taxa were collected from Beasley River sites (a total of
90 taxa) compared with Hardey River sites (51 taxa); although this may in part be
due to the additional site sampled on the Beasley River.
• The microinvertebrate fauna was typical of tropical systems reported elsewhere.
• Microinvertebrate taxa richness varied considerably between river and sampling
occasion. During January 2010, the greatest number of microinvertebrate taxa was
recorded from BR3 (39 taxa), and the least from HR6 (10 taxa). During May 2010,
the greatest number of taxa was recorded from BR1, BR2 and HR5 (all recorded 33
taxa). Again, the least number of microinvertebrate taxa was recorded from HR6 (10
taxa).
• Of interest within the microinvertebrate fauna was the collection of two species
which are only known from the Australian continent, including the Cladocera Moina
cf. micrura recorded from HR5 and Alona cf. rigidicaudis from BR3. Both of these
species are known from across Australia, with a greater number of records in the
eastern states.
• Other microinvertebrate taxa of interest included one species which is rarely
recorded within Australia, the Rotifera Asplanchnopus hyalinus, and another which is
cosmopolitan but rare, the Rotifera Trichocerca cf. agnatha. The former species was
recorded from BR2 in January, and the latter from BR1 in May.
4.3 Hyporheic fauna
The main hyporheic fauna findings were:
• The vast majority of taxa recorded from hyporheic samples were classified as
stygoxene (67%) and do not have specialised adaptations for groundwater habitats.
However, 12% of the taxa were classified as occasional hyporheos stygophiles, 3%
were stygobites, 3% were permanent hyporheic stygophiles, and 6% were possible
hyporheic taxa.
• Hyporheos fauna (i.e. stygobites, possible hyporheic, occasional stygophiles, and
permanent hyporheos stygophiles) were recorded from both river systems. A
greater number of occurrences of hyporheos taxa were recorded from the Beasley
River, although this may be a reflection of the greater sampling effort in this system
(three sites successfully sampled for hyporheos in the Beasley River compared with
one site on the Hardey River).
Hardey Aquatic Surveys: 2010 Wetland Research & Management
39
• Species considered to be restricted to the hyporheos included the stygobitic
amphipod ?Nedsia sp.; occasional stygophiles Mesocyclops cf. darwini (copepod),
Microcyclops varicans (copepod), Elmid beetle larvae Austrolimnius sp., and
Hydraenid beetle Hydraena sp.; the permanent hyporheic stygophile Candonopsis
tenuis (ostracod); and, the possible hyporheos species Oligochaeta spp. and dytiscid
beetle Limbodessus sp.
4.4 Macroinvertebrate fauna
The main macroinvertebrate findings were:
• A total of 92 macroinvertebrate taxa were recorded from the five sites sampled in
January and May 2010. Of these, 58 were recorded in January and 71 were recorded
in May. A greater number of macroinvertebrate taxa were recorded from the
Beasley River (80 taxa) than the Hardey River (62 taxa). Again, this may be due, at
least in part, to the additional site sampled on the Beasley River.
• The composition of macroinvertebrate taxa was typical of freshwater systems
throughout the world (Hynes 1970), and was dominated by Insecta. Of the insects,
the majority were Diptera (36% of Insecta), closely followed by Coleoptera (25% of
Insecta). Molluscs only comprised 3% of the total fauna.
• Macroinvertabrate taxa richness varied between sites and sampling period. In
January, the number of macroinvertebrate taxa recorded ranged from 22 at BR2 to
33 at both BR1 and HR5. In May, the greatest number of taxa was recorded from
BR3 (39 taxa), and the least from HR6 (30 taxa).
• The majority of macroinvertebrate taxa recorded were common, ubiquitous species.
Of the taxa recorded from the Beasley River, 3% had restricted distributions, with 2%
being Northern Australian species, and 1% being endemic to the Pilbara. A total of
10% of the macroinvertebrate taxa from the Hardey River had restricted
distributions; 5% were Northern Australian and 5% were Pilbara Endemic species.
• Of interest was the collection of species known only from the Pilbara region of
Western Australia, including the stygal amphipod ?Nedsia sp., beetle Tiporus
tambreyi and the dragonfly Ictinogomphus dobsoni. Only one Pilbara endemic
species was recorded from the Beasley River, while all three species were found in
the Hardey River.
• It is generally considered that the functional complexity and ‘health’ of an aquatic
ecosystem is reflected by the diversity of functional feeding groups present. All
functional feeding groups were represented in both systems. Predators were the
dominant taxa from both the Hardey and Beasley rivers, followed by collectors.
4.5 Fish
The main fish findings were:
Hardey Aquatic Surveys: 2010 Wetland Research & Management
40
• Seven of the twelve freshwater fish species known from the Pilbara were recorded
during the current study. These were the western rainbowfish Melanotaenia
australis, spangled perch Leiopotherapon unicolor, Hyrtl’s tandan (eel-tailed catfish)
Neosiluris hyrtlii, Fortescue grunter Leiopotherapon aheneus, bony bream
Nematalosa erebi, flathead goby Glossogobius giurus and barred grunter Amniataba
percoides.
• Spangled perch and western rainbowfish were the most common species recorded,
and were found at all sites, while Hyrtl’s tandan was only recorded from BR1 and
HR5.
• The greatest number of fish species was recorded from BR1 and HR5 (seven species).
All other sites recorded six species.
• Generally, the fish recorded are common widespread species. However, the
Fortescue grunter has a restricted distribution within the Pilbara Region of Western
Australia. It is only known from the Fortescue, Robe and Ashburton river systems.
The Fortescue grunter is reasonably common within its range. This species is
currently listed as ‘Lower Risk Near Threatened’ on the IUCN Redlist of Threatened
Species (IUCN 2009). Its status is considered to require updating. This species was
recorded from all sites on both the Hardey and Beasley rivers.
Hardey Aquatic Surveys: 2010 Wetland Research & Management
41
5 RECOMMENDATIONS
Recommendations are provided for future work:
1) The original design was to sample up to 11 sites, with 6 reference sites (three on the
Beasley River and three on the Hardey River upstream of the resource) and 5
potentially exposed sites (two in the resource area itself and three on the Hardey
River immediately downstream of the resource). This design was based on locating
potential waterbodies from topographic maps. However, due to exceedingly dry
weather there were few waterbodies available to sample. It is therefore
recommended that this survey is repeated in 2011, assuming a better wet season,
which will enable aquatic sampling of additional control and potentially exposed
sites.
2) The data presented in this report provides a good baseline for both systems under
drought conditions, and likely shows an extreme condition. The survey should be
repeated under average wet season conditions to show the fauna under a less
stressed condition. The natural range in condition will provide a context for any
future mine effects, which may be small relative to natural variability.
3) The snap-shot of water quality data indicate natural (non mine-related) exceedances
of ANZECC TVs, especially in dissolved metals, but also some in situ parameters.
Continued water quality monitoring is recommended to determine the
representativeness of the current data, collected under drought conditions.
4) Two specimens of the hyporheic/stygal ?Nedsia amphipod were collected. These
may be the same or different species, and they may also be the same as Nedsia
previously collected from the Pilbara. It is recommended the two specimens are
DNA-sequenced to identify whether they are know species, or species new to
science using the gen-bank database of Pilbara Amphipod DNA sequences.
Hardey Aquatic Surveys: 2010 Wetland Research & Management
42
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APPENDICES
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Appendix 1. Site photographs BEASLEY RIVER BR1 JAN MAY
BR2 JAN MAY
BR3 (WOONGARRA POOL) JAN MAY
HARDEY RIVER
Hardey Aquatic Surveys: 2010 Wetland Research & Management
48
HR5 (KAZPUT POOL) JAN MAY
HR6 JAN MAY
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Appendix 2. ANZECC/ARMCANZ (2000) trigger values for the protection of aquatic systems in tropical northern Australia
Table A2-1. Default trigger values for some physical and chemical stressors for tropical Australia for slightly disturbed ecosystems (TP = total phosphorus; FRP = filterable reactive phosphorus; TN = total nitrogen; NOx = total nitrates/nitrites; NH4+ = ammonium). Data derived from trigger values supplied by Australian states and territories, for the Northern Territory and regions north of Carnarvon in the west and Rockhampton in the east (ANZECC/ARMCANZ 2000).
TP FRP TN NOx NH4+ DO pH
Aquatic Ecosystem (µg L-1
) (µg L-1
) (µg L-1
) (µg L-1
) (µg L-1
) % saturationf
Upland Rivere 10 5 150 30 6 90-120 6.0-7.5
Lowland Rivere 10 4 200-300
h 10
b 10 85-120 6.0-8.0
Lakes & Reservoirs 10 5 350c 10
b 10 90-120 6.0-8.0
Wetlands3 10-50
g 5-25
g 350-1200
g 10 10 90
b-120
b 6.0-8.0
b = Northern Territory values are 5µgL-1 for NOx, and <80 (lower limit) and >110% saturation (upper limit) for DO; c = this value represents turbid lakes only. Clear lakes have much lower values; e = no data available for tropical WA estuaries or rivers. A precautionary approach should be adopted when applying default trigger values to these systems; f = dissolved oxygen values were derived from daytime measurements. Dissolved oxygen concentrations may vary diurnally and with depth. Monitoring programs should assess this potential variability; g = higher values are indicative of tropical WA river pools; h = lower values from rivers draining rainforest catchments.
Table A2-2. Default trigger values for salinity and turbidity for the protection of aquatic ecosystems, applicable to tropical systems in Australia (ANZECC/ARMCANZ 2000).
Salinity Comments
Aquatic Ecosystem (µs/cm)
Upland & lowland rivers 20-250 Conductivity in upland streams will vary depending on catchment geology. The first flush may result in temporarily high values
Lakes, reservoirs & wetlands 90-900 Higher conductivities will occur during summer when water levels are reduced due to evaporation
Turbidity
(NTU)
Upland & lowland rivers 2-15 Can depend on degree of catchment modification and seasonal rainfall runoff
Lakes, reservoirs & wetlands 2-200
Most deep lakes have low turbidity. However, shallow lakes have higher turbidity naturally due to wind-induced re-suspension of sediments. Wetlands vary greatly in turbidity depending on the general condition of the catchment, recent flow events and the water level in the wetland.
Hardey Aquatic Surveys: 2010 Wetland Research & Management
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Table A2-3. Trigger values for toxicants at alternative levels of protection.
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51
Appendix 3. Water quality data from January and May 2010.
Table A3-1. In situ water quality data collected in January 2010. Shading indicates values outside ANZECC/ARMCANZ (2000) guidelines.
Site Date Time pH Temp (ºC) EC (µS/cm) DO (%) DO (mg/L)
BR1 15/01/2010 830 8.59 30.9 1718 77.2 8.50
BR2 14/01/2010 1245 8.62 34.1 1582 77 5.10
BR3 15/01/2010 1200 8.38 29.2 1628 37.5 2.95
HR5 16/01/2010 1100 7.53 31.2 1417 55 3.24
HR6 16/01/2010 900 8.89 29.7 1792 69.1 5.19
Table A3-2. In situ water quality data collected in May 2010. Shading indicates values outside ANZECC/ARMCANZ (2000) guidelines.
Site Date Time pH Temp (ºC) EC (µS/cm) DO (%) DO (mg/L)
BR1 18/05/2010 1200 8.8 21 1509 126.8 11.55
BR2 18/05/2010 1410 8.65 23 1421 161.7 13.70
BR3 18/05/2010 1530 8.75 21.2 1925 115.3 10.50
HR5 19/05/2010 1015 7.66 20.5 1242 44.5 3.88
HR6 19/05/2010 900 8.54 21.3 1672 46.3 4.14
Table A3-3. Nutrient and ionic composition data collected in the January 2010. Shading indicates values outside ANZECC/ARMCANZ (2000) guidelines. All values are mg/L. Refer Table A3-1 for dates and times of water sample collection.
Site Na Mg Ca K HCO3 CO3 Cl SO4_S Alkalinity N_NH3 N_NO3 Total_N Total_P
BR1 209 100 32.9 6.2 439 42 265 122 430 0.02 0.005 0.68 0.04
BR2 193 94.4 22.6 4.6 354 60 224 138 390 0.01 0.005 0.22 0.01
BR3 203 81.1 29.8 7.1 372 36 249 131 365 0.5 0.005 13 0.83
HR5 137 89.7 55.8 1.8 561 0.5 156 80.4 460 0.01 0.08 0.51 0.01
HR6 209 118 21.7 4.1 549 42 270 67.8 520 0.005 0.01 0.43 0.02
Table A3-4. Nutrient and ionic composition data collected in the May 2010. Shading indicates values outside ANZECC/ARMCANZ (2000) guidelines. All values are mg/L. Refer Table A3-2 for dates and times of water sample collection.
Site Na Mg Ca K HCO3 CO3 Cl SO4_S Alkalinity N_NH3 N_NO3 Total_N Total_P
BR1 217 105 37 5.5 500 30 277 133 460 0.005 0.01 0.39 0.02
BR2 176 87.7 42.9 3.9 439 48 236 146 440 0.005 0.005 0.2 0.01
BR3 291 109 30.1 10.5 433 84 402 204 495 0.02 0.005 0.69 0.04
HR5 131 85.7 58.2 2.9 598 0.5 178 104 490 0.01 0.37 0.68 0.02
HR6 186 111 34.5 5.4 598 42 272 113 560 0.17 0.05 0.91 0.03
Hardey Aquatic Surveys: 2010 Wetland Research & Management
52
Table A3-5. Metal concentration data collected in January 2010. Shading indicates values outside ANZECC/ARMCANZ (2000) guidelines. All values are mg/L.
Beasley River Hardey River
BR1 BR2 BR3 HR5 HR6
Aluminium 0.011 0.0025 0.0025 0.0025 0.0025
Arsenic 0.002 0.0005 0.002 0.002 0.0005
Boron 0.21 0.2 0.34 0.34 0.39
Barium 0.027 0.024 0.049 0.033 0.02
Cadmium 0.00005 0.00005 0.00005 0.00005 0.00005
Cobalt 0.0001 0.00005 0.0003 0.00005 0.00005
Chromium 0.00025 0.00025 0.00025 0.00025 0.00025
Copper 0.0026 0.0009 0.0015 0.001 0.0019
Iron 0.026 0.005 0.026 0.018 0.019
Manganese 0.015 0.0005 0.007 0.013 0.082
Molybdenum 0.001 0.002 0.003 0.002 0.001
Nickel 0.0005 0.0005 0.0005 0.0005 0.0005
Lead 0.0001 0.00005 0.00005 0.00005 0.00005
Selenium 0.0005 0.0005 0.0005 0.001 0.0005
Uranium 0.0009 0.0005 0.0003 0.0013 0.0005
Vanadium 0.0054 0.0038 0.0024 0.012 0.0024
Zinc 0.003 0.003 0.003 0.003 0.003
Table A3-6. Metal concentration data collected in May 2010. Shading indicates values outside ANZECC/ARMCANZ (2000) guidelines. All values are mg/L.
Beasley River Hardey River
BR1 BR2 BR3 HR5 HR6
Aluminium 0.0025 0.0025 0.0025 0.0025 0.0025
Arsenic 0.002 0.001 0.003 0.002 0.004
Boron 0.49 0.41 0.68 0.41 0.53
Barium 0.03 0.074 0.079 0.039 0.039
Cadmium 0.00005 0.00005 0.00005 0.00005 0.00005
Cobalt 0.0001 0.0001 0.0002 0.0002 0.0002
Chromium 0.00025 0.00025 0.00025 0.00025 0.00025
Copper 0.0006 0.001 0.0004 0.0018 0.0006
Iron 0.016 0.026 0.11 0.046 0.066
Manganese 0.003 0.034 0.1 0.031 0.026
Molybdenum 0.003 0.003 0.004 0.003 0.006
Nickel 0.002 0.0005 0.0005 0.0005 0.0005
Lead 0.00005 0.00005 0.00005 0.0002 0.00005
Selenium 0.0005 0.0005 0.0005 0.001 0.0005
Uranium 0.0017 0.0019 0.0005 0.0022 0.0026
Vanadium 0.011 0.006 0.0029 0.017 0.0086
Zinc 0.016 0.005 0.005 0.007 0.039
Hardey Aquatic Surveys: 2010 Wetland Research & Management
Appendix 4. Microinvertebrate data from January and May 2010.
Abundance of microinvertebrates (log10 abundance category) from each site sampled, where 1 = 1 individual, 2 = 2-10 individuals, 3 = 10 – 100, and so on.
January 2010 May 2010
BR1 BR2 BR3 HR5 HR6 BR1 BR2 BR3 HR5 HR6
PROTISTA
Ciliophora Euplotes 0 0 0 0 0 0 2 0 3 0
med. indet. ciliate 0 0 3 0 0 0 0 0 0 0
Rhizopoda Arcellidae Arcella discoides 0 0 2 1 0 2 2 0 3 1
Arcella hemisphaerica 0 0 0 0 0 0 0 0 2 0
Arcella megastoma 1 1 0 0 0 0 0 0 0 0
Arcella a 2 0 0 0 0 0 0 0 0 0
Arcella b 0 2 1 0 0 1 0 0 2 0
Arcella c 0 0 0 0 0 1 0 0 2 2
Centropyxidae Centropyxis aculeata 0 0 0 0 0 0 0 0 1 0
Centropyxis ecornis 1 0 1 1 1 2 2 0 0 0
Centropyxis a 0 0 1 0 0 0 0 0 0 0
Cyclopyxidae Cyclopyxis sp. 0 0 0 0 1 0 0 0 0 0
Difflugiidae Difflugia gramen 0 0 0 0 1 2 0 0 2 0
Difflugia sp.a 1 0 0 0 0 2 0 0 0 2
Difflugia sp.b [med, ovoid] 1 0 2 0 0 0 0 0 0 0
Euglyphidae Euglypha sp. a [sm] 0 0 0 0 0 1 0 0 0 0
Euglypha sp. b [med] 0 0 0 0 0 2 2 0 0 0
Lesquereusiidae Lesquereusia modesta 0 0 0 0 0 0 2 0 0 0
Lesquereusia spiralis 0 0 0 0 0 1 0 0 2 0
Netzelia oviformis 0 0 0 0 0 2 0 0 0 0
Netzelia tuberculata 0 0 2 2 1 1 0 0 1 0
Nebilidae Nebela sp. 0 0 1 0 0 0 0 0 0 0
ROTIFERA
Bdelloidea bdelloid sp. a [sm. contr] 0 0 2 0 0 3 0 0 2 0
bdelloid sp. b [med. contr] 2 1 0 2 0 0 0 0 0 0
bdelloid sp. c [lg. contr] 0 0 2 0 0 3 2 0 2 1
Monogononta
Asplanchnidae Asplanchnopus hyalinus 0 1 0 0 0 0 0 0 0 0
Hardey Aquatic Surveys: 2010 Wetland Research & Management
January 2010 May 2010
BR1 BR2 BR3 HR5 HR6 BR1 BR2 BR3 HR5 HR6
Brachionidae Anuraeopsis fissa 3 0 0 0 0 0 0 0 0 0
Brachionus angularis 2 0 1 0 0 0 0 3 1 0
Brachionus calyciflorus 3 0 0 0 0 1 0 0 0 0
Brachionus falcatus 3 0 0 0 0 0 0 0 0 0
Brachionus quadridentatus 2 0 0 1 0 0 0 1 1 0
Brachionus sp. 0 1 0 0 0 0 0 1 0 0
Keratella tropica 0 1 0 0 0 0 0 0 0 0
Platyias quadricornis 0 0 1 0 0 0 0 0 1 0
Dicranophoridae Dicranophorus epicharis 0 0 0 1 0 0 0 0 0 0
Euchlanidae Euchlanis cf. dilatata 0 0 0 1 0 0 0 0 0 0
Tripleuchlans plicata 0 0 0 0 0 0 1 0 0 0
Gastropodidae Ascomorpha ovalis 3 3 2 0 0 0 0 0 0 0
Lecanidae Lecane arcula 0 0 0 0 0 1 0 0 0 0
Lecane batillifer 0 0 0 0 0 2 1 0 0 0
Lecane bulla 2 1 3 1 1 1 2 1 2 0
Lecane cf. crepida 0 0 0 0 0 0 2 0 0 0
Lecane curvicornis 0 0 0 1 0 0 0 0 0 0
Lecane cf. elsa 0 0 1 0 0 0 0 0 0 0
Lecane hamata 0 1 0 0 0 0 0 0 0 0
Lecane leontina 0 0 3 0 0 0 0 0 0 0
Lecane cf. ludwigii 0 0 1 0 0 0 0 0 0 0
Lecane luna 0 1 0 0 0 0 0 1 0 0
Lecane papuana 0 0 0 0 0 0 1 0 0 0
Lecane cf. thalera 1 1 0 0 0 0 1 1 0 0
Lecane (M.) sp. a 1 0 2 1 1 0 1 0 0 0
Lecane (M.) sp. b 0 0 0 0 0 0 2 0 1 0
Lecane (M.) sp. c 0 0 0 0 0 0 1 0 1 0
Lepadellidae Colurella 0 1 3 0 0 2 3 0 2 0
Lepadella cf. acuminata 2 1 0 0 0 0 3 0 0 0
Lepadella (H.) ehrenbergii 0 0 0 0 0 1 1 0 0 0
Lepadella ovalis 0 0 1 0 0 2 0 1 2 0
Lepadella triptera 2 0 3 0 0 0 2 0 0 0
Lepadella sp. a 0 0 2 0 0 1 1 0 0 0
Squatinella sp. 0 0 0 0 0 1 0 0 0 0
Mytilinidae Mytilina ventralis 0 0 0 0 0 2 0 0 0 0
Hardey Aquatic Surveys: 2010 Wetland Research & Management
January 2010 May 2010
BR1 BR2 BR3 HR5 HR6 BR1 BR2 BR3 HR5 HR6
Notommatidae Cephalodella forficula 0 0 2 0 0 0 0 0 0 0
Cephalodella gibba 1 0 0 0 0 1 0 0 2 0
Cephalodella sp. a 0 0 1 0 0 0 1 0 1 0
Monommata sp. 0 0 0 0 0 0 0 0 1 0
Notommata sp. 0 0 0 0 0 2 0 0 0 0
Proalidae Proales sp. 0 0 2 0 0 0 0 0 0 0
Scaridiidae Scaridium longicaudum 0 0 0 0 0 1 0 0 3 0
Synchaetidae Polyarthra sp. 1 3 0 0 0 0 3 0 0 0
Synchaeta sp. 2 0 0 0 0 0 0 0 1 0
Testudinellidae Testudinella amphora 0 0 3 0 0 0 0 0 0 0
Testudinella patina 0 0 0 0 0 0 1 1 0 1
Trichocercidae Trichocerca cf. agnatha 0 0 0 0 0 1 0 0 0 0
Trichocerca pusilla 2 2 0 0 0 0 0 0 0 0
Trichocerca similis 2 2 0 4 0 1 0 0 2 0
Trichocerca similis grandis 1 0 0 0 0 0 0 0 0 0
Trichocerca cf. tigris 1 0 0 0 0 0 0 0 0 0
Trichocerca sp. [sm] 0 0 0 0 0 0 1 0 0 0
Trichotriidae Macrochaetus sp. 1 0 1 1 0 0 0 0 0 0
indet rotifer 0 0 1 0 0 0 0 0 2 0
CLADOCERA
Chydoridae Alona cf. intermedia 0 0 3 0 0 0 0 0 0 0
Alona cf. rigidicaudis 0 0 2 0 0 0 0 0 0 0
Alona cf. pseudoverrucosa 0 0 2 0 0 0 1 0 3 0
Alona sp. [decomposed] 0 0 0 0 1 0 0 0 0 0
Alonella sp. [juv.] 0 0 0 0 0 1 0 0 0 0
Armatalona macrocopa 0 0 3 0 0 0 0 0 0 0
Ephemeroporus barroisi 0 0 3 0 0 0 2 0 0 0
Daphniidae Ceriodaphnia cornuta 0 1 0 0 0 0 1 3 2 1
Simocephalus sp. [juv] 0 1 0 0 0 0 1 0 0 0
Macrotrichidae Macrothrix sp. 0 0 0 0 1 0 0 0 0 0
Moinidae Moina cf. micrura 0 0 0 1 0 0 0 0 0 0
COPEPODA
Cyclopoida Mesocyclops cf. darwini 2 1 2 0 0 0 0 1 2 1
Mesocyclops sp. a 0 0 0 1 1 1 0 0 0 1
Hardey Aquatic Surveys: 2010 Wetland Research & Management
January 2010 May 2010
BR1 BR2 BR3 HR5 HR6 BR1 BR2 BR3 HR5 HR6
Microcyclops ?varicans 0 0 1 0 0 0 0 0 0 0
cf. Paracyclops 0 0 0 1 0 0 0 0 0 0
Thermocyclops sp. 0 0 0 0 0 0 0 1 2 0
Tropocyclops sp. 0 1 1 2 0 1 1 1 0 0
copepodites 3 2 3 3 1 3 2 3 3 2
nauplii 4 4 3 3 0 3 4 4 3 4
OSTRACODA
Limnocythere 0 0 2 0 0 0 1 0 0 0
indet camouflg. ostracod 0 0 0 0 0 0 0 0 1 0
juv. ostracod a [ovoid] 0 0 0 1 0 0 1 0 0 0
juv. ostracod b [elongate] 0 0 0 1 0 0 0 0 0 0
Taxa richness 28 22 39 20 10 33 33 14 33 10
Hardey Aquatic Surveys: 2010 Wetland Research & Management
Appendix 5. Hyporheic fauna recorded from the Hardey and Beasley rivers in January and May 2010.
Abundance of invertebrates (log10 abundance category) from each hyporheic sample, where 1 = 1 individual, 2 = 2-10 individuals, 3 = 10 – 100, and so on.
January 2010 May 2010
BR1 BR2 BR3 HR6 BR1 BR2 BR3 HR6
ANNELIDA
OLIGOCHAETA Oligochaeta spp. 0 0 0 1 2 0 0 0
CRUSTACEA
AMPHIPODA
Crangonyctoid Melitidae ?Nedsia sp. 0 0 0 0 0 1 0 0
COPEPODA
Cyclopoida Cyclopodidae Mesocyclops cf. darwini 0 0 2 0 0 0 0 0
Microcyclops varicans 0 3 2 2 0 0 0 2
OSTRACODA Candonopsis tenuis 0 2 0 0 2 0 0 0
ARACHNIDA
ACARINA Hydracarina spp. 1 0 2 0 2 1 0 0
COLLEMBOLLA Collembolla spp. 1 0 0 0 0 0 0 0
INSECTA
COLEOPTERA Carabidae Carabidae spp. (A) 2 0 0 0 0 0 0 0
Dytiscidae Limbodessus sp. (A) 0 0 2 0 0 0 0 0
Elmidae Austrolimnius sp (L) 0 1 0 0 0 0 0 0
Heteroceridae Heteroceridae spp. (L) 0 1 2 0 0 0 0 0
Hydraenidae Hydraena sp. 0 0 0 1 0 0 0 0
Hydrophilidae Hydrophilidae spp. (L) 2 1 2 1 1 0 0 0
Georissidae Georissus sp. 2 1 0 0 0 0 0 0
Scirtidae Scirtidae spp. (L) 0 0 2 2 0 3 1 0
DIPTERA Chironomidae
Tanypodinae Paramerina sp. 0 2 0 3 0 0 0 0
Procladius sp. 0 0 0 2 0 0 0 0
Hardey Aquatic Surveys: 2010 Wetland Research & Management
January 2010 May 2010
BR1 BR2 BR3 HR6 BR1 BR2 BR3 HR6
Orthocladinae Thienemanniella sp. 0 0 0 2 0 0 0 0
Corynonoeura sp. 0 0 0 3 0 0 0 0
WWO8 0 0 0 0 0 0 1 0
WWO12 0 0 0 1 0 0 0 0
Chironomini Paratendipes "K1" 3 1 0 0 0 0 0 0
Chironomus sp. 0 0 0 1 0 0 0 0
Dicrotendipes sp2 0 0 0 2 0 0 0 0
Cladopelma curtivala 0 0 0 2 0 0 0 0
Tanytarsus sp. 3 0 0 2 0 0 0 0
Paratanytarsus sp. 0 0 0 1 1 0 0 0
Ceratopogonidae Ceratopogoniinae spp. (P) 0 0 2 1 0 0 0 0
Ceratopogoniinae spp. 3 3 3 2 2 3 3 2
Dasyheilenae spp. 3 2 1 1 3 3 0 1
Muscidae Muscidae spp. 0 0 0 0 0 1 0 0
Pelecorhynchidae Pelecorhynchidae spp. 0 1 0 1 0 0 0 0
Tipulidae Tipulidae spp. 2 0 0 0 2 0 0 0
TAXA RICHNESS 10 11 10 19 8 6 3 3
Hardey Aquatic Surveys: 2010 Wetland Research & Management
Appendix 6. Macroinvertebrate data from January and May 2010.
Abundance of macroinvertebrates (log10 abundance category) from each site sampled, where 1 = 1 individual, 2 = 2-10 individuals, 3 = 10 – 100, and so on.
January 2010 May 2010
BR1 BR2 BR3 HR5 HR6 BR1 BR2 BR3 HR5 HR6
TURBELLARIA Turbellaria spp. 0 0 0 0 0 0 1 0 1 0
CNIDARIA
HYDROZOA Hydra sp. 0 0 0 2 0 0 2 2 2 4
MOLLUSCA
GASTROPODA Planorbidae Gyraulus hesperus 0 2 0 0 2 3 4 2 0 4
Lymnaeidae Austropeplea lessoni 1 0 0 2 2 0 0 2 0 3
BIVALVIA Hyriidae Velesunio wilsonii 2 0 0 0 0 2 0 0 0 0
ANNELIDA
OLIGOCHAETA Oligochaeta spp. 2 3 2 3 0 2 1 2 2 4
ARTHROPODA
CRUSTACEA
AMPHIPODA Melitidae ?Nedsia sp. 0 0 0 0 1 0 0 0 0 0
ARACHNIDA
ACARINA Hydracarina spp. 3 3 3 2 3 5 3 4 3 4
Oribatida spp. 0 0 0 0 0 0 1 0 1 0
INSECTA
COLEOPTERA Dytiscidae Allodessus bistrigatus 0 0 0 0 0 0 0 1 0 0
Antiporus bakewelli 0 0 0 0 1 0 0 1 0 0
Cybister godeffroyi 1 0 0 0 0 0 0 0 0 0
Cybister tripunctatus 0 0 0 2 0 0 0 0 0 0
Hydroglyphus daemeli 0 0 0 0 0 2 0 0 1 0
Hydroglyphus trilineatus 0 0 0 0 0 0 0 0 2 0
Hardey Aquatic Surveys: 2010 Wetland Research & Management
January 2010 May 2010
BR1 BR2 BR3 HR5 HR6 BR1 BR2 BR3 HR5 HR6
Hyphydrus elegans 0 0 0 0 1 0 0 0 1 0
Hyphydrus lyratus 0 0 1 0 0 0 0 0 0 0
Hyphydrus sp. (L) 0 0 0 0 0 0 1 0 0 0
Laccophilus sharpi 0 0 0 0 0 1 0 0 0 0
Necterosoma sp. (L) 0 0 0 0 0 0 0 2 0 0
Necterosoma regulare 2 2 2 3 2 1 1 3 2 2
Onychohydrus sp. (L) 0 0 0 0 0 0 0 0 0 2
Tiporus tambreyi 3 3 3 0 3 0 1 2 0 2
Tribe Bidessini sp. (L) 0 0 2 0 0 0 0 0 0 0
Gyrinidae Dineutus australis 0 0 0 0 0 1 0 0 0 2
Hydraenidae Hydraena sp. 0 0 0 1 0 0 0 0 0 0
Limnebius sp. 0 0 0 0 1 0 0 0 0 0
Octhebius sp. 2 0 1 0 0 0 0 0 0 0
Hydrochidae Hydrochus sp. 3 1 0 3 2 1 0 0 2 0
Hydrophilidae Berosus sp. (L) 0 0 0 0 0 0 2 3 0 0
DIPTERA Ceratopogonidae Ceratopogonidae spp. (P) 1 0 3 0 0 2 0 0 0 0
Ceratopogoninae spp. 2 3 2 2 3 3 2 4 3 0
Dasyheleinae spp. 2 3 2 3 3 4 3 2 2 4
Chironomidae Chironomidae spp. (P) 0 0 2 1 3 0 0 0 0 3
Paramerina sp. 1 2 0 1 0 2 0 0 3 0
Larsia ?albiceps 3 3 3 3 3 3 4 0 4 3
Procladius sp. 2 2 2 1 3 0 3 3 2 4
Nanocladius sp. 0 0 0 0 0 0 1 0 0 0
WWT13 1 0 0 1 0 0 0 0 0 0
Chironomus sp. 0 0 0 0 0 3 0 5 3 3
Cryptochironomus griseidorsum 0 0 0 0 0 0 2 0 0 0
Paratendipes "K1" 0 2 0 0 0 0 0 0 0 0
Polypedilum (Pentapedilum) leei 1 1 0 0 1 5 2 1 0 0
Polypedilum nubifer 0 0 0 0 0 0 0 1 0 2
Dicrotendipes sp1 0 0 0 1 0 0 0 0 0 0
Dicrotendipes sp2 0 0 0 1 0 0 2 0 0 2
Cladopelma curtivala 1 0 1 2 1 0 3 0 0 1
Polypedilum sp. 0 0 1 1 0 0 1 0 2 0
Kiefferulus intertinctus 0 0 0 0 0 0 0 2 0 0
Parachironomussp. (?K2) 1 0 0 0 0 0 0 0 0 0
Hardey Aquatic Surveys: 2010 Wetland Research & Management
January 2010 May 2010
BR1 BR2 BR3 HR5 HR6 BR1 BR2 BR3 HR5 HR6
Tanytarsus sp. 2 2 2 2 0 3 2 2 3 0
Paratanytarsus sp. 3 3 3 3 3 3 2 0 4 0
Cladotanytarsus sp. 0 0 0 0 0 0 3 0 4 0
WWTS5 0 0 0 0 0 0 2 0 0 0
Culicidae Anopheles sp. 2 0 2 0 2 2 2 0 3 0
Culex sp. 2 0 0 0 0 0 0 0 2 2
Empididae Empididae spp. 0 0 0 0 0 0 0 2 0 0
Psychidae Psychodidae spp. 0 0 0 0 0 0 0 0 2 0
Stratiomyidae Stratiomyidae spp. 0 0 1 2 0 2 1 0 0 0
Tabanidae Tabanidae spp. 0 0 0 0 0 1 0 1 0 0
EPHEMEROPTERA Baetidae Cloeon sp. 1 3 2 3 0 5 4 4 2 4
Caenidae Tasmanacoenis arcuata 0 0 0 0 0 2 3 2 0 0
HEMIPTERA Belostomatidae Diplonychus sp. (imm) 2 0 2 0 2 2 2 2 0 2
Diplonychus eques 0 0 0 0 0 0 0 1 1 0
Gelastocoridae Nertha sp. 1 0 0 0 0 0 0 0 0 0
Corixidae Micronecta sp. (imm) 0 0 0 0 0 3 3 4 2 4
Gerridae Limnogonus fossarum gilguy 2 2 0 2 0 0 2 0 0 0
Hebridae Hebrus axillaris 0 0 0 1 0 0 2 0 0 0
Notonectidae Anisops sp. (imm.) 0 0 0 0 0 0 0 2 0 0
Anisops sp. (female) 0 0 0 0 0 0 0 4 0 0
Anisops deanei 0 0 0 0 0 0 0 2 0 0
Anisops nabillus 0 0 0 0 0 0 0 2 0 0
Anisops nasutus 0 0 0 0 0 0 0 3 0 1
Mesoveliidae Mesovelia vittigera 0 0 0 1 0 0 0 0 0 0
Paraplea Ranatra occidentalis 2 0 0 0 0 0 0 0 0 0
Paraplea brunni 3 2 0 2 3 5 4 2 0 3
LEPIDOPTERA Nymphulinae sp. WRM 1 0 0 2 0 0 0 0 0 0 0
ODONATA
Zygoptera Zygoptera spp. (imm) 2 2 2 1 2 0 0 2 0 3
Coenogrionidae Coenagrionidae spp. (imm) 2 0 0 2 0 0 0 0 0 0
Agriocnemis rubescens 2 2 3 0 2 3 2 2 2 3
Pseudagrion aurefrons 0 1 1 2 0 3 2 2 2 3
Pseudagrion microcephalum 1 0 0 0 0 0 0 0 0 0
Anisoptera Anisoptera spp. (imm) 0 0 0 0 0 4 0 0 0 0
Aeshnidae Aeshnidae spp. (imm.) 0 0 0 0 0 0 3 0 1 3
Hardey Aquatic Surveys: 2010 Wetland Research & Management
January 2010 May 2010
BR1 BR2 BR3 HR5 HR6 BR1 BR2 BR3 HR5 HR6
Hemianax papuensis 0 0 0 0 0 2 0 2 0 0
Gomphidae Austrogomphus gordoni 0 0 0 0 1 0 0 0 0 0
Lindeniidae Ictinogomphus dobsoni 0 0 0 1 0 0 0 0 0 0
Libellulidae Diplacodes haematodes 0 0 2 1 2 2 2 2 2 2
Orhtetrum caledonicum 0 0 0 0 0 1 0 4 0 2
Tramea sp. 0 0 0 0 0 0 0 3 0 2
TRICHOPTERA Ecnomidae Ecnomus sp. 0 2 1 1 0 0 0 0 1 0
Hydroptilidae Orthotrichia sp. 0 0 1 0 1 0 0 0 0 0
TAXA RICHNESS 33 22 28 33 26 32 37 39 31 30