HARDEY RESOURCE: AQUATIC ECOSYSTEM SURVEYS€¦ · PRE- & POST-WET 2010 SAMPLING FINAL REPORT HARDEY RESOURCE: AQUATIC ECOSYSTEM SURVEYS Wetland Research & Management January 2011

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 Unpublished DRAFT report by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).


iii

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


3.3.2 Hyporheos taxa .................................................................................................................................. 22

3.4 Macroinvertebrates ............................................................................................... 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


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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


1

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.


2

Figure 1. Location of the Hardey Resource in the Pilbara Region of W.A., showing the Hardey and Beasley river systems.


3

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.


4

0

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Figure 2. Rainfall at the Airstrip gauging station on the Hardey River, showing average total monthly rainfall (left) and total annual rainfall (right).

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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.


5

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.


6

Figure 5. Location of the Hardey River potential impact sites and the Beasley River reference sites with respect to the Hardey resource.


7

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.


8

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.


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.


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.


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.


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.


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


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.


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).


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


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


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.


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


Co

pp

er

(mg

/L

)

0

0.01

0.02

0.03

0.04

BR1 BR2 BR3 HR5 HR6


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


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.


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



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


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)


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).


21

3.3 Hyporheic fauna


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


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.


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).


23

3.4 Macroinvertebrates


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


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.


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


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

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BR1 BR2 BR3 HR5 HR6


Ma

cro

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ta

xa

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January May

Figure 14. Macroinvertebrate taxa richness recorded from each site on each sampling occasion.


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,


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).


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).


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


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.


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


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.


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).


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.


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).


34

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Figure 21. Length-frequency plots of bony bream from selected sites.


35

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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.


36

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Figure 23. Length-frequency plots for barred grunter from selected sites on the Hardey and Beasley rivers.


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.


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).


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:


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.


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.


42

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46

APPENDICES


47

Appendix 1. Site photographs BEASLEY RIVER BR1 JAN MAY

BR2 JAN MAY

BR3 (WOONGARRA POOL) JAN MAY

HARDEY RIVER


48

HR5 (KAZPUT POOL) JAN MAY

HR6 JAN MAY


49

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.


50

Table A2-3. Trigger values for toxicants at alternative levels of protection.


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


52

Table A3-5. Metal concentration data collected in January 2010. Shading indicates values outside ANZECC/ARMCANZ (2000) guidelines. All values are mg/L.


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.


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


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




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




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




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


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.


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



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


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.



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




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




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




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

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