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BOUNDARY HILL SOUTH PROJECT

Aquatic Ecology Assessment

Q1

Boundary Hill Expansion Environmental Impact Statement

Aquatic Ecology Assessment

Prepared for:

AECOM on behalf of Angle American (Callide Mine)

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PO Box 2363, Wellington Point QLD 4160 Telephone: + 61 3286 3850 Facsimile: + 61 3821 7936

frc reference: 111103

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1 Using the documents or data in electronic form without requesting and checking them for accuracy against the original signed hard copy version; and

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Boundary Hill Expansion EIS: Aquatic Ecology FRC_Files:frc_projects:Projects:2011:111103_AEC_Bound_Hill:Report:Current:AE:111103Riii_AE_13-07_05_1604_NS.docx

Document Control Summary

Project No.: 111103

Status: Final Report

Project Director: Lauren Thorburn

Project Manager: Nirvana Searle

Title: Boundary Hill Expansion Environmental Impact Statement: Aquatic Ecology Assessment

Project Team: C. Chargulaf, C. Josey, B. Cook, N. Searle and L. Thorburn

Client: AECOM on behalf of Anglo American (Callide Mine)

Client Contact: Jared Brook

Date: 5 July 2013

Edition: 111103Riii_AE

Checked by: Carol Conacher _______________

Issued by: Nirvana Searle _______________

Distribution Record

AECOM: 2 electronic copies (1 word copy and 1 pdf copy)

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Boundary Hill Expansion EIS: Aquatic Ecology

Contents

Summary i

1 Introduction 1

1.1 Project Background 1

1.2 Description of the Survey Area 2

2 Legal Framework 5

2.1 Commonwealth’s Environmental Protection and Biodiversity Conservation Act 1999 5

2.2 Queensland’s Environmental Protection Act 1994 10

2.3 Queensland’s Fisheries Act 1994 13

2.4 Queensland’s Nature Conservation Act 1992 16

2.5 Queensland’s Land Protection (Pest and Stock Management) Act 2002 17

2.6 Queensland’s Water Act 2000 19

2.7 Queensland’s Sustainable Planning Act 2009 20

2.8 Wetlands of National, State or Regional Significance 23

3 Methods 26

3.1 Survey Design 26

3.2 Aquatic Habitat 29

3.3 Aquatic Plants 32

3.4 Aquatic Macroinvertebrates 35

3.5 Aquatic Vertebrates 39

3.6 Limitations 42

4 Aquatic Habitat 43

4.1 Aquatic Habitat of the Region 43

4.2 Aquatic Habitat of the Survey Area 45

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5 Aquatic Plants 66

5.1 Aquatic Plants of the Region 66

5.2 Aquatic Plants of the Survey Area 66

6 Aquatic Macroinvertebrates 73

6.1 Aquatic Macroinvertebrate Communities of the Region 73

6.2 Aquatic Macroinvertebrates of the Survey Area 73

7 Aquatic Vertebrates 86

7.1 Aquatic Vertebrates of the Region 86

7.2 Aquatic Vertebrates of the Survey Area 93

8 Summary of Aquatic Ecological Values 105

9 Potential Impacts 106

9.1 Operation and Maintenance of Vehicles and Other Equipment 109

9.2 Vegetation Clearing and Earthworks 110

9.3 Management of Water Resources 112

9.4 Loss of Catchment Area 112

9.5 Loss of On-site Dams and Wetlands 113

9.6 Creek Diversions 113

9.7 Changes to Flow Regimes 114

9.8 Creek Crossings 114

9.9 Matters of National Environmental Significance 115

10 Mitigation Measures 116

10.1 Operation and Maintenance of Vehicles and Equipment 116

10.2 Vegetation Clearing and Earthworks 116

10.3 Management of Water Resources 117

10.4 Loss of Catchment Area 118

10.5 Loss of On-site Dams and Wetlands 118

10.6 Creek Diversions 119

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10.7 Creek Crossings 121

10.8 Monitoring Requirements 123

11 Risk Assessment 125

11.1 Methods 125

11.2 Impact Assessment 128

12 Cumulative Impacts 133

13 Conclusions 134

14 References 136

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Tables

Table 2.1 State and Commonwealth conservation status of significant species that might occur in the Fitzroy Basin. 8

Table 3.1 Location of sites. 27

Table 3.2 Habitat bioassessment scores used to derive overall condition categories. 30

Table 3.3 Water quality objectives for water quality parameters measured in situ. 31

Table 3.4 Growth habits of aquatic plants in standing or flowing water. 33

Table 3.5 WQOs for the Callide Creek Catchment, in edge and composite (pool, run and / or riffle) habitat for slightly to moderately disturbed streams. 36

Table 3.6 Electrofishing and net efforts at each site in the post-wet season survey. 41

Table 3.7 Electrofishing and net efforts at each site in the pre-wet season survey. 41

Table 4.1 Aquatic habitat at each site in both surveys. 47

Table 5.1 Mean percent cover and species richness of aquatic plants at each site in the post-wet season survey. 68

Table 5.2 Mean percent cover and species richness of aquatic plants at each site in the pre-wet season survey. 70

Table 6.1 Abundance of macrocrustaceans at each site in the post-wet season survey. 85

Table 6.2 Abundance of macrocrustaceans at each site in the pre-wet season survey. 85

Table 7.1 Fish species caught in the Fitzroy Basin, in previous surveys and in the current seasonal surveys. 87

Table 7.2 Fish species richness and abundance at each site in post-wet season survey. 96

Table 7.3 Fish species richness and abundance at each site in pre-wet season survey. 97

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Table 7.4 Fish species recorded in the current seasonal surveys and the range of water quality conditions in which they are known to occur. 101

Table 9.1 Summary of potential impacts and proposed mitigation measures. 107

Table 11.1 Value criteria for aquatic ecology attributes. 125

Table 11.2 Thresholds for magnitude of impact for aquatic ecology receptors. 126

Table 11.3 Matrix used to estimate the significance of potential impacts after mitigation. 127

Table 11.4 Summary of the potential impacts of the Boundary Hill Expansion on aquatic ecology, the relevant mitigation and management measures and the residual risk. 129

Figures

Figure 3.1 Total monthly rainfall for 2011-2012 and long term mean monthly rainfall at the Thangool Airport weather station. 26

Figure 3.2 Quadrant diagram for SIGNAL 2 / Family Bi-plot. 39

Figure 4.1 Habitat bioassessment scores at each site in each survey. 46

Figure 4.2 Reach environ at site CBC-ML dominated by grasses and bare ground in the pre-wet season survey. 54

Figure 4.3 Grasses, eucalypt trees and bare ground at site CC-WE in the post-wet season survey. 55

Figure 4.4 Grasses and eucalypt trees at site CBC-DS in the post-wet season survey. 55

Figure 4.5 Eroded left bank at site CBC-DS2 in the post-wet season survey. 56

Figure 4.6 Particle size distribution at each site in the post-wet season survey (visual assessment). 57

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Figure 4.7 Particle size distribution at each site in the pre-wet season survey (visual assessment). 58

Figure 4.8 Bedrock substrate at site CBC-US in pre-wet season survey. 58

Figure 4.9 Water temperature at each site in both surveys. 60

Figure 4.10 The pH at each site in both surveys, and the Fitzroy Basin WQO range for Callide Creek. 61

Figure 4.11 Electrical conductivity at each site in both survey, and the Fitzroy Basin WQO for Callide Creek. 62

Figure 4.12 Turbidity at each site in both surveys, and the Fitzroy Basin WQO for Callide Creek. 63

Figure 4.13 Percent saturation of dissolved oxygen at each site in both surveys, and the Fitzroy Basin WQO range for Callide Creek. 65

Figure 5.1 Common rush at site CBC-ML in the post-wet season survey. 71

Figure 5.2 Water primrose at site CC-WE in the pre-wet season survey. 71

Figure 6.1 Abundance of macroinvertebrates in bed habitat at each site in both surveys, and at a DNRM reference site. 74

Figure 6.2 Abundance of macroinvertebrates in edge habitat at each site in both surveys, and at DNRM reference sites. 75

Figure 6.3 Taxonomic richness of macroinvertebrates in bed habitat at each site in both surveys, and at the DNRM reference site. 76

Figure 6.4 Taxonomic richness of macroinvertebrates in edge habitat at each site in both surveys, and at DNRM reference sites. 77

Figure 6.5 PET richness of macroinvertebrates in bed habitat at each site in both surveys, and at a DNRM reference site. 78

Figure 6.6 PET richness of macroinvertebrates in edge habitat at each site in both surveys, and at DNRM reference sites. 79

Figure 6.7 SIGNAL 2 scores of macroinvertebrates in bed habitat at each site in both surveys, and at DNRM reference site. 80

Figure 6.8 SIGNAL 2 scores of macroinvertebrates in edge habitat at each site in both surveys and at DNRM reference sites. 81

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Figure 6.9 SIGNAL 2 / family bi-plot for macroinvertebrate communities in bed habitat at all sites in both surveys, and at DNRM reference site. 82

Figure 6.10 SIGNAL 2 / family bi-plot for macroinvertebrate communities in edge habitat at all sites in both surveys, and at DNRM reference site. 83

Figure 6.11 Freshwater prawn, caught at three sites in the post-wet season survey. 84

Figure 6.12 Common yabby, caught at site CBC-DS1 in post-wet survey. 84

Figure 7.1 Eastern rainbowfish, caught at site CC-WE in the post-wet season survey. 93

Figure 7.2 Common carp gudgeon, caught at site CBC-DS2 in the pre-wet season survey. 94

Figure 7.3 Agassiz’s glassfish, caught at site CC-WE in the pre-wet season survey. 94

Figure 7.4 Spangled perch, caught at site CBC-DS1 in the post-wet season survey. 94

Figure 7.5 Mosquitofish, caught at site CC-DS1 in the post-wet season survey. 95

Figure 7.6 Life-history stage abundance of fish at each site in the post-wet season survey. 98

Figure 7.7 Life-history stage abundance of fish at each site in the pre-wet survey. 99

Maps

111103CM Location of the Boundary Hill South 4

111103WLb Location of Great Barrier Reef World Heritage Area in relation to the project area 7

111103HEV Location of High Ecological Value areas 12

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111103WMA Location of Wetland Management areas 21

111103WPA Location of Wetland Protection Areas 22

111103WL Location of EHP mapped wetlands 24

111103SM Aquatic Ecology Sampling Locations 28

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Boundary Hill Expansion EIS: Aquatic Ecology i

Summary

This report has been prepared for AECOM, on behalf of Anglo American (Coal Management) Pty Ltd. It provides information on aquatic ecology for the Environmental Impact Statement (EIS) for the Boundary Hill South (BHS) project. The scope of this survey includes an assessment of aquatic habitat, aquatic plant and animal distribution and the likely impacts to these values within the BHS project area. The BHS project area refers to the area covered by Mining Lease Application (MLA) 80186. The survey area for this assessment includes Callide Creek and associated tributaries and wetlands, upstream of, within and downstream of the BHS project area. These waterways are within the Dawson River subcatchment of the Fitzroy Basin. Measures to minimise and mitigate the potential impacts to aquatic ecology are outlined.

Existing Environment

The aquatic habitat, plants and animals of the survey area were assessed in the pre-wet and post-wet seasons. Based on these assessments, each site that held water was given a River Bioassessment Program habitat condition score. Aquatic plants, macroinvertebrates, fish and turtles were surveyed using standard techniques, where suitable habitat existed. Aquatic plants and animal communities of the region were also described, to provide regional context for the results of the current seasonal surveys, and to determine the biological values of the waterways potentially affected by the BHS project.

The biological values of the aquatic ecosystems within the survey area were moderate and were consistent with those of the wider catchment. Environmental Values (EVs) are influenced primarily by the ephemeral and intermittent nature of the region’s waterways; although agricultural development can also influence the water quality and physical characteristics of aquatic habitats. Creeks and tributaries in the catchment were generally in moderate to good habitat condition and were characterised by:

⋅ low habitat diversity

⋅ moderately unstable banks

⋅ low vegetation cover, and

⋅ high deposition of fine sediment.

Water quality measured in situ, where available, was moderate during the surveys with low pH and percent saturation of dissolved oxygen. Biodiversity was relatively low, with a low percent cover of aquatic plants and low species richness. Fish and macroinvertebrate

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Boundary Hill Expansion EIS: Aquatic Ecology ii

species that are tolerant of varying and often harsh conditions were caught in the survey area. However, the fish communities within the BHS project area were likely to contribute to the success of downstream populations, through movement or migration.

No listed species of aquatic plants or animals, under state or Commonwealth legislation, were recorded or were likely to occur in the waterways of the BHS project area. Site CC-WE was classified as a wetland management area that might be impacted by the BHS project.

Potential Impacts and Mitigation Measures

Construction and mining activities that have the potential to impact on aquatic ecology include the:

⋅ operation and maintenance of vehicles and equipment

⋅ vegetation clearing and earthworks

⋅ management of water resources

⋅ loss of catchment area

⋅ loss of on-site wetlands

⋅ creek diversions

⋅ changes to flow regimes, and

⋅ construction of creek crossings, including haul roads.

The BHS project is likely to result in a localised loss of aquatic habitat, plants and animals during construction and operation, which is most likely to occur as a result of the:

⋅ unplanned discharge of mine-affected water

⋅ loss of catchment area

⋅ potential diversion of a creek channel, and

⋅ construction of creek crossings.

However, these impacts are not predicted to have regional significance given the number of waterways and wetlands in the catchment. These impacts will be minimised as far as practical by the implementation of appropriate mitigation measures and the development of an Environmental Management Plan and Plan of Operations. However, further

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Boundary Hill Expansion EIS: Aquatic Ecology iii

monitoring may be required to determine the impact of the BHS project on aquatic ecology, in order to advise of adaptive management for the BHS project.

The BHS project is not likely to impact upon habitats of conservational significance, on listed vulnerable or endangered species or on Matters of National Environmental Significance, with respect to aquatic ecology.

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Boundary Hill Expansion EIS: Aquatic Ecology 1

1 Introduction

1.1 Project Background

Anglo American’s Anglo Coal (Callide Management) Pty Ltd currently operates the Callide Mine in central Queensland, which consists of four existing pits:

⋅ Dunn Creek

⋅ The Hut

⋅ Trap Gully, and

⋅ Boundary Hill.

Coal production from Callide Mine is approximately 10 million tonnes per annum with most of the coal being used by the Callide Power Station. The existing Boundary Hill pit has a limited life span, with resources expected to be exhausted by 2014. Anglo Coal (Callide Management) Pty Ltd is preparing to expand operations at the Boundary Hill pit through the Boundary Hill South (BHS) project, which is immediately to the south of the existing Boundary Hill pit. The BHS project covers approximately 1069 ha, of which approximately 317 ha would be subject to disturbance associated with mining operations, and is in MLA 80186, which would be amended to represent the updated mine lease boundary.

The current Boundary Hill pit is mined using open-cut mining techniques with overburden removed by a dragline supported by a hydraulic excavator and truck pre-strip fleet. Coal is either stockpiled in-pit or crushed and screened at the Boundary Hill Coal Handling Plant area. Crushed coal is then conveyed to a screening and secondary crusher, and sold as an unwashed product, with no tailings generated. This process would be used for the operation of the BHS project using existing infrastructure with minimal change. Activities associated with the BHS would include:

⋅ development of open-cut operations in the extended area

⋅ construction of a haul road north from the extended open-cut pit

⋅ construction of a new overburden dump area to the west of the pit

⋅

Anglo Coal (Callide Management) Pty Ltd engaged AECOM to prepare the Environmental Impact Statement (EIS). frc environmental were subsequently engaged by AECOM to

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complete an aquatic ecology assessment for the EIS. The aims of the aquatic ecology assessment were to:

⋅ provide a detailed description of the aquatic ecological values of the survey area, with consideration to both state and federal requirements

⋅ assess the potential impacts to aquatic ecology associated with the mine expansion, and

⋅ inform the assessment of the appropriate mitigation measures to use during construction and operation.

1.2 Description of the Survey Area

The BHS project is located in central Queensland, approximately 20 km north-east of Biloela and 85 km south-west of Gladstone (Map 111103CM). The BHS project area sits over the Callide Basin Coal Measures, as mapped by the Department of Environment and Heritage Protection (EHP) and is in the Callide Creek subcatchment within the Fitzroy Basin. Within the BHS project area are a number of small, ephemeral creeks. These creeks flow into Callide Creek, which then flows north for approximately 40 km into the Don River, which then flows west approximately 60 km into the Dawson River. The Dawson River is one of the major tributaries of the Fitzroy River, which discharges into the Coral Sea south-east of Rockhampton.

The survey area for this assessment included the waterways within and downstream of the BHS project area, extending approximately 13 km to Callide Creek near Jambin. As specified in the terms of reference, the BHS project area is located immediately south of the existing Boundary Hill mine pit, and covers the following allotments

⋅ part Lot 1 SP231268;

⋅ part Lot 94 RN1524;

⋅ Lot 134 RN417;

⋅ Lot 1 SP231268;

⋅ part Lot 170 FTY1843;

⋅ part Lot TR170 FTY1843 – Timber Reserve; and

⋅ Lot 122 SP108702.

The BHS project area comprises approximately 1069 hectares (ha), with approximately 317 ha subject to disturbance associated with the mining operations, including pits and

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spoil dumps. The project area is currently subject to mine lease application 80121, which has been amended to represent the updated project mine lease boundary.

Stream flows in the region are highly variable and most waterways are ephemeral, with channels drying out for long periods and aquatic animals becoming concentrated in the evaporating pools. As a consequence, habitat, water quality and the composition of animal communities are highly variable over time.

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2 Legal Framework

2.1

Any actions that are likely to have a significant impact on a matter of national environmental significance are subject to assessment under the Commonwealth’s Environment Protection and Biodiversity Conservation Act 1999 1 (EPBC Act) approval process. Matters of national environmental significance include:

⋅ world heritage properties

⋅ national heritage places

⋅ wetlands of international importance

⋅ threatened species and ecological communities

⋅ migratory species

⋅ Commonwealth marine areas

⋅ Great Barrier Reef Marine Park, and

⋅ nuclear actions (including uranium mines).

World Heritage Properties

Properties that have been inscribed on the World Heritage list are automatically declared world heritage properties and are protected under the EPBC Act. There are currently 18 world heritage properties in Australia. The EPBC Act regulates actions that will, or are likely to, have a significant impact on the world heritage values of a world heritage property. This includes relevant actions that occur outside the boundaries of a World Heritage Area. Impacts to world heritage properties may either be direct impacts, or indirect impacts due to activities upstream.

The Fitzroy Basin drains to the Great Barrier Reef World Heritage Area (GBRWHA) and Great Barrier Reef Marine Park (GBRMP), which support extensive mangrove, saltmarsh,

1 Act no. 91 of 1999 as amended, prepared on 19 February 2012 taking into account amendments up to Act No. 46 of 2011. Prepared by the Office of Legislative Drafting and Publishing, Attorney General’s Department, Canberra.

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seagrass, algal, and coral communities, approximately 300 km downstream from the BHS project. Given this distance, the BHS project is unlikely to have an impact on these world heritage properties where the appropriate mitigation measures are in place to protect downstream water quality and flows.

National Heritage Places

National heritage places include natural, historic and Indigenous places of outstanding heritage and value. There are currently 107 sites listed on the register of national heritage places, which include the world heritage properties.

There are no national heritage places that relate to aquatic ecology within the BHS project area. The only national heritage place in the vicinity of the proposed BHS project is the Great Barrier Reef, which is over 300 km downstream of the BHS project area (Map 111103WLb).

Wetlands of International Importance (Ramsar Wetlands)

The EPBC Act regulates actions that will, or are likely to, have a significant impact on the ecological character of a Ramsar wetland (wetlands of international significance). This includes relevant actions that occur outside the boundaries of a Ramsar wetland. There are no Ramsar wetlands in the BHS project area. The Shoalwater and Corio Bays Ramsar area is located approximately 70 km north of where the Fitzroy River drains into the ocean. The BHS project is unlikely to have an impact on these Ramsar wetlands where the appropriate mitigation measures are in place to protect downstream water quality and flows.

Threatened Species and Ecological Communities

Two threatened animal species, the Fitzroy River turtle (Rheodytes leukops) and the estuarine crocodile (Crocodylus porosus), a migratory species, may occur in the vicinity of the BHS project area (Table 2.1). The Fitzroy River turtle is listed as vulnerable under the EPBC Act and is endemic (characteristic of or restricted to a particular region) to the waterways of the Fitzroy River and its tributaries (DERM 2010). The estuarine crocodile is a migratory species that is also listed as vulnerable and is typically found in tidal reaches of rivers (including the Fitzroy River).

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There are no records of listed migratory or marine animals, such as crocodiles, dolphins, whales, dugong or marine turtles, within 20 km of the BHS project area (DERM 2012c). Populations of these animals have been recorded in the Fitzroy Estuary and / or the Great Barrier Reef, approximately 300 km downstream of the BHS project area.

Table 2.1 State and Commonwealth conservation status of significant species that might occur in the Fitzroy Basin.

Family Species Common Name NCWR EPBC Act

Chelidae Rheodytes leukops Fitzroy River turtle V V

Crocodylidae Crocodylus porosus estuarine crocodile V O, M Source (DSEWPC 2012; EHP 2012) C least concern V vulnerable O marine species M migratory species – not listed

Fitzroy River Turtle

The Fitzroy River turtle’s (Rheodytes leukops) distribution is restricted to the Fitzroy Basin; however, the closest record of Fitzroy River turtle to the BHS project area is from the Dawson River at Baralaba, approximately 84 km to the west of the BHS project area (DEWHA 2010).

Biological data on the movement patterns of the Fitzroy river turtle is largely limited to tracking studies conducted in the Fitzroy River at Glenroy Crossing (Tucker et al. 2001). Home ranges typically vary widely among individuals, however, on average, turtles were observed to have a local mean range span of 417 m (Tucker et al. 2001).

Little information is available on the abundance and life history of the Fitzroy River turtle across its greater distribution. Riffle zones are an important habitat for the Fitzroy River turtle, with the home ranges of individuals typically overlapping this habitat (Tucker et al. 2001), possibly due to increased foraging success in riffle habitats, (Legler & Cann 1980) or due to a greater efficiency of aquatic cloacal respiration in highly oxygenated waters such as riffle zones (Priest 1997; Franklin 2000; Gordos et al. 2004).

Under low-flow events, or as riffle zones become seasonally ephemeral (i.e. completely dry), the Fitzroy River turtle retreats to deeper sections of pool habitats, or even isolated waterholes, next to riffle zones (Tucker et al. 2001; Limpus et al. 2007). As riffle zones

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throughout most of the home range of the Fitzroy River turtle are likely to be ephemeral, this species should not be considered to be a riffle zone specialist; rather, the turtles exploit this habitat to forage for abundant food sources such as benthic invertebrates and algae in the wet season and early dry season (Limpus et al. 2007). This species has not been recorded in small farm dams created outside of permanent riverine habitat, or in permanent billabongs that are parallel to the main stream of a creek or river (Limpus et al. 2007).

The Fitzroy River turtle has a weakly bimodal pattern of increased surfacing activity during dawn and dusk; however, this pattern was not consistently observed among individual turtles (Gordos & Franklin 2002). There is no information available on the diurnal habitat preferences or the seasonal movement patterns of the Fitzroy River turtle.

Targeted species surveys were not undertaken as part of this assessment, as suitable habitat for the Fitzroy River turtle was not found within the survey area. Based on the known habitat preferences and distribution of this species (Limpus et al. 2007), it was considered unlikely that the Fitzroy River turtle occurs in the survey area.

Migratory Species

Estuarine crocodiles are found in the Fitzroy Basin and are classified as a migratory species under the EPBC Act. Estuarine crocodiles have been recorded in the Fitzroy River and they may be present in other perennial freshwaters of the Fitzroy Basin. Estuarine crocodiles have not been recorded within 20 km of the Project area, in addition no suitable habitat has been identified within the project area (DERM 2009b). It is unlikely that estuarine crocodiles will be in the vicinity of the project area.

Commonwealth Marine Areas

Commonwealth marine waters generally include the area from the boundary of state coastal waters (3 nautical miles) to 200 nautical miles from the coast. Commonwealth marine areas are matters of national environmental significance under the EPBC Act. Marine protected areas that are Commonwealth reserves are also protected under the EPBC Act. The BHS project is more than 300 km upstream of any Commonwealth marine areas and is highly unlikely to have an impact on these areas, where the appropriate mitigation measures are in place to protect downstream water quality and flows.

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Great Barrier Reef Marine Park

Actions that may have a significant impact on the GBRMP are regulated under the EPBC Act. The BHS project is more than 300 km upstream of the GBRMP and is highly unlikely to have an impact on the GBRMP, where the appropriate mitigation measures are in place to protect downstream water quality and flows.

Nuclear Actions

Nuclear actions are not relevant to the BHS project.

2.2 Queensland’s Environmental Protection Act 1994

The Environmental Protection Act 1994 (EP Act) 2 is the key legislation for environmental management and protection in Queensland. The EP Act establishes a general environmental duty, and a duty to notify environmental harm that applies to all persons and corporations. The EP Act provides for environmental protection policies that establish the Environmental Values (EVs) to be preserved, and that may set quality standards for segments of the environment (e.g. water, air, waste and noise). The EVs of waterways in Queensland are protected under the EP Act and the subordinate Environmental Protection (Water) Policy 2009 (EPP Water) 3.

Environmental Protection (Water) Policy 2009

The EPP Water has been established to protect Queensland waters while allowing for ecologically sustainable development. The purpose of the policy is to identify EVs for aquatic ecosystems and for human uses; and determine water quality guidelines and water quality objectives (WQOs) to protect EVs.

EVs and WQOs have been established for many waterways in Queensland under Schedule 1 of the EPP Water. The EPP Water defines an indicator for an EV as a property that can be measured or decided in a quantitative way. WQOs are numerical

2 Reprint No. 10G, Reprinted as in force on 5 April 2012. Reprint prepared by the Office of the Queensland Parliamentary Council.

3 Reprint No. 1C, Reprinted as in force on 30 September 2011. Reprint prepared by the Office of the Queensland Parliamentary Council.

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concentrations or statements for indicators that protect a stated environmental value and are generally developed based on the review of the available site-specific information relevant to each environmental value.

The EVs of waters to be enhanced or protected under the EPP Water are:

⋅ biological integrity of a modified aquatic ecosystem

⋅ suitability for recreational use

⋅ suitability for minimal treatment before supply as drinking water

⋅ suitability for agricultural use, and

⋅ suitability for industrial use.

Specific (EVs) and WQOs have been prescribed for the Fitzroy Basin (DERM 2011c). The EPP Water Dawson River Sub-basin Environmental Values and Water Quality Objectives (DERM 2011b) were used for the BHS project area.

Environmentally sensitive areas are designated under the Environmental Protection Regulation 2008. No High ecological value (HEV) aquatic ecosystems have been identified within the vicinity of the survey area (Map 111103HEV). HEV areas are to be managed with the intent of achieving an effectively unmodified waterway condition, by achieving effectively unmodified water quality (20th, 50th and 80th percentiles of HEV waters), habitat, biota, flow and riparian areas. However, these waters may not currently be in HEV condition, and could currently be in slightly disturbed condition or could be more modified waters, which can be progressively improved to achieve HEV condition.

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2.3 Queensland’s Fisheries Act 1994

All waters of the state are protected against degradation by direct or indirect impact under section 125 of the Fisheries Act 1994 (Fisheries Act) 4. If litter, soil, a noxious substance, refuse or other polluting matter is on land (including the foreshore and non-tidal land), in waters, or in a fish habitat, and it appears to the Chief Executive that the polluting matter is likely to adversely affect fisheries resources or a fish habitat, the Chief Executive of the Department of Agriculture, Fisheries and Forestry may issue a notice requiring the person suspected of causing the pollution to take action to redress the situation.

Waterway Barriers

Activities authorised by the Mineral Resources Act 1989 5 that are carried out in a relevant mining lease, are not currently subject to the provisions of Sustainable Planning Act 2009 6 (SPA). That is, activities carried out within mining leases do not currently require development permits under the SPA.

Details of requirements for the construction and raising of a waterway barrier under SPA are include here, as some activities may not be covered by the Mineral Resources Act 1989.

The construction and raising of a waterway barrier is classed as operational works under the Sustainable Planning Act 2009 7 (SPA), and therefore requires a development approval through the Integrated Development Assessment (IDAS) process. Included in the development approval process is an assessment under the Fisheries Act. Under Part 5, Division 3A, Section 76 of the Act, a waterway barrier works approval is needed to build any structure across a freshwater waterway, whether it is temporary or permanent. The purpose of this part of the Act is to provide a balance between the need to construct dams, weirs, culverts and road crossings, and the need to maintain fish movement. Waterway barriers may be required for the BHS project (e.g. construction of haul road If approval is given, the Chief Executive of Department of Agriculture,

4 Reprint No. 7 as in force on 5 May 2011. Reprint prepared by the Office of the Queensland Parliamentary Council.

5 Reprint No. 13. Reprinted as in force on 2 March 2012. Prepared by the Office of the Queensland Parliamentary Counsel.

6 Act no. 36 of 2009. Reprint as in force on 2 March 2012. Reprint No. 2 Prepared by the Office of Queensland Parliamentary Counsel.

7 Act no. 36 of 2009. Reprint as in force on 2 March 2012. Reprint No. 2 Prepared by the Office of Queensland Parliamentary Counsel.

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Fisheries and Forestry (DAFF) must be satisfied that movement of fish across the waterway barrier works will be adequately provided for, if necessary by construction of a fishway.

The construction or raising of waterway barrier works may be either assessable or self-assessable development, depending on the nature of works. This is normally determined at the detailed design phase of a project.

If the proposed waterway barrier does require a development permit, the Fisheries Queensland group within DAFF assesses whether or not an approval should be issued, and whether a fishway should be built with the structure.

To assess the requirements for a fishway on a proposed structure, the following issues are considered:

⋅ Are there fish in the waterway that need to move across the site of the waterway barrier works?

⋅ Are there habitats upstream and / or downstream of the proposed works that the fish need to move into?

⋅ What are the effects of existing barriers (natural or man-made) upstream or downstream of the site of the waterway barrier works?

⋅ Will the drown-out characteristics of the proposed waterway barrier works allow adequate fish passage? and

⋅ Can a fishway be incorporated into the proposed works?

When a fishway is required, Queensland Fisheries have developed a standard design process that ensures that both biologists and engineers are involved in developing the fishway design. Once the fishway is built, monitoring is required to confirm that the fishway is effective, or to identify any adjustments needed.

While the provision of effective fish passage may not be a mandatory requirement under current legislation, it is recommended where there would other wise be deleterious impacts on fish communities.

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Non-indigenous Fish

Under the Fisheries Regulation 2008, non-indigenous fish are fish living in an area where they are not naturally found. A non-indigenous fish can be a native Australian species or a non-native species (i.e. exotic). Some exotic non-indigenous fish from other countries can be kept without a permit as long as they cannot escape into the local waterways.

Of the species known in the Fitzroy Basin, there are three exotic non-indigenous species:

⋅ mosquitofish (Gambusia holbrooki)

⋅ goldfish (Carassius auratus), and

⋅ guppies (Poecilia reticulata).

Declared Noxious Fish

Declared noxious species are listed under the Fisheries Regulation 2008 8. Declared noxious fish cannot be kept, hatched, reared or sold, and must be destroyed if caught. They must not be returned to the water in any form, and cannot be used as bait (alive or dead). Mosquitofish are a declared noxious fish.

Declared Fish Habitat Areas

Fish habitat areas are declared under the Fisheries Act to enhance existing and future fishing activities and to protect the habitat for fish and other aquatic animals. They mainly cover inshore and estuarine habitats, as these are recognised as being highly valuable habitats for commercially and recreationally important fish and crustaceans. While normal community use and activities (including legal fishing activities) are not restricted in fish habitat areas, any works or activities that may disturb habitats within a fish habitat area, require a specific permit under the provisions of the Fisheries Act. There are no fish habitat areas in or near the BHS project area; with the Fitzroy River declared fish habitat area the closest to the BHS project area, approximately 80 km away within estuarine reaches of the Fitzroy River.

8 Reprint No. 2G, Reprinted as in force on 1 January 2010. Reprint prepared by the Office of the Queensland Parliamentary Council.

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2.4 Queensland’s Nature Conservation Act 1992

Native plant and animal species are protected in Queensland under the Nature Conservation Act 1992; extinct in the wild, endangered, vulnerable, near threatened and least concern species are listed in the Nature Conservation (Wildlife) Regulation 2006 9 (NCWR). No listed endangered, vulnerable, or near threatened aquatic species are known from the waterways of the BHS project area, although the estuarine crocodile and Fitzroy River turtle occur downstream, and are both listed as vulnerable under the NCWR.

The white-throated snapping turtle (Elseya albagula) is known to occur in the Fitzroy Basin and was only described in 2006 (Thomson et al. 2006); previously it had been regarded as a form of the more common and widely distributed northern snapping turtle (Elseya dentata). The white-throated snapping turtle is listed as ‘least concern’ under the NCWR, but has been identified as a high priority for conservation in the Department of Environment and Heritage Protection’s (EHP’s) species prioritisation framework.

White-throated Snapping Turtle

Within the greater Fitzroy, Burnett and Mary River Basins, the white-throated snapping turtle has been recorded almost exclusively in close association with permanently flowing stream reaches, typically characterised by a sand-gravel substrate with submerged rock crevices, undercut banks and / or submerged logs and fallen trees (Hamman et al. 2007). Within the Fitzroy and Mary River Basins, the white-throated snapping turtle is regularly associated with areas of high shade, including submerged logs and overhanging riparian vegetation, during the day; and shallow riffle zones at night (Hamman et al. 2007). Capture records suggest that the white-throated snapping turtle is rarely found in reaches without these habitats (Hamman et al. 2007).

Across its distribution, individuals have been recorded from both shallow flowing pools and in deeper, slow flowing pools of at least 6 m deep (Hamman et al. 2007). This species has been recorded in high densities at the Ned Churchward Weir on the Burnett River (Hamman et al. 2007) and there is a relatively large, self-sustaining population in the Fitzroy Barrage impoundment (Limpus et al. 2007). It has also been recorded from the existing Eden Bann Weir impoundment (Limpus et al. 2007). Populations of the white-throated snapping turtle tend to be close to suitable nesting habitats (frc environmental 2007; Hamman et al. 2007).

9 Reprint No. 3B.Reprinted as in force on 1 January 2012. Reprint prepared by the Office of the Queensland Parliamentary Council.

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The white-throated snapping turtle has not been recorded from man-made water bodies isolated from flowing streams (e.g. farm dams or sewage treatment plants) suggesting that it does not move long distances over dry land (Hamman et al. 2007).

As with the Fitzroy River turtle, predation of eggs is believed to be a major factor resulting in the low abundance of both juvenile and immature white-throated snapping turtles across the species’ distribution (Hamman et al. 2007). Nest predation is a major factor responsible for the low abundance of juvenile and immature turtles of a number of Australian turtles, including Krefft’s river turtles (Emydura macquarii krefftii) and snake-necked turtles (Chelodina longicollis) (Thompson 1983).

Activities within the Project area are not likely to result in a significant impact to animals listed under the NCWR, as the Project is not expected to impact on their key habitat (Section 11.1).

2.5 Queensland’s Land Protection (Pest and Stock Management) Act 2002

Declared Weeds

The Land Protection (Pest and Stock Route Management) Act 2002 (the Land Protection Act) 10 provides a framework for improved management of weeds, pest animals and the stock route network. Declared noxious weeds in Queensland are listed under the Land Protection (Pest and Stock Route Management) Regulation 200311.

Class 1 declared pests are uncommon in Queensland, and if introduced, are likely to have adverse economic, environmental or social impacts. Class 1 pests established in Queensland must be eradicated from the state.

Class 2 and 3 declared pests are established in Queensland and have, or could have, an adverse economic, environmental or social impact. Landowners must take all reasonable steps to keep their land free from Class 2 pests. Landowners are not required to remove Class 3 pests, unless their land is next to an area of environmental significance, which is not the case for the BHS project area.

10 Reprint No. 4A. Reprinted as in force on 2 March 2012. Prepared by the Office of the Queensland Parliamentary Counsel.

11 Reprint No. 5A. Reprinted as in force on 28 May 2012. Prepared by the Office of the Queensland Parliamentary Counsel.

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Weeds of National Significance

Weeds of National Significance can also be used to assess weeds; it is outside of the legislative framework but provides a useful condition assessment tool. Weeds of National Significance is an inaugural list based on the top twenty weeds as endorsed by the Agricultural and Resource Management Council of Australia and New Zealand, Australia and New Zealand Environment and Conservation Council and Forestry Ministers.

Weeds of National Significance are determined by their:

⋅ invasiveness

⋅ impacts

⋅ potential for spread, and

⋅ socio-economic and environmental values.

Hymenachne (Hymenachne amplexicaulis) is listed as a weed of national significance and occurs in the BHS project area (Australian Weeds Committee 2012). Other declared aquatic weeds such as water hyacinth (Eichhornia crassipes) and salvinia (Salvinia molesta) are also known from the Fitzroy Basin (FBA 2008). Water hyacinth and salvinia are Class 2 declared pest plants under the Land Protection Act (DAFF 2012).

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2.6 Queensland’s Water Act 2000

The purpose of the Water Act 2000 (Water Act) 12 is to provide for the sustainable management of water and other resources. The BHS project may require approvals under the Water Act for the construction, control and management of works with respect to water conservation and protection, drainage, supply, flood control and prevention. Under Section 269 of the Water Act, a riverine protection permit is required to:

⋅ remove vegetation in a watercourse, wetland or spring

⋅ excavate in a watercourse, wetland or spring, and / or

⋅ place fill in a watercourse, wetland or spring.

As such, approval may be required to construct creeks crossings (e.g. for road crossings) or for watercourse diversions.

A Water Resource Plan (WRP) and a Resource Operations Plan (ROP) have been prepared for the Fitzroy Basin in Queensland under the Water Act. The WRPs set the strategic framework for the allocation and sustainable management of water within the region. WRPs are reviewed and replaced before the end of a plan's 10-year life. The ROPs are a plan prepared under the provision of the Water Act, by the Chief Executive, to implement a WRP by defining the rules that govern the allocation and management of water in order to achieve the WRP objectives.

12 Reprint No. 8F, Reprinted as in force on 2 March 2012. Reprint prepared by the Office of the Queensland Parliamentary Council.

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2.7 Queensland’s Sustainable Planning Act 2009

Integrated Development Assessment System: Referable Wetlands

EHP has an advice agency role for wetlands under the IDAS and schedules of the Sustainable Planning Regulation 2009 13. These wetlands are identified as Wetland Protection Areas and Wetland Management Areas on maps of referable wetlands. Wetland management areas consist of wetlands of high ecological significance plus a 100 m wide trigger area.

Development triggers for wetlands, as listed in Schedule 7 of the Sustainable Planning Regulation, include:

⋅ reconfiguring a lot if:

− any part of the land is situated wholly or partly within a wetland management area, and

− the reconfiguration results in more than six lots being created, or any lot resulting from the reconfiguring is less than 5 ha.

⋅ material change of use, other than for a domestic activity, if any part of the land is situated wholly or partly within a wetland management area.

However, it should be noted that activities authorised by the Mineral Resources Act 1989 and that are carried out in a relevant mining lease are not currently subject to the provisions of SPA.

There are several wetland management areas in the survey area (Map 111103WMA); however, there are no wetland protection areas (Map 111103WPA).

13 Reprint No. 2. Reprinted as in force on 2 March 2012. Prepared by the Office of the Queensland Parliamentary Counsel.

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2.8 Wetlands of National, State or Regional Significance

Wetlands of national significance are not specifically protected under state or Commonwealth legislation; however, the Directory of Important Wetlands in Australia identifies nationally important wetlands, and provides a substantial knowledge base of what defines wetlands. A wetland is listed as a wetland of national significance if it:

⋅ is a good example of a wetland type that occurs within a biogeographic region in Australia

⋅ is a wetland that plays an important ecological or hydrological role in the natural functioning of a major wetland system or complex

⋅ is a wetland that is important as the habitat for animal taxa at a vulnerable stage in their life cycles, or provides a refuge when adverse conditions such as drought prevail

⋅ supports 1% or more of the national populations of any native plant or animal taxa

⋅ supports native plant or animal taxa or communities that are considered endangered or vulnerable at the national level, or

⋅ is of outstanding historical or cultural significance (DSEWPC 2012).

There are no wetlands of national significance within the project area. Several wetlands have been mapped within the vicinity of the survey area (Map 111103WL).

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State Planning Policy Protecting Wetlands of High Ecological Significance in Great Barrier Reef Catchments

This policy, which came into effect on 25 November 2011, provides direction on the following wetland protection issues relevant to the Sustainable Planning Act 2009:

⋅ how planning instruments can protect EVs in wetlands of high ecological significance in Great Barrier Reef catchments, and

⋅ how particular development can achieve the relevant policy outcomes for protecting wetland EVs.

The policy requires that development within Great Barrier Reef wetland protection areas, other than in an urban area, is outside of the wetland and avoids adverse effects on the wetland, and that development within an urban area is outside of the wetland of high ecological significance and avoids adverse effects on the wetland and, where adverse effects cannot be avoided, those effects are minimised and offset.

Developments that trigger development assessment for a Great Barrier Reef wetland protection area are listed in the Sustainable Planning Regulation 2009 (Schedule 3, Part 1 Table 4) and include operational works that are high-impact earthworks and material change of use, and reconfiguring a lot that involves operational works that are high-impact earthworks. Schedule 26 of the Sustainable Planning Regulation 2009 also provides the definition of high-impact earthworks and works that are excluded from the definition. Examples of high-impact earthworks are:

⋅ filling of land, including raising the level of land, by the placing of fill material

⋅ excavation of land, including excavation to create a canal, channel or water storage

⋅ construction of a levee, bund wall or diversion bank

⋅ construction or raising of a dam, weir or other barrier across a waterway, and

⋅ construction of a road, culvert or causeway.

There are several wetland protection areas within 30 km of the survey area (Map 111103WPA); however, there are none within the BHS project area.

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3 Methods

3.1 Survey Design

Survey Timing

Aquatic habitat condition, aquatic plants, aquatic macroinvertebrates and fish were surveyed in the post-wet season from 26 to 29 April 2012 and in the pre-wet season from 17 to 20 September 2012. The weather was fine to overcast during both surveys (BOM 2012).

There was 1.4 mm of rainfall between March 25 and April 18, but no rainfall in the 8 days before the post-wet survey. There was 2 mm of rain during the post-wet season survey. Rainfall was lower than average in April,2012, but was higher than average from December 2011 to March 2012. Overall, the total mean rainfall for the wet season (November to March) was 439.2 mm, which was above the average of 424.1 mm (BOM 2012).

There was no rainfall in the survey area for 21 days before the pre-wet season survey, and no rain fell during the pre-wet season survey. Rainfall was lower than average in September 2012. Overall, the total mean rainfall for the dry season (May to September) was 131.6 mm, which was below the average of 149.9 mm (Figure 3.1) (BOM 2012).

Figure 3.1 Total monthly rainfall for 2011-2012 and long-term mean monthly rainfall at the Thangool Airport weather station.

0

20

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100

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Site Details

Seasonal aquatic surveys were completed at seven sites to assess post-wet and pre-wet season aquatic ecology within, upstream and downstream of the BHS project area, including:

⋅ site CBC-US, upstream of the proposed BHS project area

⋅ site CBC-ML, in the proposed BHS project area

⋅ sites CBC-DS, CC-DS1, CC-DS2 and CBC-DS2, downstream of the proposed BHS project area, and

⋅ site CC-WE, a wetland site downstream of the proposed BHS project (Table 3.1 and Map 111103SM).

Table 3.1 Location of sites.

Site Location Easting a Northing a

Background Site

CBC-US Campbell Creek upstream of the BHS project area

249121 7320205

Potentially Impacted Sites

CBC-ML Campbell Creek in the BHS project area 247099 7318981

CBC-DS1 Campbell Creek 2.75 km downstream of the BHS project area

244843 7318118

CBC-DS2 Campbell Creek 7.05 km downstream of the BHS project area

242032 7316929

CC-DS1 Callide Creek 16.08 km downstream of the BHS project area

238832 7314740

CC-DS2 Callide Creek 16.23 km downstream of the BHS project area

236254 7317842

CC-WE Wetland on Callide Creek 21.23 km downstream of the BHS project area

239227 7314483

a site position recorded using a GPS (WGS 84, Zone 56J)

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3.2 Aquatic Habitat

Aquatic Habitat of the Region

The typical aquatic habitat of the streams and creeks in the Callide catchment were described through literature review, to provide a regional context for the condition of the waterways within the survey area.

Habitat Bioassessment Scores

Habitat bioassessment score datasheets (DNRM 2001) were used to numerically score nine criteria, which were then allocated to one of four categories (excellent, good, moderate and poor). The sum of the numerical rating from each category produced an overall habitat condition assessment score (Table 3.2).

This method is not directly applicable to ephemeral systems in Queensland; using this method, even pristine ephemeral systems are rarely classed as being in excellent condition, due to the nature of the ephemeral waterways (e.g. limited bottom substrate and available cover provided by sand). Nevertheless, it is a useful system for comparing between sites within a region. According to this system sites with scores:

⋅ >110 were considered to be in excellent condition

⋅ between 75 and 110 were considered to be in good condition

⋅ between 39 and 74 were considered to be in moderate condition, and

⋅ ≤38 were considered to be in poor condition.

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Table 3.2 Habitat bioassessment scores used to derive overall condition categories.

Habitat category Category score range

Excellent Good Moderate Poor

bottom substrate / available cover 16–20 11–15 6–10 0–5

embeddedness 16–20 11–15 6–10 0–5

velocity / depth category 16–20 11–15 6–10 0–5

channel alteration 12–15 8–11 4–7 0–3

bottom scouring & deposition 12–15 8–11 4–7 0–3

pool / riffle, run / bend ratio 12–15 8–11 4–7 0–3

bank stability 9–10 6–8 3–5 0–2

bank vegetative stability 9–10 6–8 3–5 0–2

streamside cover 9–10 6–8 3–5 0–2

Total Score for the Site 111–135 75–110 39–74 0–38

Habitat Condition

The in-stream habitat condition at each site was assessed based on the Australian River Assessment System (AUSRIVAS) protocol described in the Queensland AUSRIVAS Sampling and Processing Manual (DNRM 2001), including the following parameters:

⋅ habitat bioassessment scores

− bottom substrate or available cover

− embeddedness (when fine sand and silt cover the substrate)

− velocity or depth

− channel alteration

− bottom scouring and deposition

− pool / riffle, run / bend ratio

− bank stability, and

− bank vegetative stability and streamside cover

⋅ reach environs (land immediately next to the riparian zone)

⋅ bank erosion

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⋅ substrate composition (silt / clay, sand, pebble, cobble and boulder)

⋅ channel diversity (pool, riffle or run), and

⋅ in-stream habitat (in-stream vegetation and substrate characteristics).

Water Quality Measured In Situ

Water quality was measured in situ at each site, where water was present. A Hydrolab QUANTA multi-parameter water quality probe was used to measure:

⋅ water temperature

⋅ pH

⋅ electrical conductivity, and

⋅ dissolved oxygen.

Turbidity was measured in situ at all sites using a HACH 2100Q portable turbidity meter.

The Hydrolab QUANTA meter was calibrated daily and the HACH 2100Q was calibrated at the beginning and end of the surveys.

Results were compared to the Environmental Protection (Water) Policy 2009 Callide Creek Catchment Environmental Values and Water Quality Objectives for moderately disturbed aquatic ecosystems (WQO) to protect aquatic ecosystems (Table 3.3) (DERM 2011b; a).

Table 3.3 Water quality objectives for water quality parameters measured in situ.

Parameter Units Water Quality Objective

dissolved oxygen a % saturation 85–110

pH b pH units 6.5–8.5

electrical conductivity b µS/cm Low flow: 600

High flow: 1150

turbidity a NTU 50 a values for these indicators are based on the QWQG Central Coast regional water quality guidelines b values for these indicators are based on sub-regional low-flow water quality guidelines derived as part of

the process to establish EVs and WQOs in the Fitzroy Basin

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3.3 Aquatic Plants

Aquatic Plants of the Region

The aquatic plants of the region were described through literature review, to provide a regional context for the condition of the creeks within the survey area. Listed species were determined from those listed under the EPBC Act or NCWR.

Aquatic Plant Survey

Background

Aquatic plants are valuable components of the ecosystem as they:

⋅ are primary producers, providing food for other organisms

⋅ oxygenate the water and sediment

⋅ provide habitat for freshwater fauna, including fish and macroinvertebrates

⋅ can help regulate water flow, and

⋅ can stabilise riverbanks and streams.

The distribution and abundance of each species of aquatic plant reflects the ecological condition of the site. For example a high concentration of phytoplankton (algae in the water column) is indicative of high nutrient content, and a high abundance of exotic weeds is indicative of disturbance to the area. Low abundance or species richness may indicate the site is infrequently inundated, while the presence of submerged attached species indicates that a site is likely to be commonly inundated.

Some aquatic plants that require permanent standing or flowing water are species of conservation significance, such as artesian milfoil (Myriophyllum artesium), and could be indicators of an impact.

Aquatic Plants in Standing or Flowing Water

Aquatic plants in standing or flowing water include algae, ferns and flowering plants. Algae are simple plants without true roots, leaves or flowers. They include microscopic single celled plants and larger multi-celled plants that have stem-like and leaf-like structures such as Chara. Ferns are vascular plants that reproduce by spores, aquatic

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ferns include species such as Azolla and Nardoo (Marsilea drummondii). Flowering plants include monocotyledons (grasses and grass-like plants with one cotyledon) and dicotyledons (herbaceous and woody plants with two cotyledons).

Aquatic plants in standing or flowing water are grouped into four broad classes of growth habit (Table 3.4). The presence of abundant and / or diverse aquatic plant communities containing species from these various classes indicates that permanent (or near-permanent) water is likely at the site.

Some species can grow in one or more of these growth habits, for example water fern (Ceratopteris thalictroides) can be free floating or submerged. Some species require temporary periods of drying to reproduce, and some species such as spike rushes (Juncus sp., Eleocharis sp.) and spiny mudgrass (Pseudoraphis spinescens) that grow as emergents in in standing or flowing water are also common in drier areas adjacent to water (e.g. stream banks or dry stream beds).

Table 3.4 Growth habits of aquatic plants in standing or flowing water.

Class of Aquatic Plant Description

Submerged Submerged aquatic plants are rooted in the bed of the stream or wetland, with leaves totally covered by water most of the time. Some species may have underwater flowers, whereas other species may require water levels to decrease to trigger flowering and have flowers above the water level. Examples of submerged aquatic plants include milfoils (Myriophyllum spp.), ribbon weed (Vallisneria sp.), ottelia (Ottelia alismoides), pondweeds (Potamogeton spp.) and hornworts (Ceratophyllum spp.).

Attached floating Attached floating aquatic plants are rooted in the bed of the stream or wetland, with leaves typically floating on top of the water. Flowers are usually above the water. Examples of attached floating aquatic plants include water lilies (Nymphaea spp., Nelumbo sp., Ottelia ovalifolia), frogbit (Hydrocharis dubia), Triglochin spp., and floating heart (Nymphoides spp.).

Free floating Free-floating plants float on top of the water, or in the water column, with roots trailing into the water column. Flowers are typically above the water. Examples of free-floating aquatic plants include Azolla spp., thin duckweed (Spirodela punctate) and tiny duckweed (Wolffia angusta). Several declared weeds are free floating species, including Salvinia molesta and water hyacinth (Eichhornia crassipes).

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Class of Aquatic Plant Description

Emergent Emergent plants are rooted in the bed of the stream or wetland, with leaves and flowers above the water. Examples of emergent aquatic plants include spike rushes (Juncus spp.), Eleocharis spp., sedges (Cyperus spp.), bulrush (Typha spp.), Persicaria spp., frogsmouth (Philydrum lanuginosum), Monochoria cyanea, water primrose (Ludwigia spp.). Emergent weed species including Hymenachne acutigluma and para grass (Brachiaria mutica).

Other Aquatic Plants

Aquatic plants are also commonly found in areas adjacent to standing or flowing water, or in areas that are currently dry but have recently contained water. This includes plants in the ground stratum such as grasses (e.g. swamp rice grass, Leersia hexandra), grass-like plants (Cyperus spp., Juncus spp. and Eleocharis spp.), and herbaceous species (e.g. Persicaria spp., Marsilea spp.).

Survey Methods

Aquatic plants were surveyed using methods similar to those outlined in the River and Riparian Land Management Technical Guideline (Dixon et al. 2006). Aquatic plants in the river channel at each site were assessed along a single 100 x 10 m belt transect that extended along one bank and included both the banks and the adjacent channel bed (i.e. from 1 m in-stream to 9 m up the channel bank). The transect includes submerged areas, the wetted edge and a section of the dry bank. At each site, aquatic plants were identified, and the following recorded:

⋅ species richness

⋅ growth form of each species (submerged, free-floating, attached-floating or emergent)

⋅ total percent cover (% of substrate [bed / bank] covered by each species), and

⋅ whether the plant was native or exotic to Australia.

Aquatic plant species were identified in the field, where practical. Representative specimens were collected for identification in the frc environmental laboratory or by the Queensland Herbarium, if required.

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The Census of Queensland Flora 2010 (Queensland Herbarium 2010) was used to classify aquatic vegetation as native or exotic.

3.4 Aquatic Macroinvertebrates

Aquatic Macroinvertebrate Communities of the Region

The macroinvertebrate communities of the region were described through literature review. Between 1997 and 2001, the Department of Natural Resources and Mines (DNRM) undertook macroinvertebrate surveys in the region at the following DNRM sites:

⋅ 1303010 (Bell Creek at upstream railway crossing)

⋅ 130347A (Callide Creek at Callide dam inflow), and

⋅ 130306B (Don River at Rannes).

In the DNRM surveys, the following habitats were surveyed for macroinvertebrates:

⋅ edge

⋅ sandy bed

⋅ rocky bed

⋅ riffle, and

⋅ aquatic plants.

By comparison, only edge and bed (mostly sandy or silty bed) habitats were surveyed in the current surveys.

In order to use the macroinvertebrate communities as an indicator of the likely health or condition at the sites sampled by DNRM, taxonomic richness, PET richness and SIGNAL 2 scores were calculated. The mean values at each DNRM site were compared to the macroinvertebrate communities at the sites in the current surveys. SIGNAL 2 / family bi-plots were completed for communities in edge habitat, to provide a comparison for the results of the current surveys.

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Sample Collection

At each site, one macroinvertebrate sample was collected from bed (pool) habitat and one macroinvertebrate sample was collected from edge habitat; riffle habitats were not present. Sampling methods followed the procedures in the Queensland AUSRIVAS sampling manual (DNRM 2001). A standard triangular-framed, macroinvertebrate sampling net with 250 µm mesh was used to collect the samples. A 10 m long section of stream bed or edge habitat was disturbed, and a sample collected by sweeping the net through the disturbed area.

All samples were preserved and returned to frc environmental’s Brisbane laboratory, where they were sorted, counted and identified to the lowest practical taxonomic level (in most instances family), to comply with AUSRIVAS standards and those described by Chessman (2003).

Macrocrustaceans (e.g. river prawns, glass shrimps and yabbies) were also caught in the fish surveys, using a combination of electrofishing and bait trapping. All macrocrustaceans were identified and counted in the field and specimens were returned to the environment. A detailed description of fish survey methods is provided in section 3.5.

Data Analysis

Calculation of Indices

Taxonomic richness, abundance, PET richness and SIGNAL 2 scores were calculated for each sample. These indices were used to indicate the current ecological health of surveyed waterways.

Table 3.5 WQOs for the Callide Creek Catchment, in edge and composite (pool, run and / or riffle) habitat for slightly to moderately disturbed streams.

Indicator Guideline (Edge

Habitat) Guideline (Composite

Habitat)

Richness (> or = the number) 23 – 33 12 – 21

PET taxa (> or = the number) 2 – 5 2 – 5

SIGNAL 2 Score (> or = the number)

3.31 – 4.20 3.33 – 3.85

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Taxonomic Richness

Taxonomic richness is the number of taxa (in this assessment, families) in a sample. Taxonomic richness is a basic, unambiguous and effective diversity measure. However, it is affected by arbitrary choice of sample size. Where all samples are of equal size, taxonomic richness is a useful tool when used in conjunction with other indices. Richness does not take into account the relative abundance of each taxon, so rare and common taxa are given equal weighting.

Abundance

Abundance is the total number of macroinvertebrates sampled.

PET Richness

Plecoptera (stoneflies), Ephemeroptera (mayflies), and Trichoptera (caddisflies) are referred to as PET taxa, and they are particularly sensitive to disturbance such as water quality or environmental degradation. While some groups of macroinvertebrates are tolerant to water degradation (e.g. pollution) and / or environmental degradation (e.g. loss of habitat associated with sedimentation), others are sensitive to these stressors (Chessman 2003). The numbers of PET families typically increase in sites with good habitat and water quality. PET taxa are often the first to disappear when water quality or environmental degradation occurs (EHMP 2007). The lower the PET score, the greater the inferred degradation. However, Plecoptera are unlikely to occur within the survey area, as they prefer cool, clear, fast-flowing streams with a high percent saturation of dissolved oxygen.

SIGNAL 2 Scores

SIGNAL 2 (Stream Invertebrate Grade Number — Average Level [version 2]) scores are based on the sensitivity of each macroinvertebrate family to pollution or habitat degradation. Each macroinvertebrate family has been assigned a grade number between one and ten based on their sensitivity to various pollutants. A low number means that the macroinvertebrate is tolerant of a range of environmental conditions, including common forms of water pollution (e.g. suspended sediments and nutrient enrichment).

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SIGNAL 2 scores are weighted for abundance. The scores take the relative abundance of tolerant or sensitive taxa into account (instead of only the presence or absence of these taxa). The overall SIGNAL 2 score for a site is based on:

⋅ the total of the SIGNAL grade

⋅ multiplied by the weight factor for each taxon, and

⋅ divided by the total of the weight factors for each taxon.

SIGNAL 2 scores are interpreted in conjunction with the number of families found in the sample. This is achieved using a SIGNAL 2 / family bi-plot (Chessman 2003). The plots are divided into quadrants, with each quadrant indicative of particular conditions (Figure 3.2). Quadrant boundaries for the SIGNAL 2 / Family Bi-plot used for this study are based on the lower QWQG value for richness and SIGNAL scores. This technique would require considerable sampling (in effect calibration) within the region. Interpretation of the bi-plot with regard to quadrant boundaries should therefore be approached with caution. Wetlands will have naturally lower scores than streams in the same region. This is due to the macroinvertebrate orders with the highest SIGNAL 2 sensitivity grades being naturally rare in wetlands.

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Figure 3.2 Quadrant diagram for SIGNAL 2 / Family Bi-plot.

3.5 Aquatic Vertebrates

Aquatic Vertebrates of the Region

The aquatic vertebrate communities of the region were described through literature review. Sources included, but were not limited to, the Commonwealth’s Department of Sustainability, Environment, Water, Population and Communities (DESEWPC) online Environment Protection and Biodiversity Conservation Act Protected Matters Search Tool and EHP’s Wildlife Online database.

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Fish Communities

Fish communities were surveyed using a combination of electrofishing and baited traps, where water levels were suitable (Table 3.6 and Table 3.7). All available habitats (e.g. pool, riffle, run and bend) were fished at each site. Electrofishing was conducted using a Smith-Root LR-24 backpack electrofisher in shallow water in accordance with the Australian Code of Electrofishing Practice 1997. Where there was sufficient water, five small (2 mm mesh size) baited traps were set at each site for a minimum of two hours.

To avoid the re-capture of fish, all caught fish were kept in an aerated nally bin filled with water, on the shore, until the last trap was retrieved.

The life-history stage, abundance and apparent health of every fish caught were recorded and fish were returned to the water. Specimens that were unable to be identified in the field were euthanised and returned to the laboratory for identification. The sampling of fishes was conducted under General Fisheries Permit No. 153223 and Animal Ethics Approval No. CA 2012/02/593 issued to frc environmental.

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Table 3.6 Electrofishing and net efforts at each site in the post-wet season survey.

Site Method Habitat Date Time

In Time Out

Settings Effort

CBC-DS2 backpack electrofishing

pool 2012-04-27 1555 1615 95 V

30 Hz

12%

143 sa

small bait traps (5)

pool 2012-04-27 1515 0830 – 17.25 h

CC-DS1 backpack electrofishing

pool 2012-04-28 1130 1205 115 V

30 Hz

12%

477 sa


pool 2012-04-28 1240 1640 – 4 h

CC-WE backpack electrofishing

pool 2012-04-28 1500 1530 110 V

30 Hz

12%

525 s

a Lack of suitable habitat to sample prevented the full time being reached

Table 3.7 Electrofishing and net efforts at each site in the pre-wet season survey.

Site Method Habitat Date Time

In Time Out Settings Effort

CBC-DS2 small bait traps (2)

pool 2012-09-18 0900 1400 – 10 h

CC-WE backpack electrofishing

pool 2012-09-18 1500 1530 110 V

30 Hz

12%

525 s


pool 2012-09-18 1040 1240 – 10 h

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Data Analysis

Fish communities at each site were assessed for the:

⋅ species richness (the number of species caught at a site)

⋅ total abundance (total number of individuals caught at a site)

⋅ abundance of each life-history stage (total number of adult, intermediate and juvenile fish caught at each site)

⋅ abundance of exotic species (species listed under the Fisheries Regulation 2008), and

⋅ abundance of listed species.

Listed species were determined from those listed under the EPBC Act or the NCWR.

Turtles

There was no suitable habitat to allow for turtle surveys at any sites in either survey (i.e. water level at sites were either too shallow or dry).

Other Aquatic Vertebrates

Aquatic vertebrates (other than fish and turtles) observed in this survey were recorded.

3.6 Limitations

Due to the time constraints of the BHS project, it was not possible to collect multiple seasonal data; so only a single, post-wet season survey and a pre-wet season survey were completed. Also, due to the nature of ephemeral streams, some sites were dry and could not be surveyed.

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4 Aquatic Habitat

4.1 Aquatic Habitat of the Region

The Fitzroy Basin is generally used for agriculture, industry, mining and urban development. The Fitzroy Basin discharges into Keppel Bay, which forms part of the Great Barrier Reef. Flows within the basin are essential for a number of receiving environments including flow-dependent ecosystems, such as palustrine and lacustrine wetlands. The current survey area lies within the Callide Creek catchment within the Dawson River subcatchment.

The Fitzroy Basin covers an area of approximately 93 000 km2, with a human population of 7 000 (TRACK 2012). Previous studies found the overall condition of most streams in the Don / Callide Tributaries of the Dawson River to be moderate (Telfer 1995; Van Manen 2005). These studies found that aquatic habitat scores ranged from moderate to poor; with very low channel diversity and pools and runs the most common habitat type. Bed substrate ranged from boulders to sand and / or silt. The riparian zone was dominated by eucalypt communities and was found to be in a very poor condition (narrow zones with a high percentage of exotic species). Riverbanks were moderately stable to very stable, with erosion, stream flow and uncontrolled stock access contributing to poor bank stability. Reach environs were found to be in moderate condition and the dominant land use in the area was grazing, predominantly on thinned and cleared native vegetation. Channels were moderately to very highly disturbed by bridges and culverts, grazing and roads. Little in-stream aquatic vegetation was identified, due to high turbidity in the watercourse or dry channels. The ephemeral nature of the region means that the availability of aquatic habitat is seasonal and is limited to periods following rainfall, or to isolated perennial pools.

Habitat Condition

The aquatic habitat condition of the Dawson subcatchment is considered to be poor to moderate; however, upper sections and tributaries are considered to be good, including Callide Creek (Telfer 1995). Aquatic habitat is dominated by woody debris and detritus and moderate flows are necessary for adequate fish passage (Telfer 1995). The aquatic habitat condition of sites within the BHS project area was considered to be moderate, with low streamside cover and little habitat diversity.

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Reach Environs

In the State of the Rivers survey, the condition of the reach environs vary across the Dawson River subcatchment, although most stream segments are in moderate condition, as were most sites in the current survey. Stream segments with very poor or poor condition are mainly in the western, southern and northern-upland tributaries, and in the Don and Callide tributaries of the Dawson River. Stream segments with good to very good scores are mostly in the upper and regulated Dawson River subcatchments. Factors that impact the condition of the reach environs include the extent of vegetation clearing along the stream for cropping and exposure to cattle grazing and watering (Telfer 1995). Clearing riparian vegetation allows unfiltered sediment and run off into waterways; cattle trample banks while grazing and watering, increasing turbidity in the aquatic ecosystem.

Riparian Vegetation

Riparian zones within the Fitzroy Basin are generally cleared or consist of thin or altered remnant vegetation structure and composition. The highest proportion of exotic species occurs in sections of the Don and Callide subcatchments, which is due to the extensive cleared land associated with grazing and cropping (Telfer 1995).

Bank Stability

In the State of the Rivers survey, the stability of the banks throughout the catchment is generally good, with most banks being stable or very stable. Erosion is the most extensive process occurring throughout the catchment, and is the dominant process in 94% of stream segments. Erosion commonly occurs at bends, at obstacles, and at irregular locations along the lower and upper banks. The presence of stock and clearing of vegetation are the major factors contributing to the disturbance of banks (Telfer 1995), including at many sites in the current survey.

Substrate Composition

Substrates in the Fitzroy Basin comprise all forms, from silt / clay to bedrock but is dominated by pebble, gravel, sand and silt / clay (SKM 2010), similar to the substrate at sites in the current survey.

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Channel Diversity

In the State of the Rivers survey, channel diversity throughout the catchment is mostly low to very low. Generally, channel diversity is highest in the northern-upland tributary and in the Don and Callide subcatchments. Run habitat is the most commonly identified channel habitat type throughout the catchment, followed by pools and then riffles (Telfer 1995).

In-stream Habitat

In the State of the Rivers survey, the condition of in-stream habitat is considered to be generally poor to moderate. Similarly, the overall habitat value for aquatic life is rated at most sites (71%) as very poor to good, similar to the in-stream habitat at most sites in the current survey. Subcatchments that exhibit aquatic habitat in mostly good to very good condition include the upper tributaries subcatchment and the upper Dawson River subcatchment. Individual branches, individual logs, and leaf and twig cover is the most common in-stream habitat. Vegetative debris is the predominant aquatic habitat in this catchment, which highlights the importance of riparian zones to aquatic organisms in the Dawson River subcatchment (Telfer 1995).

4.2 Aquatic Habitat of the Survey Area

Habitat Bioassessment Scores

In the post-wet season survey, the habitat condition was moderate at most sites, except at site CBC-US, which had a good habitat condition (Figure 4.1). The lowest score was at site CBC-DS, though it still had a moderate habitat condition. This lower score was because the site had:

⋅ a road clearing at the edge of the reach

⋅ stock access, and

⋅ a substrate dominated by sand.

The relatively good habitat condition at site CBC-US was primarily due to:

⋅ little fine sediment in the substrate (i.e. a good embeddedness score)

⋅ more available cover and habitat (associated with a good embeddedness score), and

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⋅ less channel alteration, bottom scouring and deposition (due to lower rainfall and slower water flows).

In the pre-wet season survey, only sites that had water were given a bioassessment score. The habitat condition at sites CBC-DS2 and CC-WE was similar to the post-wet season survey, and was considered to be in moderate condition (Figure 4.1). This was primarily due to the:

⋅ available cover and habitat (i.e. a good embeddedness score)

⋅ moderate stability of the banks, and

⋅ sites being reduced in habitat (i.e. isolated pools).

A detailed description of each site and the habitat condition, including for dry sites, is presented in Table 4.1.

Figure 4.1 Habitat bioassessment scores at each site in each survey.

– – –

– –

poor

moderate

good

excellent

0

20

40

60

80

100

120

140

CBC-US CBC-ML CBC-DS1 CBC-DS2 CC-DS2 CC-DS1 CC-WE

Background Site


Hab

itat B

ioas

sess

men

t Sco

re

pre-wet survey post-wet survey

– not surveyed

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Tabl

e 4.

1 A

quat

ic h

abita

t at e

ach

site

in b

oth

surv

eys.

Site

D

escr

iptio

n

Phot

ogra

ph

Bac

kgro

und

Site

CB

C-U

S

Cam

pbel

l C

reek

The

mild

ly s

inuo

us,

ephe

mer

al c

hann

el w

as d

ry in

bot

h su

rvey

s; t

he c

hann

el w

as

6 m

wid

e an

d ch

arac

teris

ed b

y be

droc

k su

bstra

te w

ith s

and.

Th

e av

erag

e he

ight

of

both

ban

ks w

as 1

m.

The

re w

as e

vide

nce

that

run

-off,

flo

w a

nd c

lear

ing

of

vege

tatio

n ha

d af

fect

ed

bank

st

abili

ty.

O

ccas

iona

l cl

umps

of

na

tive

shru

bs

char

acte

rised

the

ripar

ian

zone

, with

gra

sses

and

sm

all t

rees

(<10

m).

Tra

iling

ban

k ve

geta

tion

and

shad

ing

of t

he c

hann

el p

rovi

ded

aqua

tic h

abita

t. D

ue t

o th

e hi

ghly

ep

hem

eral

nat

ure

of th

e w

ater

cour

se, f

ish

pass

age

wou

ld b

e re

stric

ted

exce

pt in

ver

y hi

gh fl

ow.

Vie

w u

pstre

am in

pos

t-wet

sea

son

surv

ey.

Vie

w u

pstre

am in

pre

-wet

sea

son

surv

ey.

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tal

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atic

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Site

D

escr

iptio

n

Phot

ogra

ph

Pote

ntia

lly Im

pact

ed S

ites

CB

C-M

L

Cam

pbel

l C

reek

The

mild

ly s

inuo

us,

ephe

mer

al c

hann

el w

as d

ry in

bot

h su

rvey

s.

The

chan

nel w

as

1 m

wid

e, w

ith lo

w b

anks

. Th

e le

ft ba

nk w

as 1

.2 m

hig

h an

d th

e rig

ht b

ank

was

1 m

hi

gh.

The

subs

trate

had

mod

erat

e co

mpa

ctio

n an

d ra

nged

from

silt

and

/ or

cla

y to

be

droc

k.

The

ripar

ian

zone

was

2 m

wid

e on

bot

h ba

nks,

dom

inat

ed b

y na

tive

gras

ses

and

larg

e tre

es (>

10 m

; how

ever

, shr

ubs

and

smal

ler t

rees

(<10

m w

ere

also

pr

esen

t. G

rass

es in

the

cha

nnel

pro

vide

d aq

uatic

hab

itat

durin

g flo

w.

The

re w

as

evid

ence

of

st

ock

acce

ss

caus

ing

mod

erat

e di

stur

banc

e.

D

ue

to

the

high

ly

ephe

mer

al n

atur

e of

the

wat

erco

urse

, fis

h pa

ssag

e w

ould

be

rest

ricte

d ex

cept

in h

igh

flow

.

Vie

w u

pstre

am in

pos

t-wet

sea

son

surv

ey.

Vie

w u

pstre

am in

pre

-wet

sea

son

surv

ey.

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atic

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Site

D

escr

iptio

n

Phot

ogra

ph

CB

C-D

S1

Cam

pbel

l C

reek

The

mild

ly s

inuo

us, e

phem

eral

cha

nnel

was

dry

in b

oth

surv

eys

and

was

3 m

wid

e,

with

an

aver

age

bank

hei

ght o

f 2 m

. Th

e su

bstra

te w

as m

ainl

y sa

nd w

ith g

rave

l and

pe

bble

s. T

he ri

paria

n zo

ne w

as 2

m w

ide

on b

oth

bank

s, w

ith s

ome

shru

bs, g

rass

es

and

smal

l an

d la

rge

trees

. S

hadi

ng o

f th

e ch

anne

l an

d tra

iling

ban

k ve

geta

tion

prov

ided

aqu

atic

hab

itat

whe

n in

flo

w.

Ove

rall,

ban

k st

abili

ty w

as m

oder

ate,

but

af

fect

ed b

y cl

earin

g of

veg

etat

ion,

run

-off,

flow

and

sto

ck a

cces

s.

Due

to th

e hi

ghly

ep

hem

eral

nat

ure

of th

e w

ater

cour

se, f

ish

pass

age

wou

ld b

e re

stric

ted

exce

pt in

hig

h flo

w.

Vie

w u

pstre

am in

pos

t-wet

sea

son

surv

ey.

Vie

w u

pstre

am in

pre

-wet

sea

son

surv

ey.

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atic

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Site

D

escr

iptio

n

Phot

ogra

ph

CB

C-D

S2

Cal

lide

Cre

ek

The

mild

ly s

inuo

us,

ephe

mer

al c

hann

el h

ad a

n av

erag

e w

idth

of

1 m

, w

ith a

n av

erag

e po

ol d

epth

of 0

.7 m

. A

roa

d cu

t thr

ough

the

mid

dle

of th

e si

te.

In th

e po

st-

wet

sur

vey,

the

re w

as a

dee

p po

ol o

n th

e so

uthe

rn s

ide

of t

he r

oad

and

two

shal

low

er p

ools

on

the

north

ern

side

. I

n th

e pr

e-w

et s

urve

y, t

here

was

onl

y on

e sm

all p

ool r

emai

ning

on

the

sout

hern

sid

e.

The

left

bank

was

2.0

m h

igh

and

the

right

ban

k w

as 2

.5 m

hig

h, w

ith m

oder

ate

bank

ero

sion

. R

un-o

ff, v

eget

atio

n cl

earin

g an

d st

ream

flow

affe

cted

ban

k st

abili

ty.

The

subs

trate

was

com

pose

d of

a r

ange

of

parti

cle

size

s co

mpr

isin

g co

bble

s, p

ebbl

es,

sand

, gr

avel

and

silt

/ c

lay.

G

rass

do

min

ated

the

rip

aria

n zo

ne w

ith s

ome

nativ

e sh

rubs

and

sm

all

trees

(<1

0 m

).

Trai

ling

bank

veg

etat

ion

and

isol

ated

aqu

atic

pla

nts

(Per

sica

ria s

p.) p

rovi

ded

aqua

tic

habi

tat.

Ove

rall

ther

e w

as h

igh

chan

nel d

istu

rban

ce.

Due

to

the

high

ly e

phem

eral

na

ture

of t

he w

ater

cour

se, f

ish

pass

age

wou

ld b

e re

stric

ted

exce

pt in

hig

h flo

w.

Vie

w u

pstre

am in

pos

t-wet

sea

son

surv

ey.

Vie

w u

pstre

am in

pre

-wet

sea

son

surv

ey.

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Site

D

escr

iptio

n

Phot

ogra

ph

CC

-DS

1

Cal

lide

Cre

ek

The

ephe

mer

al c

hann

el w

as r

elat

ivel

y st

raig

ht a

nd w

as 1

0 m

wid

e, w

ith a

n is

olat

ed

pool

in th

e po

st-w

et s

easo

n su

rvey

. Th

is p

ool w

as d

ry in

the

pre-

wet

sea

son

surv

ey.

The

stee

p le

ft ba

nk w

as 3

m h

igh

and

the

mod

erat

ely

slop

ing

right

ban

k w

as 2

.5 m

hi

gh.

The

subs

trate

had

mod

erat

e ag

grad

atio

n an

d co

nsis

ted

of a

rang

e of

sed

imen

t si

zes

com

pris

ing

sand

, gra

vel a

nd p

ebbl

es.

The

ripar

ian

zone

was

cha

ract

eris

ed b

y sh

rubs

and

larg

e tre

es (>

10 m

), w

ith s

ome

gras

ses

and

smal

l tre

es (<

10 m

). A

quat

ic

habi

tat

in

the

post

-wet

se

ason

su

rvey

co

nsis

ted

of

larg

e pa

tche

s of

flo

atin

g du

ckw

eed

(Spi

rode

la p

unct

ata)

, in

divi

dual

log

s an

d br

anch

es.

The

re w

as h

igh

dist

urba

nce,

with

ban

k st

abili

ty w

as a

ffect

ed b

y ve

geta

tion

clea

ring,

run-

off a

nd s

tock

ac

cess

. D

ue to

the

high

ly e

phem

eral

nat

ure

of th

e w

ater

cour

se fi

sh p

assa

ge w

ould

be

rest

ricte

d ex

cept

in h

igh

flow

.

Vie

w u

pstre

am in

pos

t-wet

sea

son

surv

ey.

Vie

w u

pstre

am in

pre

-wet

sea

son

surv

ey.

frc e

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atic

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52

Site

D

escr

iptio

n

Phot

ogra

ph

CC

-DS

2

Cal

lide

Cre

ek

The

ephe

mer

al c

hann

el w

as d

ry in

bot

h su

rvey

s.

The

chan

nel w

as 2

.5 m

wid

e an

d ha

d a

3 m

hig

h le

ft ba

nk a

nd a

2 m

hig

h rig

ht b

ank,

with

cle

ared

veg

etat

ion

on b

oth

side

s.

Ban

k st

abili

ty w

as a

ffect

ed b

y ru

n-of

f, flo

w a

nd t

he r

oad.

Th

e su

bstra

te

com

pris

ed a

mix

ture

of s

ilt /

clay

, san

d, g

rave

l and

peb

bles

. Tr

ees

and

shru

bs in

the

ripar

ian

zone

wer

e sc

atte

red

on th

e 3

m w

ide

right

ban

k an

d se

mi-c

ontin

uous

on

the

3.5

m w

ide

left

bank

. T

he l

arge

am

ount

of

vege

tatio

n gr

owin

g in

the

cha

nnel

su

gges

ts i

rreg

ular

flo

w.

Cas

tor

oil

(Ric

inus

com

mun

is)

dom

inat

ed t

he c

reek

bed

up

stre

am.

The

site

was

ver

y hi

ghly

dis

turb

ed w

ith e

vide

nce

of e

rosi

on a

nd s

ever

e ag

grad

atio

n. T

here

was

a s

mal

l (re

cent

ly in

stal

led)

gau

ging

wei

r at

the

eas

t en

d of

th

e si

te.

Due

to th

e hi

ghly

eph

emer

al n

atur

e of

the

wat

erco

urse

, fis

h pa

ssag

e w

ould

be

rest

ricte

d ex

cept

in h

igh

flow

.

Vie

w u

pstre

am in

pos

t-wet

sea

son

surv

ey.

Vie

w u

pstre

am in

pre

-wet

sea

son

surv

ey.

frc e

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atic

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53

Site

D

escr

iptio

n

Phot

ogra

ph

CC

-WE

Wet

land

The

site

was

cha

ract

eris

ed b

y re

lativ

ely

smal

l ele

vate

d ar

eas

with

in a

wet

land

. In

the

post

-wet

sea

son

surv

ey, t

he a

vera

ge w

ette

d w

idth

was

100

m a

nd th

e w

etla

nd h

ad

an a

vera

ge d

epth

of

0.2

m a

nd a

max

imum

dep

th o

f 1.

5 m

. I

n th

e pr

e-w

et s

easo

n su

rvey

, th

e w

ette

d w

idth

dec

reas

ed t

o ap

prox

imat

ely

30 m

. T

he s

ite i

s in

a

mod

erat

ely

flat a

rea,

with

a lo

w a

vera

ge b

ank

heig

ht o

f 0.2

m.

The

subs

trate

had

low

co

mpa

ctio

n an

d w

as d

omin

ated

by

silt

/ cla

y, w

ith s

and

and

grav

el.

In th

e po

st-w

et

seas

on s

urve

y, t

here

wer

e aq

uatic

pla

nts

incl

udin

g H

ymen

achn

e sp

., C

yper

us s

p.,

Junc

us s

p., P

ersi

caria

sp.

, Lud

wig

ia s

p., M

arsi

lea

sp. a

nd P

aspa

lum

sp.

The

ripa

rian

zone

was

>10

0 m

wid

e on

bot

h ba

nks

and

was

dom

inat

ed b

y na

tive

gras

ses

and

tall

trees

(>1

0 m

); th

ere

wer

e al

so s

ome

shru

bs a

nd s

mal

l tre

es (

<10

m).

The

wet

land

ha

d go

od s

hadi

ng a

nd s

ome

traili

ng b

ank

vege

tatio

n.

The

adja

cent

land

was

use

d fo

r gra

zing

and

ther

e w

as e

vide

nce

of h

orse

s an

d ca

ttle

acce

ssin

g th

e w

etla

nd.

Run

-of

f, flo

w,

stoc

k ac

cess

, ve

geta

tion

clea

ring

and

flood

plai

n sc

ours

affe

cted

ban

k st

abili

ty.

As

the

wet

land

was

cha

ract

eris

ed b

y an

isol

ated

poo

l, fis

h pa

ssag

e w

ould

be

rest

ricte

d ex

cept

in h

igh

flow

.

Vie

w u

pstre

am in

pos

t-wet

sea

son

surv

ey.

Vie

w u

pstre

am in

pre

-wet

sea

son

surv

ey.

frc environmental


Reach Environs

The reach environs (i.e. land immediately next to the riparian zone) at most sites were dominated by grasses and eucalypt trees. However, there were also some substantial areas of bare ground at sites CBC-US, CBC-ML and CC-DS1 (Figure 4.2).

Overall, the reach environs had been moderately affected by human activities; land use in the survey area included low intensity grazing at all sites and an unused reserve area at site CBC-ML, in the BHS project area. Cattle access to the creeks has caused some minor disturbance at most of the sites.

Figure 4.2 Reach environ at site CBC-ML dominated by grasses and bare ground in the pre-wet season survey.

frc environmental


Riparian Vegetation

Native grasses and eucalypt trees typically dominated the riparian vegetation at all sites. The riparian zone was generally narrow at most sites. The most established vegetation occurred at site CC-WE, where there were mature eucalypts (Figure 4.3). Grasses and young eucalypt trees dominated the riparian vegetation of the ephemeral creeks at all other sites (Figure 4.4). There were also several weed species in the riparian zone; e.g. Noogoora burr at site CBC-DS.

Figure 4.3 Grasses, eucalypt trees and bare ground at site CC-WE in the post-wet season survey.

Figure 4.4 Grasses and eucalypt trees at site CBC-DS in the post-wet season survey.

frc environmental


Bank Stability

Banks were stable to moderately stable at all sites, except at site CC-DS2, where bank stability was poor and there was substantial erosion (Figure 4.5). The poor bank stability at this site was due to flow and runoff, and the low cover of vegetation and the dominant vegetation being grass.

Figure 4.5 Eroded left bank at site CBC-DS2 in the post-wet season survey.

frc environmental


Substrate Composition

In the post-wet season survey, the substrate was mixed at all sites, however, bedrock was also common at sites CBC-US and CBC-ML (Figure 4.6).

The substrate composition in the pre-wet season survey was similar to the substrate composition in the post-wet season survey. It was dominated by gravel, sand and silt and / or clay at most sites (Figure 4.7), with bedrock at sites CBC-US and CBC-ML (Figure 4.8). The variety of substrates at most sites would provide good habitat for aquatic organisms in periods of flow.

Figure 4.6 Particle size distribution at each site in the post-wet season survey (visual assessment).

0

25

50

75

100


Background Site


Perc

ent C

over

silt / clay (<1 mm) sand (1–4 mm) gravel (4–16 mm) pebble (16–64 mm) cobble (64–256 mm) boulder (>256 mm) bedrock

frc environmental


Figure 4.7 Particle size distribution at each site in the pre-wet season survey (visual assessment).

Figure 4.8 Bedrock substrate at site CBC-US in pre-wet season survey.

0

25

50

75

100


Background Site Potentially Impacted Sites

Perc

ent C

over

age

silt / clay (<1 mm) sand (1–4 mm) gravel (4–16 mm) pebble (16–64 mm) cobble (64–256 mm) boulder (>256 mm) bedrock

frc environmental


Channel Diversity

Channel diversity was poor at all sites. Each of the ephemeral watercourses either contained isolated pools or were dry. It is expected that these sites would have runs and pool habitat in moderate to high flows. There is also the potential for temporary riffle habitat to occur at some sites in periods of high flow, but these riffles would be unlikely to occur for long periods of time.

In-stream Habitat

In-stream habitat (i.e. structural elements) provides refuge and food for aquatic animals such as fish, turtles and macrocrustaceans. In-stream habitats at most sites were dominated by small pools, with a low percent cover of woody debris, and trailing bank or overhanging vegetation. Larger substrates (e.g. pebbles, cobbles and boulders) provided some habitat at most sites.

frc environmental


Water Quality

Temperature

There is no WQO for water temperature. Water temperatures were slightly higher in the pre-wet season survey than in the post-wet season survey (Figure 4.9). Water temperature at any given site was likely to reflect a number of factors including the:

⋅ season

⋅ time of day

⋅ size of the water body

⋅ prevailing weather conditions

⋅ flow, and

⋅ riparian cover.

Figure 4.9 Water temperature at each site in both surveys.

– – – – – – –

– –

0

5

10

15

20

25

30


Background Site


Wat

er T

empe

ratu

re (°

C)

post-wet season pre-wet season

– dry site

frc environmental


pH

In the post-wet season survey, the pH was below the WQO range at each site where there was water; however, in the pre-wet season survey the pH was within the WQO range at each site (Figure 4.10). The change in pH at each site between surveys was likely to be related to the change in water level (i.e. evaporation may have resulted in a concentration of salts).

Figure 4.10 The pH at each site in both surveys, and the Fitzroy Basin WQO range for Callide Creek.

–

– – – – – –

– –

Fitzroy Basin WQO range – Callide Creek

0

1

2

3

4

5

6

7

8

9


Background Site


pH

post-wet season

pre-wet season

– dry site

frc environmental


Electrical Conductivity

In the post-wet season survey, electrical conductivity was above the Fitzroy Basin WQO for Callide Creek catchment at each site. In the pre-wet season survey, electrical conductivity was above the WQO for high flow at site CBC-DS2, and within the WQO range at site CC-WE (Figure 4.11). This high electrical conductivity was likely to be due to:

⋅ local geology and/or land use (i.e. grazing), and

⋅ the small volume of water in the pool, as evaporation might have concentrated the ions in the water.

Figure 4.11 Electrical conductivity at each site in both survey, and the Fitzroy Basin WQO for Callide Creek.

– – – – – – – –

–

Fitzroy Basin WQO – Callide Creek (base flow)

0

500

1000

1500

2000

2500


Background Site


Elec

tric

al C

ondu

ctiv

ity (μ

S/cm

)

pre-wet season

post-wet season – dry site

Fitzroy Basin WQO – Callide Creek (high flow)

frc environmental


Turbidity

In the post-wet season survey, turbidity was below the Fitzroy Basin WQO for Callide Creek at all sites; and in the pre-wet season survey, turbidity was above the WQO at both sites (Figure 4.12). The high turbidity in the pre-wet season survey may be due to the decrease in water levels. High turbidity at site CC-WE was also likely to be influenced by eroded banks from livestock watering.

Figure 4.12 Turbidity at each site in both surveys, and the Fitzroy Basin WQO for Callide Creek.

– – –

– – – –

– –

0

50

100

150

200

250


Background Site


Turb

idity

(NTU

)

post-wet season

pre-wet season

– dry site

Fitzroy Basin WQO trigger value – Callide Creek

frc environmental


Dissolved Oxygen

The percent saturation of dissolved oxygen was outside the WQO range in both surveys. In the post-wet season survey, the percent saturation of dissolved oxygen was below the WQO range at sites CBC-DS2 and CC-DS1, and above the WQO range at site CC-WE. In the pre-wet season survey, the percent saturation of dissolved oxygen was below the WQO range at site CBC-DS2, and above the WQO range at site CC-WE (Figure 4.13). The low percent saturation of dissolved oxygen at sites CC-DS1 and CBC-DS2 in both surveys was likely to be due to the low water levels, with only isolated pools present at each site. The percent saturation of dissolved oxygen is sensitive to periods of stagnation, which is typical of ephemeral waterways, and dissolved oxygen can vary considerably (DERM 2009a). Variation in the percent saturation of dissolved oxygen between sites and between surveys is likely to reflect the:

⋅ time of day measurements were taken (plants photosynthesise during the day, producing oxygen)

⋅ photosynthetic rates of algae and aquatic plants (which are affected by light availability and temperature)

⋅ rate of oxygen uptake by micro-organisms in the waterway associated with decomposing organic matter, and

⋅ amount of surface mixing at a monitoring point (caused by flows, wind and bird activity).

frc environmental


Figure 4.13 Percent saturation of dissolved oxygen at each site in both surveys, and the Fitzroy Basin WQO range for Callide Creek.

– – – –

– – –

– –

Fitzroy Basin WQO range – Callide Creek

0

20

40

60

80

100

120

140

160


Background Site


Dis

solv

ed O

xyge

n (%

sat

urat

ion)

post-wet season

pre-wet season

– dry site

frc environmental


5 Aquatic Plants

5.1 Aquatic Plants of the Region

There is little information about aquatic plants of the Callide catchment. Of the 3 758 plant species in the Fitzroy Basin, approximately 174 are wetland indicator species (DERM 2011d). In a survey of 101 sites, 105 aquatic and semi-aquatic plant species were recorded in the Fitzroy Basin between 1989 and 1991 (Duivenvoorden 1992). The most common genera were:

⋅ Cyperus spp.

⋅ Persicaria spp.

⋅ Juncus spp., and

⋅ Potamogeton spp.

Persicaria had the widest distribution, occurring at 56% of sites, although Juncus spp. and Cyperus spp. were the most common species at sites with low diversity (one to two species). The composition of species throughout the Fitzroy Basin was found to be highly dynamic, and large reductions in diversity were recorded after a large flood followed by drought in 1991. In extreme weather, Cyperus and Juncus species commonly survived, whereas Persicaria species often disappeared (Duivenvoorden 1992).

There are many exotic species in the Fitzroy Basin and five were recorded in the current seasonal surveys.

Listed threatened species occur in the Fitzroy Basin, but are unlikely to occur in the BHS project area and were not recorded in the current seasonal surveys.

5.2 Aquatic Plants of the Survey Area

A total of 26 species of aquatic plants were recorded in the survey area in two surveys. In the post-wet season survey, there were 17 species of aquatic plants in the survey area. Aquatic plants were recorded at all sites surveyed. Aquatic plant species richness was highest at site CC-WE (six species) and lowest at sites CBC-DS1 and CC-DS2 (two species). Percent cover of aquatic plants was highest at site CC-DS2 (73.6% mean aquatic plant cover) and lowest at site CBC-DS1 (12.5% mean aquatic plant cover) (Table 5.1).

frc environmental


In the pre-wet season survey, there were nine species of aquatic plants in the survey area at all sites surveyed. Aquatic plants were recorded at all sites surveyed. Aquatic plant species richness was highest at sites CBC-DS2 and CC-DS1 (five species) and lowest at site CC-WE (one species). Percent cover of aquatic plants was highest at site CC-DS2 (78.5% mean aquatic plant cover) and lowest at site CC-WE (0.9% mean aquatic plant cover) (Table 5.2). The low species richness and cover of aquatic plants in both surveys was likely to be due to the highly ephemeral nature of the watercourses. The fewer species recorded in the pre-wet season survey was likely to be due to the lower water level at the sites surveyed.

Aquatic plants with an emergent growth form were the most abundant (i.e. had the highest cover) and most widespread (i.e. recorded at more sites) in both surveys. Common taxa included:

⋅ common rush (Figure 5.1)

⋅ water couch (Figure 5.2), and

⋅ swamp ricegrass.

There was one floating-attached species, water primrose at site CC-WE in both surveys (Table 5.1). There were no submerged aquatic plants in the surveys, as these species cannot persist in ephemeral aquatic habitats.

frc e

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Eco

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68

Tabl

e 5.

1 M

ean

perc

ent c

over

and

spe

cies

rich

ness

of a

quat

ic p

lant

s at

eac

h si

te in

the

post

-wet

sea

son

surv

ey.

Plan

t Spe

cies

Com

mon

Nam

e

Bac

kgro

und

Site

Po

tent

ially

Impa

cted

Site

s

CB

C-U

S C

BC

-ML

CB

C-D

S1

CB

C-D

S2

CC

-DS1

C

C-D

S2

CC

-WE

Emer

gent

Alte

rnan

ther

a de

ntic

ulat

a le

sser

joyw

eed

– –

– –

0.4

– –

Cyn

odon

sp.

B

erm

uda

gras

s –

41.5

–

– –

– –

Cyp

erus

era

gros

tis

umbr

ella

sed

ge

1.7

– –

– –

– 0.

2

Cyp

erus

exa

ltatu

s a

gian

t fla

t-sed

ge

– –

– –

0.7

– –

Cyp

erus

java

nicu

s a

Java

n fla

t-sed

ge

– –

– 0.

2 –

0.1

–

Ech

inoc

hloa

cru

s-ga

lli

barn

yard

gra

ss

28

– –

– 7.

2 73

.5

–

Hym

enac

hne

sp. b

– –

– –

– –

– 0.

1

Junc

us u

sita

tus

com

mon

rush

1.

2 1.

1 –

– –

– –

Leer

sia

hexa

ndra

sw

amp

riceg

rass

–

0.5

8 7.

6 5.

3 –

–

Lept

ochl

oa d

igita

ta

umbr

ella

can

egra

ss

– –

– 2.

8 –

– –

Mar

sile

a hi

rsut

a ha

iry n

ardo

o –

– –

– –

– 9.

1

Pas

palu

m d

istic

hum

w

ater

cou

ch

– –

4.5

2.6

0.6

– 14

.4

Per

sica

ria s

p.

– –

–

–

– 0.

7

Per

sica

ria a

ttenu

ata

atte

nuat

ed

smar

twee

d –

– –

0.8

– –

–

Typh

a sp

. cu

mbu

ngi

– 3

– –

– –

–

frc e

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atic

Eco

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69

Plan

t Spe

cies

Com

mon

Nam

e

Bac

kgro

und

Site

Po

tent

ially

Impa

cted

Site

s

CB

C-U

S C

BC

-ML

CB

C-D

S1

CB

C-D

S2

CC

-DS1

C

C-D

S2

CC

-WE

Floa

ting

Atta

ched

Ludw

igia

pep

loid

esw

ater

prim

rose

–

– –

– –

– 11

.7

Tota

l Tax

onom

ic

Ric

hnes

s

4 4

2 5

5 2

6

Mea

n C

over

(%)

32

.7

46.1

12

.5

14.0

14

.2

73.6

36

.2

a id

entif

icat

ion

conf

irmed

by

Que

ensl

and

Her

bariu

m

b po

ssib

ly H

ymen

achn

e am

plex

icau

lis a

Wee

d of

Nat

iona

l Sig

nific

ance

and

dec

lare

d C

lass

2 p

est u

nder

the

Land

Pro

tect

ion

(Pes

t and

Sto

ck R

oute

Man

agem

ent)

Act

20

02

– no

t pre

sent

frc e

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tal

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atic

Eco

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70

Tabl

e 5.

2 M

ean

perc

ent c

over

and

spe

cies

rich

ness

of a

quat

ic p

lant

s at

eac

h si

te in

the

pre-

wet

sea

son

surv

ey.

Plan

t Spe

cies

C

omm

on N

ame

Bac

kgro

und

Site

Po

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Figure 5.1 Common rush at site CBC-ML in the post-wet season survey.

Figure 5.2 Water primrose at site CC-WE in the pre-wet season survey.

Exotic Species

A potential Weed of National Significance was found at site CC-WE in the post-wet season survey: Hymenachne amplexicaulis; however, conclusive identification was not possible due to lack of reproductive material. There were four exotic species in the post-wet season survey, including:

⋅ Hymenachne at site CC-WE, downstream of mining lease

⋅ giant flat-sedge at site CC-DS1 (downstream of mining lease)

⋅ barnyard grass at site CBC-US (upstream of mining lease) and at sites CC-DS1 and CC-DS2 (downstream of the mining lease), and

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⋅ Bermuda grass, at site CBC-ML (within the mining lease).

In the pre-wet season survey, there was one exotic species, giant flat-sedge.

Listed Species

No species of aquatic plants listed under the EPBC Act or NCWR are known to occur in the region (DERM 2012b), nor were any recorded in the current seasonal surveys.

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6 Aquatic Macroinvertebrates

6.1 Aquatic Macroinvertebrate Communities of the Region

Aquatic macroinvertebrate communities of the Fitzroy Basin were surveyed at three sites by the Department of Natural Resources and Mines (DNRM).

Overall, macroinvertebrate communities at DNRM sites were typically in better condition than those in the current seasonal surveys. The abundance, taxonomic richness and PET richness in bed habitat were higher at DNRM sites. The taxonomic richness and PET richness in edge habitat were higher at sites in the current seasonal surveys than at DNRM sites, but abundance at sites in the current seasonal surveys was similar to or lower than the abundance at DNRM sites.

At DNRM sites, aquatic macroinvertebrate communities were dominated by:

⋅ non-biting midge larvae (sub-family Chironominae)

⋅ mayfly larvae (family Baetidae)

⋅ caddisfly larvae (family Leptoceridae), and

⋅ freshwater shrimp (family Atyidae).

Freshwater shrimps and prawns were likely to be relatively common in the survey area as they are commonly found in the Fitzroy Basin.

6.2 Aquatic Macroinvertebrates of the Survey Area

Abundance

The abundance of macroinvertebrates in bed habitat was lower at all sites in the current surveys than at DNRM reference site 130306B (Don River). This is expected, as the sites in the current surveys were smaller waterbodies (Figure 6.1). The highest abundance in the current surveys was at site CC-WE in the pre-wet season survey. This was due to a high abundance of biting midges (family Ceratopogonidae), which are often found in muddy substrates such as those at site CC-WE (Gooderham & Tsyrlin 2002).

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Figure 6.1 Abundance of macroinvertebrates in bed habitat at each site in both surveys,

and at a DNRM reference site.

– – –

–

– – – x – –

0

50

100

150

200

250

300

350

CB

C-U

S

CB

C-M

L

CB

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S1

CB

C-D

S2

CC

-DS

1

CC

-DS

2

CC

-WE

1303

06B

Background Site

Potentially Impacted Sites DNRM site

Abu

ndan

ce

post-wet season

pre-wet season

DNRM

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The abundance of macroinvertebrates in edge habitat at all sites in the current surveys was higher than or similar to the abundance of macroinvertebrates at DNRM reference sites (Figure 6.2). The abundance of macroinvertebrates was higher in the pre-wet season survey at sites CBC-DS2 and CC-WE. This was likely to be due to less water available, so animals were taking refuge in edge habitat. The high abundance at site CC-WE was due to the high abundance of biting midge larvae (family Ceratopogonidae) and non-biting midge larvae (subfamily Chironominae), while high abundance at site CBC-DS2 was due to non-biting midge larvae (subfamily Tanypodinae).

Figure 6.2 Abundance of macroinvertebrates in edge habitat at each site in both surveys, and at DNRM reference sites.

– – –

–

– – –

– –

0

100

200

300

400

500

600

700

800

900

CB

C-U

S

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C-M

L

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C-D

S2

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-DS

1

CC

-DS

2

CC

-WE

1303

06B

1303

47A

1303

010

Background Site

Potentially Impacted Sites DNRM sites

Abu

ndan

ce

post-wet season

pre-wet season

DNRM

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Taxonomic Richness

� �

Macroinvertebrate taxonomic richness in bed habitat was below the Fitzroy Basin WQO range for Callide Creek catchment at all sites in both surveys, except at site CC-WE in the post-wet season survey (Figure 6.3). Taxonomic richness was much lower at all sites than at DNRM reference site 130306B (Don River). This is likely to be due to the location of the sites; the DNRM reference site was on a river while the sites in this survey were on smaller ephemeral waterways. Biting midge larvae (family Ceratopogonidae) and non-biting midge larvae (subfamily Chironominae) were the most dominant taxa in both surveys.

Figure 6.3 Taxonomic richness of macroinvertebrates in bed habitat at each site in both

surveys, and at the DNRM reference site.

– – –

–

– – – x – –

0

5

10

15

20

25

30

35

40

45

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C-U

S

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L

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S1

CB

C-D

S2

CC

-DS

1

CC

-DS

2

CC

-WE

1303

06B

Background Site


Taxo

nom

ic R

ichn

ess

post-wet season

pre-wet season

DNRM

Bed Habitat

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� � �

Macroinvertebrate taxonomic richness in edge habitat was within the WQO range at:

⋅ site CBC-DS2 in the pre-wet season survey

⋅ site CC-DS1 in the post-wet season survey, and

⋅ site CC-WE in the post-wet season survey (Figure 6.4).

The lower taxonomic richness in the pre-wet survey was likely to be due to the highly ephemeral nature of the watercourses. Taxonomic richness was lower at all sites in the current surveys than at DNRM references sites. The lower taxonomic richness at each site in the survey area was most likely to be due to the sites being reduced to small pools in each survey.

Figure 6.4 Taxonomic richness of macroinvertebrates in edge habitat at each site in

both surveys, and at DNRM reference sites.

– – –

–

– – –

– –

0

10

20

30

40

50

60

CBC-US CBC-ML CBC-DS1 CBC-DS2 CC-DS1 CC-DS2 CC-WE 130306B 130347A 1303010

Background Site


Taxo

nom

ic R

ichn

ess

post-wet season

pre-wet season

DNRM

Edge Habitat

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PET Richness

� �

Overall, the PET richness in bed habitat was very low. Only one PET taxa was caught in bed habitat, at site CBC-DS2 in the post-wet season survey (Figure 6.5). The PET richness in the survey area was significantly lower than at DNRM reference site 130306B (Don River).

Figure 6.5 PET richness of macroinvertebrates in bed habitat at each site in both surveys, and at a DNRM reference site.

– – –

– – – – x – – 0

1

2

3

4

5

6

7

CB

C-U

S

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C-M

L

CB

C-D

S1

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C-D

S2

CC

-DS

1

CC

-DS

2

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-WE

1303

06B

Background Site


PET

Ric

hnes

s

post-wet season

pre-wet season

DNRM

Bed Habitat

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� � �

PET richness in edge habitat was within the WQO range at sites CBC-DS2 and CC-DS1, but was below the WQO range at site CC-WE in both surveys (Figure 6.6). The lower PET richness results in CC-WE was likely to be due to many of the PET taxa were more likely to occur in a river environment than in a shallow wetland environment. PET richness was significantly lower at all sites than at DNRM references sites. The absence of stonefly larvae negatively affects PET richness calculations, however the larvae are unlikely to occur in central Queensland as the preferred habitat for stoneflies does not typically occur in the region.

Figure 6.6 PET richness of macroinvertebrates in edge habitat at each site in both

surveys, and at DNRM reference sites.

– – –

– – – –

– – 0

1

2

3

4

5

6

7

8

9

10

CBC-US CBC-ML CBC-DS1 CBC-DS2 CC-DS1 CC-DS2 CC-WE 130306B 130347A 1303010

Background Site


PET

Ric

hnes

s

post-wet season

pre-wet season

DNRM

Edge Habitat

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SIGNAL 2 Scores

� �

SIGNAL 2 scores in bed habitat were within WQO range at sites CBC-DS2 and CC-DS1 in the post-wet season survey, and below the WQO range at site CC-WE in both surveys (Figure 6.7). Non-biting midge larvae (subfamily Chironominae) were the most dominant taxa in both surveys. Wetlands will have naturally lower scores than streams in the same region. This is due to the macroinvertebrate orders with the highest SIGNAL 2 sensitivity grades being naturally rare in wetlands.

Figure 6.7 SIGNAL 2 scores of macroinvertebrates in bed habitat at each site in both

surveys, and at DNRM reference site.

– – –

–

– – – x – –

0

0.5

1

1.5

2

2.5

3

3.5

4

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C-U

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-DS

1

CC

-DS

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CC

-WE

1303

06B

Background Site


SIG

NA

L 2

Scor

e

post-wet season

pre-wet season

DNRM

Bed Habitat

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� � �

SIGNAL 2 scores in edge habitat were below the WQO range at all sites in both surveys, except at site CBC-DS2 in the post-wet season survey (Figure 6.8). SIGNAL 2 scores at all sites were similar to SIGNAL 2 scores at DNRM reference site 1303010 (Bell Creek), but were lower than DNRM reference sites 130306B (Don River) and 130347A (Callide Creek).

Figure 6.8 SIGNAL 2 scores of macroinvertebrates in edge habitat at each site in both

surveys and at DNRM reference sites.

– – –

–

– – –

– –

0

0.5

1

1.5

2

2.5

3

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5

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1303

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1303

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Background Site


SIG

NA

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Scor

e

post-wet season

pre-wet season

DNRM

Edge Habitat

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SIGNAL 2 Family Bi-plots

� �

Macroinvertebrate communities in bed habitat at all sites were within quadrant 4 in both surveys, which potentially suggests industrial and / or agricultural pollution has affected the community composition (Figure 6.9). However, it is likely that this result is due to the application of the SIGNAL metric, which was developed as an ecological indicator for permanent flowing streams in temperature southern Australia, to ephemeral streams in central Queensland. DNRM reference site 130306B (Don River) was in quadrant 2, indicating high salinity or high concentrations of nutrients.

Figure 6.9 SIGNAL 2 / family bi-plot for macroinvertebrate communities in bed habitat at all sites in both surveys, and at DNRM reference site.

0

0.5

1

1.5

2

2.5

3

3.5

4

0 5 10 15 20 25 30 35 40 45

SIG

NA

L 2

Scor

e

Taxonomic Richness

post-wet season

pre-wet season

DNRM site 130306B

Bed Habitat

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� � �

Macroinvertebrate communities in edge habitat at all sites were within quadrant 4 in both surveys, which suggests industrial and / or agricultural pollution has affected the community composition (Figure 6.10). However, it is likely that this result is due to the application of the SIGNAL metric, which was developed as an ecological indicator for permanent flowing streams in temperature southern Australia, to ephemeral streams in central Queensland. DNRM reference site 130306B (Don River) was in quadrant 2, indicating high salinity or high concentrations of nutrients.

Figure 6.10 SIGNAL 2 / family bi-plot for macroinvertebrate communities in edge habitat at all sites in both surveys, and at DNRM reference site.

0

0.5

1

1.5

2

2.5

3

3.5

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0 5 10 15 20 25 30 35 40 45 50

SIG

NA

L 2

Scor

e

Taxonomic Richness

post-wet season

pre-wet season

DNRM site 130306B

Edge Habitat

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Macrocrustaceans Caught in the Fish Survey

Two species of macrocrustaceans were caught in both surveys:

• freshwater prawn (Macrobrachium sp.) (Figure 6.11), and

• common yabbies (Cherax sp.) and

• an orange-tipped yabby in the post-wet survey (Figure 6.12).

Freshwater prawns and yabbies were caught at sites downstream of the BHS project area (Table 6.1 and Table 6.2). The common yabby is listed as vulnerable on The International Union of Conservation of Nature and Resources Red List of Threatened Species, but it is not listed under the EPBC Act or NCWR.

Figure 6.11 Freshwater prawn, caught at three sites in the post-wet season survey.

Figure 6.12 Common yabby, caught at site CBC-DS1 in post-wet survey.

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61

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1

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–

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– –

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– –

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7 Aquatic Vertebrates

7.1 Aquatic Vertebrates of the Region

Fish

There is little information about fish communities in the Callide Catchment. Five fish species were recorded in the survey area, out of a known 42 species from 24 families in the Fitzroy Basin (Table 7.1). No species caught is listed under the vulnerable schedule of the EPBC Act or NCWR.

The noxious pest mosquito fish (Gambusia holbrooki) were the only exotic species caught in the current seasonal surveys. They have also been caught in previous studies within the Fitzroy Basin (frc environmental 2008). The exotic guppy (Poecilia reticulata) and goldfish (Carassius auratus) are known from the Fitzroy Basin (Berghuis & Long 1999; frc environmental 2009).

The more permanent water holes in the Fitzroy Basin offer suitable refuge habitat for a range of native and exotic species in the dry season. Fish may disperse throughout the system in the wet season. Each of the fish species in the survey area requires some physical in-stream habitat for shelter or for reproduction. A variety of physical aquatic habitat (e.g. woody debris and substrate diversity) also supports diverse macroinvertebrate communities, which are prey to many of the fish in the survey area. Most of the common fish species (e.g. eastern rainbow fish, Agassiz’s glassfish, carp gudgeons and spangled perch) are tolerant species that can live in water characterised:

• low percent saturation of dissolved oxygen

• high electrical conductivity, and

• relatively high turbidity.

Many of the species recorded in the current seasonal surveys are native to intermittent and ephemeral systems of central and western Queensland, and migrate up and downstream, and between different habitats at particular stages of their life cycle (Cotterell 1998; Marsden & Power 2007). Stimuli for movement include small and large discharge events and changes in water temperature.

Of the species known in the catchment that were not found in the current seasonal surveys, most undergo migrations upstream and downstream as adults to spawn, and as juveniles for dispersal. Fish migrations have generally been assumed to take place during periods of high flow, when permanent waterholes that provide refuge for fish become

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reconnected to the main river channels (and this report provides some evidence to support this assumption, as more species were caught in the post-wet season than in the pre-wet season). Juvenile fish also migrate in low to moderate flows. Spring and summer are generally the most important months for migration; however, maintaining fish passage is important throughout the year (Marsden & Power 2007)

Table 7.1 Fish species caught in the Fitzroy Basin, in previous surveys and in the current seasonal surveys.

Family

Species Common Name Fitzroy Basin

Current Seasonal Surveys

Ambassidae

Ambassis agassizii Agassiz's glassfish

Anguillidae

Anguilla obscura Pacific shortfin eel –

Anguilla reinhardtii marbled eel –

Apogonidae

Glossamia aprion mouth almighty –

Ariidae

Neoarius graeffei blue catfish –

Atherinidae

Craterocephalus marjoriae silverstreak hardyhead –

Craterocephalus stercusmuscarum

fly-specked hardyhead –

Belonidae

Strongylura krefftii freshwater longtom –

Centropomidae

Lates calcarifer barramundi –

Clupeidae

Nematalosa erebi bony bream –

Cyprinidae

Carassius auratus goldfish a –

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Family



Eleotridae

Gobiomorphus australis striped gudgeon –

Giurus margaritacea snakehead gudgeon –

Hypseleotris compressa Empire gudgeon –

Hypseleotris spp. carp gudgeons

Morgunda adspersa purple-spotted gudgeon

–

Oxyeleotris lineolatus sleepy cod –

Philypnodon grandiceps flathead gudgeon –

Gobiidae

Glossogobius giuris tank goby –

Redigobius bikolanus speckled goby –

Hemiramphidae

Arrhamphus sclerolepis snub-nosed garfish –

Kuhliidae

Kuhlia rupestris jungle perch –

Megalopidae

Megalops cyprinoides ox-eye herring –

Melanotaeniidae

Melanotaenia splendida splendida

eastern rainbowfish

Melanotaenia splendida tatei desert rainbowfish –

Mugilidae

Mugil cephalus sea mullet –

Myxus petard pinkeye mullet –

Osteoglossidae

Scleropages leichardti southern saratoga –

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Family



Percichthyidae

Macquaria ambigua oriens golden perch –

Plotosidae

Neosilurus hyrtlii Hyrtl’s catfish –

Porochilus rendahli Rendahl's catfish –

Tandanus tandanus freshwater catfish –

Poecilidae

Gambusia holbrooki mosquitofish a

Poecilia reticulata guppy a –

Pseudomugilidae

Pseudomugil signifier Pacific blue eye –

Retropinnidae

Retropinna semoni Australian smelt –

Scorpaenidae

Notesthes robusta bullrout –

Terapontidae

Amniataba percoides barred grunter –

Bidyanus bidyanus silver perch –

Hephaestus fuliginosus sooty grunter –

Leiopotherapon unicolour spangled perch

Scortum hillii leathery grunter – Source (DERM 2012a) – not caught a exotic, declared noxious species

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Turtles

The Fitzroy Basin has a high conservation value with respect to freshwater turtles, as there are several species endemic to the region. Six species have been recorded in the Fitzroy Basin (Limpus et al. 2007):

• Krefft’s river turtle (Emydura macquarii krefftii)

• Fitzroy River turtle (Rheodytes leukops)

• white-throated snapping turtle (Elseya albagula)

• broad-shelled river turtle (Chelodina expansa)

• snake-necked turtle (C. longicollis), and

• saw-shelled turtle (Wollumbinia latisternum).

Krefft’s River Turtle (Emydura macquarii krefftii)

Krefft’s river turtle is common in the Fitzroy Basin and inhabits rivers, creeks and lagoons through eastern Queensland from just north of Brisbane to Princess Charlotte Bay (Wilson & Swan 2008). Turtles from the Emydura genus are omnivorous, feeding on macrophytes, invertebrates, small vertebrates and carrion (Wilson & Swan 2008). They are often observed basking on protruding rocks or logs (Wilson & Swan 2008).

Fitzroy River Turtle (Rheodytes leukops)

Fitzroy River turtles were not captured during either field survey. The species is particularly difficult to catch in nets, and rarely enters traps (M. Gordos, Conservation Manager, NSW DPI, pers. comm. July 2007). The most successful and most commonly used, method to survey Fitzroy River turtles is hand capture on snorkel (M. Gordos, Conservation Manager, NSW DPI, pers. comm. July 2007). Snorkel surveys were not possible during the present surveys due to shallow water and / or high turbidity (and hence low visibility).

The Fitzroy River turtle is endemic to the natural permanent riverine habitats of the middle and lower Fitzroy catchment (Limpus et al. 2007). Little information is available on the abundance and life history of the Fitzroy River turtle across its greater distribution. Riffle zones are an important habitat for the Fitzroy River turtle, with the home ranges of individuals typically overlapping these habitats (Tucker et al. 2001), possibly due to increased foraging success in these habitats (Legler & Cann 1980) or a greater efficiency

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of aquatic cloacal respiration in highly oxygenated waters such as riffle zones (Priest 1997; Franklin 2000; Gordos et al. 2004).

However, under low flow events, or as riffle zones become seasonally ephemeral (i.e. dry completely), the Fitzroy River turtle retreats to deeper sections of pool habitats, or even isolated waterholes, adjacent to riffle zones (Tucker et al. 2001; Limpus et al. 2007). As riffle zones throughout most of the range of the Fitzroy River turtle are likely to be ephemeral, this species should not be considered to be a riffle zone specialist; rather, they exploit this habitat to forage for abundant food sources, such as benthic invertebrates and algae during the wet season and early dry season (Limpus et al. 2007). This allows the turtles to take up nutrients and build fat reserves for the dry season, which is essential for preparing to breed (Limpus et al. 2007). Therefore, while large, slow flowing pools can support populations of the Fitzroy River turtle, they are likely to have a lower carrying capacity than reaches containing riffle zones (Limpus et al. 2007).

Based on the known habitat preferences of this species (i.e. large, permanent pools with ephemeral riffles and large woody debris), it is considered highly unlikely that the Fitzroy River turtle occurs in the BHS project area.

White-throated Snapping Turtle (Elseya albagula)

Within the greater Fitzroy, Burnett and Mary River catchments, the white-throated snapping turtle has been recorded almost exclusively in close association with permanent flowing stream reaches, typically characterised by a sand-gravel substrate with submerged rock crevices, undercut banks and / or submerged logs and fallen trees (Haman et al. 2007). Within the Fitzroy and Mary River catchments, the white-throated snapping turtle is regularly associated with areas of high shade, including submerged logs and overhanging riparian vegetation, during the day; and shallow riffle zones at night (Haman et al. 2007). Capture records suggest that the white-throated snapping turtle is rarely found in reaches without such refuge (Haman et al. 2007). The white-throated snapping turtle has not been recorded from man-made water bodies isolated from flowing streams, such as farm dams or sewage treatment plants, suggesting that the white-throated snapping turtle does not move extended distances over dry land (Haman et al. 2007). White-throated snapping turtles have not been recorded in the Callide Creek catchment (SKM 2011), and due to a lack of habitat, it is unlikely that the white-throated snapping turtle occurs in the BHS project area.

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Broad-Shelled River Turtle (Chelodina expansa)

The broad-shelled river turtle is known from the Murray Darling Basin though there are distinct populations in coastal and central Queensland (Cogger 1996). The Fitzroy Basin represents the northern limit of this species, and it is not abundant at most sites within the basin, apart from in floodplain habitat in the lower Fitzroy (Limpus et al. 2007). It is therefore unlikely to occur in the study area.

Snake-necked Turtle (Chelodina longicollis)

The snake-necked turtle is a generalist species that is omnivorous (Wilson & Swan 2008) and able to survive in a wide range of water quality conditions (including in relatively saline waterbodies (Hart et al. 1991), and is known to migrate overland in a strategy to seek out quality food sources (Chessman 1984). Although it was not sighted or captured during the present surveys, it is possible that there are snake-necked turtles in the study area, although it is unlikely that the study area supports a large population of this species.

Saw-shelled Turtle (Wollumbinia latisternum)

The saw-shelled turtle is widely distributed across Australia; however, within the Fitzroy Basin this species has only been captured in the middle and lower reaches (Limpus et al. 2007). They typically inhabit large, slow-moving riverine reaches and impoundments, so it is unlikely that the saw-shelled turtle occurs in the BHS project area.


No other aquatic mammals, reptiles or amphibians of conservational significance have been recorded from, or are likely to occur within the proposed mining lease (DERM 2012c; SEWPAC 2012). Platypus (Ornithorhynchus anatinus) has not been recorded from the Callide River (DERM 2012c). No evidence of platypus was observed at the sites visited during the field surveys, and it is unlikely that they would inhabit ephemeral streams in the area such as Meteor Creek. However, they may be present in more permanent water bodies in the region (DERM 2012c) (beyond the study area).

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7.2 Aquatic Vertebrates of the Survey Area

Fish

Community Composition

A total of five species of fish were caught in the current surveys:

• eastern rainbowfish (Melanotaenia splendida) (Figure 7.1)

• common carp gudgeon (Hypseleotris sp.) (Figure 7.2)

• Agassiz’s glassfish (Ambassis agassizii) (Figure 7.3)

• spangled perch (Leiopotherapon unicolor) (Figure 7.4), and

• mosquitofish (Gambusia holbrooki) (Figure 7.5).

In the post-wet season survey, all five species of fish were caught. The most abundant species caught was the common carp gudgeon; however, they were only caught at site CBC-DS2, downstream of the BHS (Table 7.2). Spangled perch and rainbowfish were more widespread than the other species, as each was caught at two sites.

In the pre-wet season survey, only three species of fish were caught:

• eastern rainbowfish

• common carp gudgeon, and

• Agassiz's glassfish (Table 7.3)

The most abundant and widespread species in the pre-wet survey was the common carp gudgeon, with all three species caught at both sites that had water (Table 7.2, Table 7.3).

Figure 7.1 Eastern rainbowfish, caught at site CC-WE in the post-wet season survey.

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Figure 7.2 Common carp gudgeon, caught at site CBC-DS2 in the pre-wet season survey.

Figure 7.3 Agassiz’s glassfish, caught at site CC-WE in the pre-wet season survey.

Figure 7.4 Spangled perch, caught at site CBC-DS1 in the post-wet season survey.

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Figure 7.5 Mosquitofish, caught at site CC-DS1 in the post-wet season survey.

Species Richness

Fish species richness was low in the post-wet season survey, ranging from two to four fish species at sites CC-WE and CC-DS2, while all other sites were dry or had no fish (Table 7.2). In the pre-wet season survey, three species were caught at both sites with water, while all other sites were dry (Table 7.3).

The low diversity of fish species was indicative of the ephemeral nature of the streams, which are unlikely to contain diverse communities of fish except during periods of high flow or floods due to restricted fish passage when the watercourses are characterised by isolated pools.

Abundance

The abundance of fish was generally low in both surveys. In the post-wet season survey, the total abundance of fish ranged from five to 50 individuals at sites CC-WE and CBC-DS2 (Table 7.2). In the pre-wet season survey the total abundance of fish ranged from eight to 67 individuals at sites CC-WE and CBC-DS2 (Table 7.3).

The abundance of fish communities in ephemeral waterways, such as those in the current seasonal surveys, are commonly highly variable both spatially and temporally.

frc e

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96

Tabl

e 7.

2 Fi

sh s

peci

es ri

chne

ss a

nd a

bund

ance

at e

ach

site

in p

ost-w

et s

easo

n su

rvey

.

Spec

ies

C

omm

on N

ame

Bac

kgro

und

Site

Po

tent

ially

Impa

cted

Site

s

CB

C-U

S C

BC

-ML

CB

C-D

S C

BC

-DS2

C

C-D

S1

CC

-DS2

C

C-W

E

Am

bass

is a

gass

izii

a A

gass

iz’s

gla

ssfis

h –

– –

– –

– 3

Gam

busi

a ho

lbro

oki b

mos

quito

fish

– –

– 1

1 –

–

Hyp

sele

otris

sp.

a ca

rp g

udge

on

– –

– 43

–

– 1

Leio

poth

erap

on u

nico

lor a

span

gled

per

ch

– –

– 4

18

– –

Mel

anot

aeni

a sp

lend

ida

a ea

ster

n ra

inbo

wfis

h –

– –

2 3

– –

Tota

l Tax

onom

ic R

ichn

ess

0 0

0 4

0 3

2

Tota

l Abu

ndan

ce

0 0

0 50

0

22

5 –

dry

site

a

nativ

e sp

ecie

s b

exot

ic s

peci

es

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Eco

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97

Tabl

e 7.

3 Fi

sh s

peci

es ri

chne

ss a

nd a

bund

ance

at e

ach

site

in p

re-w

et s

easo

n su

rvey

.

Spec

ies

C

omm

on N

ame

Bac

kgro

und

Site

Po

tent

ially

Impa

cted

Site

s

CB

C-U

S C

BC

-ML

CB

C-D

S C

BC

-DS2

C

C-D

S1

CC

-DS2

C

C-W

E

Am

bass

is a

gass

izii

a A

gass

iz’s

gla

ssfis

h –

– –

2 –

– 1

Hyp

sele

otris

sp.

a ca

rp g

udge

on

– –

– 3

– –

2

Mel

anot

aeni

a sp

lend

ida

a ea

ster

n ra

inbo

wfis

h –

– –

2 –

– 1

Tota

l tax

onom

ic ri

chne

ss

0 0

0 3

3 0

0

Tota

l abu

ndan

ce

0 0

0 8

4 0

0 –

dry

site

a

nativ

e sp

ecie

s b

exot

ic s

peci

es

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Life History Stages

In the post-wet season survey, intermediate life history stages dominated fish communities, with adult fish only caught at site CBC-DS2 (Figure 7.6). However, adult and intermediate life history stages dominated fish communities in the pre-wet season survey (Figure 7.7). Due to the fast growth rates (i.e. maturation periods within 12 months) of most of species in the survey area, this is the expected distribution of life history stages for these surveys. That is, most species breed in autumn and summer, so in September most juveniles have developed to later life-history stages.

Figure 7.6 Life-history stage abundance of fish at each site in the post-wet season survey.

– – – –

0

10

20

30

40

50

60


Background Potentially Impacted Sites

Life

His

tory

Sta

ge A

bund

ance

adult intermediate juvenile

– dry site

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Figure 7.7 Life-history stage abundance of fish at each site in the pre-wet survey.

– – –

– –

0

20

40

60

80

100

120


Background Potentially Impacted Sites

Life

His

tory

Sta

ge A

bund

ance

adult intermediate juvenile

– dry site

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Exotic Species

One mosquitofish was caught in the post-wet season survey at site CC-DS1, but not in the pre-wet season survey. Mosquitofish are a declared noxious species under Queensland’s Fisheries Regulation 2008.

Threatened Species

No species listed under the EPBC Act or NCWR were caught in the seasonal surveys.

Ecology of Fish in the Survey Area

Each of the fish species in the survey area requires some physical in-stream habitat for shelter or for reproduction. A variety of physical aquatic habitat (e.g. woody debris and substrate diversity) also supports diverse macroinvertebrate communities, which are prey to many of the fish in the survey area. Most of the species can tolerate a broad range of water quality conditions (Table 7.4).

Fish dispersal in arid regions is dependent on floodwaters, with most species dispersing over large areas during floods. In particular, native fish migrate into upstream ephemeral habitats during high flows and floods for reproduction. Flooding triggers spawning of many species, while temperature is the cue for other species (e.g. spangled perch).

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1

Tabl

e 7.

4 Fi

sh s

peci

es re

cord

ed in

the

curr

ent s

easo

nal s

urve

ys a

nd th

e ra

nge

of w

ater

qua

lity

cond

ition

s in

whi

ch th

ey a

re k

now

n to

occ

ur.

Fam

ily

Latin

Nam

e C

omm

on N

ame

Wat

er T

emp.

(º

C)

Dis

solv

ed

Oxy

gen

(mg/

L)

pH

Elec

tric

al

Con

duct

ivity

(µ

S/cm

) Tu

rbid

ity (N

TU)

Am

bass

idae

Am

bass

is a

gass

izii

a A

gass

iz’s

gla

ssfis

h 11

–33.

6 0.

3–19

.5

6.3–

9.9

19.5

–15

102

0.2–

144

Eleo

trid

ae

Hyp

sele

otris

sp.

b co

mm

on c

arp

gudg

eons

8.

4–31

.7

0.6–

12.8

4.

8–9.

1 19

.5–5

380

0.5–

65

Mel

anot

aeni

idae

Mel

anot

aeni

a sp

lend

ida

c ea

ster

n ra

inbo

wfis

h 15

–32

1.1–

10.8

6.

87–8

.47

49–7

90

0.6–

16

Tera

pont

idae

Leio

poth

erap

on u

nico

lor

span

gled

per

ch

5–44

≥0

.4

4–10

.2

333–

59 1

67

1.5–

260.

0

Sou

rces

: A

llen

et a

l. 20

02; P

usey

et a

l. 20

04

NTU

N

ephe

lom

etric

Tur

bidi

ty U

nit

a

base

d on

Aga

ssiz

’s g

lass

fish

data

col

lect

ed fr

om s

outh

-eas

t Que

ensl

and

b

ba

sed

on w

este

rn c

arp

gudg

eon

data

col

lect

ed fr

om s

outh

-eas

t Que

ensl

and

c

base

d on

eas

tern

rain

bow

fish

dat

a co

llect

ed fr

om th

e B

urde

kin

Riv

er

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Agassiz’s Glassfish

Agassiz’s glassfish is commonly found in rivers, creeks, ponds, reservoirs, drainage ditches and swamps from Cairns in Queensland to Lake Hiawatha in New South Wales, and in the Murray-Darling system (McDowall 1996; Allen et al. 2002). It is found in a variety of still or slow-flowing habitats in larger lowland rivers, upland rivers and streams, small coastal streams, and occasionally in lakes and river impoundments, particularly in areas with submerged aquatic plant and bank side vegetation (Pusey et al. 2004). It is tolerant of a range of water quality conditions, although it is often found in areas of low turbidity (Pusey et al. 2004). The diet of this species consists largely of small crustaceans and adult and larval insects, including mosquitoes (McDowall 1996). This species spawns and completes its life cycle in freshwater, and during spawning it deposits and fertilises demersal eggs on aquatic vegetation (Merrick & Schmida 1984). Information on the migration habits of Agassiz’s glassfish is limited; however, it appears that this species may undertake upstream migrations triggered by increased flow (Pusey et al. 2004).

Carp Gudgeons

Carp gudgeons include undescribed Hypseleotris species that readily hybridise (many in a hemi clonal fashion), together with the firetail gudgeon and the western carp gudgeon. Firetail gudgeons are known to hybridise with the undescribed taxa and cannot be phylogenetically distinguished from them on the basis of genetic data. While the western carp gudgeon is a valid species, identification of this species requires a microscope, which is not practical in field surveys. The western carp gudgeon has a similar distribution and ecological role as the undescribed carp gudgeons, and so has been grouped with these taxa.

Carp gudgeons occur in many of Queensland’s coastal drainages and have been recorded as far north as the Tully-Murray Swamps and as far south as the Hunter River, in central New South Wales (Pusey et al. 2004). Carp gudgeons are a benthic species typically found near aquatic vegetation and woody debris (Allen et al. 2002) in a variety of habitats including large waterbodies (e.g. rivers, lakes, dams and weirs), streams and associated floodplain habitats (Allen et al. 2002; Pusey et al. 2004). Carp gudgeons can generally tolerate a wide range of environmental conditions including:

• pH from 4.4 to 8.9

• electrical conductivity up to 4123 µS/cm, and

• water temperature up to 31.2 ºC (Pusey et al. 2004).

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Eastern Rainbowfish

The eastern rainbowfish is common to many parts of north eastern and central Australia, and is usually abundant wherever it occurs (Allen et al. 2002). Numerous subspecies are present within the Melanotaenia species complex. Several of these subspecies have been removed from the complex and given true species status, as molecular data have become available.

Rainbowfish usually prefer areas of sluggish water flow, and can be found in a variety of habitats including streams, wetlands, floodplains and lowland rivers (Pusey et al. 2004). This tropical species is tolerant of a wide range of environmental conditions (electrical conductivity to 780 µS/cm and water temperature up to 33 ºC); however, it is not often found in highly degraded streams (Marsden & Power 2007). They spawn all year round, although spawning peaks immediately before and during flood periods (Merrick & Schmida 1984). Adults migrate upstream to spawn during the wet season (from November to April) when water flows are high (Merrick & Schmida 1984).

Mosquitofish / Eastern Gambusia

Note: mosquitofish is the common name used in Queensland, eastern gambusia is the common name used in New South Wales

The mosquitofish (Gambusia holbrooki) is a widespread and abundant species whose numbers are in plague proportions in some areas of Australia. It is commonly found in all states of Australia including coastal drainages of New South Wales; however, it is native to north and central America and was introduced into Australia as a mosquito control measure that has proven to have minimal effect (Allen et al. 2002). They prefer warm, still waters and are typically found shoaling at the edges of streams and lakes (Allen et al. 2002). Mosquitofish have a large reproductive output and have broad environmental tolerances, which gives them a potential competitive advantage over native species (DPI 2000). Mosquitofish are declared noxious in Queensland under the Fisheries Act.

Spangled Perch

The spangled perch is Australia’s most widespread native fish and is abundant within almost any wet environment across coastal and inland northern Australia; from wheel ruts to water troughs, tanks, drains, lakes and rivers (Wager & Unmack 2000; Allen et al. 2002; Pusey et al. 2004). Spangled perch are thought to aestivate (remain dormant) in wet mud

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or under moist leaf litter in ephemeral water holes during droughts (Allen et al. 2002) and are likely to persist in the surveyed creeks throughout the year.

Spangled perch can generally tolerate a wide range of environmental conditions including:

• pH from 4.0 to 10.2

• electrical conductivity up to 5000 µS/cm (i.e. sea water), and

• water temperature up to 44 ºC (Allen et al. 2002; Pusey et al. 2004).

This species has the lowest pH and highest temperature tolerance of any of the species caught in the current seasonal surveys. This species has remarkable dispersal abilities and is particularly efficient at colonising new water bodies (Wager & Unmack 2000); eggs hatch in two days and the larvae develop in 24 days (Allen et al. 2002). Like other terapontids, the spangled perch is capable of rapid and extensive movements and they migrate past barriers that impede other species (Pusey et al. 2004; Marsden & Power 2007). Adults migrate upstream, during high-flow events, to spawn; and adults and juveniles undertake dispersive (lateral) migrations, from refuge habitats to floodplain habitats, during the wet season (Marsden & Power 2007).

Turtles

No turtles were caught in either survey nor were any sighted. Turtles were not specifically surveyed due to unsuitable habitat conditions.


No other aquatic vertebrates were observed during the surveys.

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8 Summary of Aquatic Ecological Values

The current condition of freshwater aquatic ecosystems within the survey area is generally moderate and is consistent with the ecological condition of aquatic ecosystems throughout the wider catchment. EVs are influenced primarily by the ephemeral and intermittent nature of the region’s waterways; although agricultural development and mining within the region has also influenced water quality and the physical characteristics of aquatic habitat. Creeks in the study area and catchment are generally in a moderate condition.

The reach environ at most sites was dominated by grasses and eucalypts, with substantial areas of bare ground at most sites in the ephemeral creeks. Based on an comparison of the Fitzroy Basin WQOs for Callide Creek, water quality was moderate in the seasonal surveys, and was characterised by a low percent saturation of dissolved oxygen and high turbidity. Land use in the survey area included low intensity grazing, which was consistent with the land use of the wider Fitzroy Basin.

The plant and animal biodiversity was low, but was dominated by species that are tolerant of varying and often harsh conditions, typical of the ephemeral waterways in the BHS project area. No listed species of freshwater plants or aquatic animals have been recorded from, or are likely to occur in, the freshwater waterways of the survey area. One exotic fish species was caught in the post-wet season survey. Overall, the condition of the survey sites was consistent with the condition of aquatic ecosystems throughout the wider catchment.

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9 Potential Impacts

Construction and mining activities associated with the BHS project have the potential to impact on aquatic ecology, through activities including:

• the operation and maintenance of vehicles and other equipment

• vegetation clearing and earthworks

• the management of water resources

• loss of catchment area for the pit and infrastructure

• loss of on-site dams and wetlands

• creek diversions

• changes to flow regimes, and

• the construction of creek crossings, such as haul roads and light vehicle access roads.

The aquatic ecology attributes that could be impacted by these activities include:

• aquatic habitat (including riverine, palustrine and lacustrine wetland habitats)

• wetlands designated as being of high ecological significance

• aquatic plants (not species of conservation significance)

• aquatic macroinvertebrates, including crustaceans (not species of conservation significance)

• fish (not species of conservation or fisheries significance), and

• turtles (not species of conservation significance such as Fitzroy River turtle and white-throated snapping turtle, as these are not expected to occur).

The assessment of impacts is based on the legislative framework and description of the existing environment. Risks to the aquatic environment will be minimised and mitigated through the design, implementation and enforcement of environmental management plans during the construction, operation and decommissioning of the project. A summary of the potential impacts and associated mitigation measures is provided in Table 9.1.

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7

Tabl

e 9.

1 S

umm

ary

of p

oten

tial i

mpa

cts

and

prop

osed

miti

gatio

n m

easu

res.

Act

ivity

/ El

emen

t Po

tent

ial I

mpa

cts

– U

nmiti

gate

d M

itiga

tion

/ Man

agem

ent P

roto

col

Det

aile

d D

escr

iptio

n R

isk

Ass

essm

ent

Con

stru

ctio

n

oper

atio

n an

d m

aint

enan

ce o

f ve

hicl

es a

nd o

ther

eq

uipm

ent d

urin

g co

nstru

ctio

n

⋅ fu

el a

nd lu

bric

ant s

pills

ent

erin

g w

ater

cour

ses

⋅ lit

ter a

nd w

aste

ent

erin

g w

ater

cour

ses

⋅ si

tes

for

stor

age,

mai

nten

ance

and

han

dlin

g of

pot

entia

l sur

face

wat

er c

onta

min

ants

suc

h as

fu

el,

was

te a

nd p

aint

s ar

e w

ithin

bun

ded

area

s co

nstru

cted

in a

ccor

danc

e w

ith A

S19

40 a

nd

abov

e th

e Q

100

flood

leve

l

⋅ ap

prop

riate

spi

ll co

ntai

nmen

t kits

are

ava

ilabl

e

⋅ a

man

agem

ent s

yste

m is

in p

lace

for a

ll sp

ills

of c

onta

min

ants

Sec

tions

9.1

& 1

0.1

Sec

tion

11

vege

tatio

n cl

earin

g an

d ea

rthw

orks

for

cons

truct

ion

of p

it an

d as

soci

ated

in

frast

ruct

ure

⋅ in

crea

sed

turb

idity

and

sed

imen

tatio

n

⋅ in

put

of n

utrie

nts

or o

ther

con

tam

inan

ts a

ssoc

iate

d w

ith th

e so

il / s

edim

ent

⋅ de

crea

sed

habi

tat f

or a

quat

ic fa

una

⋅ an

ero

sion

and

sed

imen

t con

trol p

lan

is d

evel

oped

and

impl

emen

ted

⋅ se

dim

ent d

ams

are

cons

truct

ed b

efor

e w

orks

beg

in

⋅ w

orks

are

don

e in

sta

ges

over

the

life

of th

e m

ine

⋅ tim

ing

of w

orks

is in

the

dry

seas

on, i

f pos

sibl

e

Sec

tions

9.2

& 1

0.2

Sec

tion

11

exca

vatio

n of

the

min

e pi

t and

co

nstru

ctio

n of

as

soci

ated

in

frast

ruct

ure

⋅ lo

ss o

f cat

chm

ent a

rea:

– ch

ange

s to

flow

regi

me

that

may

affe

ct fa

una

(incl

udin

g fis

h br

eedi

ng c

ues)

– de

crea

sed

habi

tat f

or a

quat

ic fa

una

⋅ lo

ss o

f on-

site

dam

s an

d w

etla

nds:

– de

crea

sed

wet

land

hab

itat f

or a

quat

ic fa

una

⋅ co

ntro

lled

disc

harg

es a

re t

imed

to

coin

cide

with

nat

ural

flo

ws,

in

acco

rdan

ce w

ith t

he M

odel

W

ater

Con

ditio

ns f

or C

oal

Min

es i

n th

e Fi

tzro

y B

asin

(20

13)

/ E

nviro

nmen

tal

Aut

horit

y, t

o m

itiga

te a

redu

ctio

n in

cat

chm

ent a

rea

⋅ lo

ng-te

rm r

emed

iatio

n of

the

cat

chm

ent,

incl

udin

g re

inst

atem

ent

of s

ome

gulli

es a

nd d

rain

age

lines

⋅ if

requ

ired,

cat

chin

g an

d tra

nslo

catin

g st

rand

ed a

quat

ic f

auna

in

acco

rdan

ce w

ith t

he F

ish

Sal

vage

Gui

delin

es

Sec

tions

9.4

, 9.

5, 9

.7

10.4

& 1

0.5

S

ectio

n 11

cons

truct

ion

of

wat

erco

urse

di

vers

ions

⋅ in

crea

sed

turb

idity

⋅ se

dim

enta

tion

⋅ de

crea

sed

habi

tat t

hrou

gh e

rosi

on

⋅ ob

stru

ctio

n of

fish

pas

sage

⋅ an

ero

sion

and

sed

imen

t con

trol p

lan

is d

evel

oped

and

impl

emen

ted

⋅ di

vers

ions

sho

uld

be d

esig

ned

and

cons

truct

ed to

pro

vide

hab

itat o

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Sec

tions

9.6

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0.6

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tion

11

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in t

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impl

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in th

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⋅ if

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cat

chin

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ce w

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delin

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⋅ cr

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are

desi

gned

in a

ccor

danc

e w

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ish

Hab

itat G

uide

line

FHG

001

– F

ish

Pas

sage

s in

S

tream

s, F

ishe

ries

Gui

delin

es fo

r Des

ign

of S

tream

Cro

ssin

gs (C

otte

rell

1998

)

Sec

tion

9.8

& 1

0.7

Sec

tion

11

frc e

nviro

nmen

tal

Bou

ndar

y H

ill E

xpan

sion

EIS

: Aqu

atic

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logy

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8

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ivity

/ El

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tent

ial I

mpa

cts

– U

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gate

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tion

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essm

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ratio

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and

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r equ

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⋅ fu

el a

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ent

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g w

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ses

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ter a

nd w

aste

ent

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g w

ater

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ses

⋅ si

tes

for

stor

age,

mai

nten

ance

and

han

dlin

g of

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face

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er c

onta

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suc

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fu

el,

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te a

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area

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m is

in p

lace

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ll sp

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onta

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ants

Sec

tions

9.1

& 1

0.1

Sec

tion

11

man

agem

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f w

ater

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urce

s –

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ance

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Sec

tions

9.

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&

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Con

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l Min

es in

the

Fitz

roy

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in (2

013)

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A

Sec

tions

9.3

& 9

.7

Sec

tion

11

man

agem

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f w

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ntro

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ases

of m

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low

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Sec

tions

9.

3,

9.7

&

10.3

S

ectio

n 11

oper

atio

n of

w

ater

cour

se

cros

sing

s –

haul

ro

ad

⋅ in

crea

sed

turb

idity

⋅ se

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⋅ de

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and

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and

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ted

⋅ cr

ossi

ngs

are

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gned

in a

ccor

danc

e w

ith F

ish

Hab

itat G

uide

line

FHG

001

– F

ish

Pas

sage

s in

S

tream

s, F

ishe

ries

Gui

delin

es fo

r Des

ign

of S

tream

Cro

ssin

gs (C

otte

rell

1998

)

Sec

tion

9.8

& 1

0.7

Sec

tion

11

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9.1 Operation and Maintenance of Vehicles and Other Equipment

Fuel Spills

Vehicles and equipment common to open-cut mining will be used in the construction and operation phases of the BHS project.

Fuel and oil required for the operation of vehicles, and construction and mining machinery presents a risk to water quality and aquatic ecology if spills enter watercourses (via either surface or ground waters). Both diesel and petrol are toxic to aquatic plants and aquatic animals at relatively low concentrations.

Diesel and petrol spills are both likely to form a layer on the surface of the water. The volatility of both diesel and petrol contributes to substantial evaporative loss, while neither product is likely to form water-in-oil emulsions due to their low viscosity. Lubricating oils, of the kind used in diesel engines and gearing, are of a relatively similar density to diesel oils. As such, lubricants would be expected to behave in a similar fashion to diesel oil, and form a surface layer. However, lubricants are much less volatile and so would not evaporate as rapidly. Once incorporated into the sediment, the degradation of oils is significantly slowed, and hydrocarbons may persist in the sediment for some time (Boehm et al. 1987 and Struck et al. 1993, both cited in Nicodem et al. 1997).

The risk to aquatic ecosystems from a fuel spill within the BHS project area is likely to be very low where best practice fuel management is implemented (Section 11.2). Additionally, the risk to aquatic plants and animals in the BHS project area and downstream waters is reduced as most stream reaches tend to be dry or isolated pools for much of the year, and therefore many spills could be effectively cleaned up before they can disperse downstream.

Upon rehabilitation of the proposed final landform of the mine, no residual impacts from split fuels and oils are expected.

Litter and Waste

Litter and waste associated with vehicle maintenance and mining operations also has the potential to entangle larger aquatic fauna, and contribute to the degradation of water quality. As appropriate controls will be in place, such as bunded storage areas and retention of run-off from mining and infrastructure areas, the risk is considered to be low.

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9.2 Vegetation Clearing and Earthworks

Vegetation clearing and earthworks will occur during both the construction and operation phases of the BHS project area. This includes vegetation clearing along new roads and access tracks, and clearing in association with diversions and mining activities. There is a high potential for soil erosion and sedimentation following vegetation clearing and earthworks, due to the intense seasonal rainfall and soil characteristics present on-site. This could lead to impacts on aquatic ecology through increased turbidity and increased concentrations of nutrients in these waterways, as well as alteration of aquatic habitats.

Increased Turbidity

Vegetation clearing and / or earthworks have the potential to increase sediment run-off to creeks and increase turbidity. Increased turbidity may negatively impact fish and macroinvertebrates, as highly turbid water reduces respiratory and feeding efficiency (Karr & Schlosser 1978: cited in Russell & Hales 1993). Increased turbidity may also adversely affect submerged aquatic plants because light penetration (required for photosynthesis) is reduced. Reduced light penetration can also lead to a reduction in temperature throughout the water column (DNR 1998).

At the time of the seasonal surveys, moderate to high turbidity was recorded. Based on the published tolerances of the species caught, the animal communities of the survey area are capable of living in turbid waters. Given these background conditions, small increases in turbidity would be unlikely to have a significant impact on aquatic ecology (Section 11.2); however, significant increases in turbidity could adversely impact the health, feeding and breeding ecology of some species of both macroinvertebrates and fishes.

Input of Nutrients or Other Contaminants

Aquatic biota could also be impacted by nutrients or other contaminants washed into the waterways with the sediment (e.g. nutrients from fertilisers used in rehabilitation). Nutrient inputs can lead to algae or aquatic plant blooms. During the day, as the algae photosynthesises, these blooms can produce a high percent saturation of dissolved oxygen. However, at night, there is a net consumption of oxygen as the algae continue to respire. This can cause the percent saturation of dissolved oxygen to be reduced very low during the night and early morning, which is harmful to biota.

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Input of nutrients or other contaminants into the waterways would impact on aquatic plants and animals. Where the spill is a one-off occurrence, communities may be impacted, but would be expected to recover over time. Chronic inputs of nutrients or contaminants to the waterways would be expected to have longer-term detrimental impacts on plant and animal communities.

Nutrient / contaminant-laden run-off is likely to be low where best practice stormwater and erosion control measures are implemented.

Decreased Habitat for Aquatic Fauna

Vegetation clearing and earthworks near and within the waterways of the BHS project area may decrease the amount of habitat available for aquatic animals. Aquatic animals use a variety of in-stream and off-stream structures for habitat, including:

• large and small woody debris

• bed and banks

• detritus

• tree roots

• boulders

• undercut banks, and

• in-stream, overhanging and trailing bank vegetation.

All of these habitat types were found in the survey area, though some would only be inundated in high flows.

In-stream habitat is an important habitat component and territory marker for many fish and macroinvertebrates. Many species live on or around in-stream habitat as it:

• provides shelter from temperature, current and predators

• contributes organic matter to the system, and

• is important for successful reproduction.

Australian fish species typically spawn either on in-stream vegetation or on hard surfaces like cobbles, boulders, and woody debris.

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The deposition of fine sediments can decrease in-stream bed roughness and habitat diversity and may result in the filling of existing pools. Within the minor (first order) tributaries throughout the BHS project area, this would be unlikely to have a significant impact, as these streams would only carry stormwater flows, and they do not generally hold water (Section 11.2).

A decrease in habitat available for aquatic animals would likely lead to a decline in the abundance and diversity of both macroinvertebrate and fish communities in the watercourses of the BHS project area, and also potentially impact on dependant predators (e.g. birds, reptiles and small mammals).

9.3 Management of Water Resources

Water will be managed in accordance with the Callide Mines Water Management Plan. A detailed description of the site water management, including mine water infrastructure and a detailed water quality assessment, is provided in the Boundary Hill South Surface Water Assessment (AECOM 2013).

Uncontrolled releases from dams that contain advanced dewatering water; mine-affected run-off and pit water are not expected to occur as part of the BHS project. However, if they did occur, they have the potential to affect the aquatic ecology of the receiving environment, including Callide Creek; and potentially the Don River. Though it is unlikely that the aquatic ecology of the Dawson River further downstream would be impacted because the contaminants would be diluted and dispersed, especially during high rainfall and flow events.

Releases of operational water to Campbell Creek will not be required, as surplus mine water can be transferred to either Lake Gasteen or the void left by the existing mine. In the event that controlled releases are required, they are not expected to have a significant impact on the aquatic ecology of the receiving environment, as they will be done in accordance with the Model Water Conditions for Coal Mines in the Fitzroy Basin (March 2013) / Environmental Authority conditions (Section 11.2).

9.4 Loss of Catchment Area

Construction of the mine pit and operational dams (for mine water, clean water diversion and sediment) will result in the loss of a number of ephemeral drainage lines and gullies within the BHS project area. Given the minor stream order (first order) of the drainage lines and gullies, and the small area of catchment to be impacted, the loss of these

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ephemeral drainages and construction of dams to capture flow within the BHS project area is unlikely to have any significant impacts on the EVs of the downstream receiving environment (Section 11.2).

9.5 Loss of On-site Dams and Wetlands

There are no dams or wetlands within the BHS project area; however, there is one wetland mapped as a wetland management area (site CC-WE) downstream, which may be impacted by the expansion of the mine. Impacts to water quality during construction and uncontrolled discharges may have localised impacts on wetland vegetation, macroinvertebrates and habitat for fish and common freshwater turtles (but not turtles of conservation significance).

There are no other wetland management areas within the immediate region (including upstream and downstream of the BHS project area) that have similar ecological values as the wetland at site CC-WE. However, the impacts on this wetland will be minimised where mitigation measures are implemented to protect water quality.

9.6 Creek Diversions

Creeks are not expected to be diverted. However, where water diversions are required, and incorporate watercourses, poorly designed diversion channels have the potential to impact on fish habitats and movement / migration, which in turn could affect the fisheries productivity of the catchment upstream. The aquatic plants and animals that inhabit each of the creeks that might be diverted are generally tolerant of a range of habitat and water quality. If diversion channels on watercourses are well engineered to maintain fish passage and replicate the aquatic habitat found in the natural creeks, the loss of some natural ephemeral watercourses is highly unlikely to result in the loss (even locally) of any species of aquatic plants or animals.

The construction of diversion channels will require clearing and disturbance, which provides the potential for increased soil erosion and sedimentation (the impacts of which have been discussed). Therefore, there is a high potential for adverse effects resulting from soil erosion and sedimentation in these areas of disturbance, potentially leading to high turbidity in the diversion channels and natural creeks downstream.

Diversion of flows from the existing channels to the completed diversion channels may leave fish and other aquatic animals such as macrocrustaceans stranded. Relocation of

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aquatic animals may be required prior to the diversion of channels, where water is present.

9.7 Changes to Flow Regimes

Changes to the flood regime, and the timing and magnitude of flows in watercourses, have the potential to impact on aquatic ecology. However, changes in flow regimes as a result of water management for the BHS project are only expected to be minor in the context of the high seasonal variation that occurs naturally in the area.

Where adequate fish passage is maintained, no impacts to fish communities are expected to occur due to altered flows. A reduction in flows to the creeks as the result of the water management strategy or the loss of catchment area has the potential to impact on the flushing of water through the creeks and on water quality. This could have an impact on the abundance and diversity of aquatic plant, macroinvertebrate and fish populations within the creeks of the BHS project area. However, releases of mine-affected water, in accordance with conditions in the Environmental Authority, will contribute to maintaining the natural flow regime (refer to section 10.4).

9.8 Creek Crossings

Creek crossings may be required to be constructed for light vehicle access road and haul road crossings of creeks.

Currently, most creek crossings in the BHS project area are dirt fords. These existing crossings have a high potential for erosion, which can increase sediment run-off into creeks and increase turbidity. Existing ford crossings are also likely to restrict fish passage in low-flow conditions.

Construction of Creek Crossings

Construction of new permanent and temporary crossings may disturb sediments, leading to increases in localised turbidity and sediment deposition. When construction is carried out during the dry season, these impacts will be minimal or absent, although a highly localised loss of aestivating crustaceans may be expected within the construction footprint. The impacts of disturbance to habitat will be highly localised and are considered acceptable in both a local and regional context, given the existing disturbed nature of the creeks. However, after the installation of crossings, the newly formed bed and banks may

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continually erode, given the high flows that occur in the region in the wet season. This may result in an increase in channel width and a loss in channel definition, which could in turn lead to a decrease in downstream flow.

When construction of creek crossings is carried out during the wet season, there will be an impact to fish passage during construction activities, and also potentially to water quality. If the waterway holds water, isolation of the work area may leave fish and other aquatic animals (e.g. turtles) stranded. These aquatic animals will need to be relocated before the start of these construction activities.

Obstruction of Fish Passage

Stream crossings can create waterway barriers that prevent or impede movements of aquatic animals (e.g. fishes and turtles). Many of the native fish of ephemeral systems in western Queensland migrate upstream and downstream and between different habitats during particular stages of their life cycle. Fish passage is already restricted in creeks within the survey area by constructed fords, and poorly designed crossings have the potential to further restrict fish movement in the catchment.

9.9 Matters of National Environmental Significance

The Great Barrier Reef World Heritage Area and the Shoalwater and Corio Bay Ramsar sites are unlikely to be impacted by the BHS project, as they are over 300 km downstream of the BHS project area, and water quality and flows that far downstream are not likely to be impacted.

The Fitzroy River turtle and the estuarine crocodile were not caught in the current seasonal surveys, and are not expected to occur in the survey area due to a lack of suitable habitat. Implementation of the site water management system will mean that downstream habitat for this species will not be impacted. The BHS project is therefore unlikely to impact on this species.

In summary, the BHS project is not likely to impact on matters of national environmental significance with respect to aquatic ecology.

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10 Mitigation Measures

10.1 Operation and Maintenance of Vehicles and Equipment

Risks associated with the spillage of fuels and other contaminants can be substantially reduced, if not eliminated, where:

• vehicle maintenance areas, portable refuelling stations and storage of fuels, oils and batteries are undertaken within bunded areas that are designed and constructed in accordance AS1940 (1940-2004) – The storage and handling of flammable and combustible liquids and are above the Q100 flood level of nearby waterways and dams

• appropriate spill containment kits are available, and used for the clean up of spills in the field. The kits should contain equipment for clean up of both spill on land or in dry creek beds, and spills to water (such as floating booms), and

• a management system is in place for all spills of contaminants, including reporting spills to the Environmental Officer (or delegated person).

10.2 Vegetation Clearing and Earthworks

The risk of sediment run-off to nearby waterways will be reduced where:

• an erosion and sediment control management plan is developed and implemented, and is reviewed regularly

• sediment dams are constructed before vegetation clearing and earthworks

• vegetation clearing and earthworks are done in stages over the life of the mine, and

• timing of clearing and earthworks for construction of creek crossings or diversions is done in the dry season and when creeks are dry, if possible.

During and after construction activities, water quality and ecosystem health of nearby waterways may be protected by:

• erosion control (e.g. jute matting, rock mulching, or similar)

• contour banks, ditches or similar formed across cleared slopes to direct run-off towards surrounding vegetation and away from creeks

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• monitoring creek water quality of creeks downstream of clearing and / or exposed soil, during periods of rainfall, and

• rehabilitation of the landscape, focusing on the:

− salvaging of clumps of native grass, shrubs and trees before clearing

− use of native vegetation of local provenance for replanting where possible, and

− replanting along the margins of creeks following construction of the creek crossings. The width of the replanted riparian vegetation should be equal or greater than the width of existing riparian vegetation. Planted trees in the riparian zone should provide canopy cover and have root systems that can stabilise the banks and the disturbed area.

10.3 Management of Water Resources

Water resources will be managed through the implementation and continuous refinement of a Site Water Management Plan, with regard to the Model Water Conditions for Coal Mines in the Fitzroy Basin (March 2013) / Environmental Authority conditions. Site drainage will be constructed to maximise non mine-affected water catchments and minimise mine-affected water catchments for collection and containment of water. Collected water will be used in dust suppression management and processing of the resource. Water quality sampling at the existing mine site water storages also indicates that the quality of stored site water is suitable for use in irrigation and stock watering. The main components of the proposed mine site water management system are:

⋅ two new mine water dams with a total capacity of 770 ML to allow the collection of mine-affected water

⋅ pit sumps that collect pit water and allow it to be pumped to the mine water dam

⋅ low wall pit dewatering pumps and a ramp dam to allow the open cut pit to be dewatered and discharged to the mine water dam

⋅ sediment dams to allow run-off from the rehabilitated areas to be treated and discharged to Campbell Creek and the Unnamed Gully

⋅ a transfer pipeline to allow excess mine water to be pumped to Lake Gasteen or to supply water to the mine water dams for use on the site when required, and

⋅ water fill points linked to the mine water dam to allow mine-affected water to be used for dust suppression.

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All dams and levees will be constructed in accordance with the Manual for Assessing Hazard Categories and Hydraulic Performances of Dams (February 2012), with an appropriate dam storage allowance. The proposed water management system will adequately manage the potential impacts to aquatic ecology.

10.4 Loss of Catchment Area

Controlled discharges from the site will coincide with natural flows, in accordance with the Model Water Conditions for Coal Mines in the Fitzroy Basin (March 2013), which may help to mitigate the impacts of a loss of catchment area and streams (where water quality meets the release criteria defined in the Environmental Authority). Impacts may also be mitigated through long-term remediation of the catchment in the BHS project area, including reinstatement of some gullies and drainage lines to direct run-off from rehabilitated areas.

10.5 Loss of On-site Dams and Wetlands

Fish and other aquatic animals (such as macrocrustaceans and turtles) may be stranded if dams and wetlands within the BHS project area are destroyed; however, this is not expected to occur. If there is going to be any loss of on-site dams and wetlands, including wetlands that have been mapped as having high ecological significance, stranded fish, macrocrustaceans and turtles should be caught and translocated to waterholes downstream of the wetlands, or to other dams and wetlands, in accordance with the Fish Salvage Guidelines, as summarised below:

• animal salvage should be in the cooler months if possible, to minimise stress to the aquatic animals (aquatic animals are less active in the cooler months)

• salvaged aquatic animals should be translocated to suitable waterholes in the Callide Creek subcatchment (to prevent the transfer of exotic fish or aquatic disease)

• fish, macrocrustaceans and turtles should be caught using gear appropriate to the waterways and species present (at the site, this is likely to include electrofishing, cast nets, seine nets and set traps), and

• aquatic animals should be handled, transported and released so as to minimise damage to the fish (e.g. handle with wet hands and hold correctly).

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Various apparatus used to catch and / or translocate fish will require a General Fisheries Permit, issued by Fisheries Queensland, and should be operated by appropriately experienced professionals.

No specific offset polices for freshwater wetland habitat exist; however, consideration could be given to the protection and rehabilitation of the nearby mapped wetland management area (site CC-WE). This could include:

• not undertaking mining or related activities within the wetland management trigger area

• preventing cattle access to the wetland (e.g. fencing)

• removal of weeds, and

• planting of riparian and edge vegetation (e.g. native sedges).

10.6 Creek Diversions

To effectively mitigate the loss of on-site aquatic and riparian habitat, any diversions should be designed and constructed to provide bed and bank habitat of a similar character to that of natural watercourses within the region. Key considerations are:

• the diversion of a low-flow channel should provide a stable, sinuous channel, of dimensions similar to the existing natural channel, and that will maintain a similar flow to the existing natural channel

• the design and construction of in-stream habitat using boulders, logs and branches from vegetation clearing, as appropriate (Brooks et al. 2006)

• diversions should only be opened to flows once geotechnical stability and vegetation requirements have been satisfactorily established

• diversions should be designed to avoid design velocities in excess of 1 m / s as far as practical, and

• where possible, diversion channels should only be initially opened to flows in the dry season (May to September).

Suggested Habitat Features of the Diversions

Habitat features of Callide Creek and its tributaries should be replicated in the design of diversion channels, if required, including:

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• engineered structural features such as boulders and jams of large woody debris, as appropriate

• trailing bank vegetation (e.g. from grasses and sedges planted on the edge of the low-flow channel)

• a diversity of substrate type, as appropriate, and

• isolated pools to provide habitat diversity.

The upper banks should be revegetated with large growing eucalypt species to stabilise banks and provide shading and woody debris to the channel; and native trees, shrubs, sedges and rushes should be planted along the lower banks to provide habitat during periods of flow.

Stranding of Fish and Other Aquatic Animals

Opening diversion channels in the dry season (May to September) will minimise the number of fish that are likely to become stranded in any refuge pools in those sections of any creeks to be diverted. Once flow is diverted from the existing channel, stranded fish should be caught and translocated to waterholes downstream of the diversion channels in accordance with the Fish Salvage Guidelines.

Changes to Flow Regimes

Where possible, the diversion channels should be designed such that natural in-stream flow velocities are not exceeded. Design features that will reduce flows in the diversion channels include the incorporation of:

• in-stream habitat structures (e.g. large woody debris and boulders), to baffle flows

• bends and meanders

• variations in water depth, including regular deep pools, and

• dense riparian vegetation, to buffer against overland flows into the diversion channel.

The impacts of increased flow velocities on erosion, and subsequently aquatic ecology, will also be reduced where erosion control measures are implemented for the diversion channels.

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10.7 Creek Crossings

Impacts associated with the construction of permanent creek crossings by roads and pipelines will be minimised if:

• construction is undertaken during the dry season (minimising the likelihood of rainfall and run-off carrying sediment and other pollutants into the creeks), and

• stormwater and erosion control measures are implemented.

Where construction is undertaken during the wet season, impacts associated with the construction of road and pipeline crossings will be minimised if (AE 2001; APIA 2009):

• the workspace is isolated, irrespective of if there is an isolated pool or flowing water; the isolation should be designed such that it is completed within one work-day, to minimise the impact on aquatic animals

• upstream and downstream dams are installed on the edge of the temporary workspace, to maximise the area of the workspace; these dams should:

− be constructed of an appropriate material for each creek (e.g. steel plates, flumes, sand bags or aqua dam)

− be made impermeable by using polyethylene liner and sand bags

• where flowing water is present, 100% of this flow is maintained downstream by using appropriately sized pumps

• pump intakes are screened, with openings no larger than 2.54 mm, to ensure that no fish are trapped

• fish are salvaged from the isolated workspace and translocated to appropriate waterways

• the upstream dam is slowly removed, to allow water to flush the sediment from the workspace area

• sediment-laden water is pumped into sumps or onto vegetation, and

• the operation of the clean-water pump to sustain flow below the downstream dams is continued until the downstream dam is removed.

Obstruction of Fish Passage

Where culverts are used, their design and installation can significantly influence fish passage (Section 11.1). It is recommended that Fisheries Queensland be consulted

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during stream crossing design and the development of maintenance regimes, and that they are designed in accordance with Fish Habitat Guideline FHG 001, Fish Passage in Streams, Fisheries Guidelines for Design of Stream Crossings (Cotterell 1998), which states that culverts should be designed such that they are:

• at least 100 m from any other waterway barrier on the creek (e.g. road crossing or dam) in order to minimise the cumulative effects of fish barriers

• as short (along the length of the stream) and as wide (across the stream channel) as possible, while being designed to allow the passage of anticipated flood volumes and associated debris, and to allow enough water depth within the culvert to facilitate fish movement (estimated to be >0.3 m deep during flow periods for the fish species likely to be present)

• open-bottomed if possible, to retain the natural morphological features of the stream. If this is not possible, culverts should be countersunk below the stream bed and natural materials such as rocks secured to the base of the culvert to increase roughness and reduce water velocity (velocities of >1 m/s will likely impede all fish passage)

• constructed without a drop-off at the culvert outlet, as this impedes fish migration upstream

• constructed with minimum disturbance to the outer banks on stream bends, as these are usually the most unstable and prone to erosion, and

• surrounded by riparian vegetation (that is planted after construction if necessary) to stabilise banks, provide food and habitat for aquatic animals, and prevent predation of aquatic animals by birds.

Impacts to in-stream habitat and aquatic plants and animals will be minimised where culverts are:

• installed at the driest time of year (preferably in the dry creek bed, avoiding pools). During the wet season, impacts may be minimised where isolation methods are adopted in accordance with the guidelines in this report, and

• maintained, and there is regular removal of debris or plant growth, which can impede fish passage (Cotterell 1998).

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10.8 Monitoring Requirements

Receiving Environment Monitoring Program

The monitoring of aquatic ecosystems is proposed as a part of a receiving environment monitoring program (REMP), to:

• monitor the impacts of the BHS project (including diversions and water releases) on downstream waterways

• inform the continual improvement of the mine’s Environmental Management Plan, and Plan of Operations, and

• trigger the requirement for remedial action should an impact be detected.

The REMP should be designed to detect changes to both the physical environment and to plant and animal communities of the waterways and focus on aquatic habitat and macroinvertebrates as indicators.

In summary, the aims of the REMP will be to:

• describe the background condition of waterways in the receiving environment, including a description of the background (i.e. without impacts from mining) condition

• describe the EVs and WQOs of the receiving environment

• determine compliance of water quality in the receiving environment with the relevant WQOs, and discuss potential causes for non-compliance and potential effects on EVs, and

• determine site-specific background values for the receiving environment within two years of the implementation of the REMP.

The REMP will:

• include monitoring of aquatic habitat and macroinvertebrates as key indicators

• incorporate a statistically-robust, quantitative design in order to reliably describe background condition and detect impacts

• be approved by the administering authority before implementation, and

• be implemented by qualified aquatic biologists.

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Monitoring of Creek Diversions

If creek diversions are required, a monitoring program should be implemented to confirm that the diversion channels are providing adequate connectivity between natural creek habitat upstream and downstream of the BHS project area (i.e. they are maintaining adequate fish passage).

A fish monitoring program should be designed and implemented by an appropriately qualified professional, but in summary it should consider the following:

• monitoring at the proposed monitoring sites outlined in the REMP

• completion of at least two baseline surveys before commissioning of the diversion channel, and at least two surveys after commissioning of the diversion channel (with the need for further surveys to be determined based on the results)

• survey of fish using gear types appropriate to the conditions at each site. This may involve the use of one, or a combination of, the following gear types:

− backpack or boat electrofishing units

− seine nets (~10 mm mesh size)

− gill nets (75 mm and 150 mm mesh)

− baited traps (2 mm and 20 mm mesh), and

− dip nets (2 mm mesh).

• at each site, the species caught and the abundance of each species by life-history stage (juvenile, intermediate, adult) should be recorded, along with the apparent health of individuals; specimens that cannot be identified in the field should be euthanised and returned to the laboratory for identification, and

• the richness, total abundance, abundance of key species, and abundance of each life-history stage should be compared between sites, using statistical analyses where appropriate.

General Fisheries and Animal Ethics permits will be required to complete the monitoring.

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11 Risk Assessment

11.1 Methods

Based on the outcomes of the desktop study and field surveys, aquatic ecology receptors that have the potential to be impacted by the Spring Gully Development were identified. The value of each aquatic ecology attribute was identified, along with the magnitude of each potential impact to these attributes, were defined in accordance with the criteria outlined in Table 11.1 and Table 11.2.

Risks to aquatic ecology values as a result of the Spring Gully Development on each aquatic ecological value have been assessed based on the determined value and magnitude of impact. Table 11.3 illustrates how the significance of a potential impact was derived.

Table 11.1 Value criteria for aquatic ecology attributes.

Value Definition

very high ⋅ an internationally important site (e.g. Ramsar wetland, or a site considered worthy of such designation)

⋅ a regularly occurring population of an internationally important species

⋅ a nationally designated site (e.g. Wetland of National Significance)

⋅ smaller areas of habitat which are essential for maintaining the viability of a larger whole area of national significance

⋅ areas of habitat that may support nationally important species listed under the Environment Protection and Biodiversity Conservation Act 1999 (EPBC Act).

⋅ aquatic species or communities listed under the EPBC Act

high ⋅ habitat of state significance (e.g. wetlands of high ecological significance in the Great Barrier Reef catchments)

⋅ aquatic species or communities listed under Queensland’s Nature Conservation Act 1992

⋅ aquatic habitat, species or communities that are rare or have a high conservation priority species within Queensland.

⋅ aquatic species or communities that are considered ‘iconic’ species within Queensland or Australia (e.g. platypus)

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Value Definition

medium ⋅ aquatic habitat or site designated by a local authority as having local conservation status

⋅ aquatic habitat or species that has importance at a catchment-scale, e.g. refuge habitat or fish breeding habitat

low ⋅ aquatic habitat not specifically protected under state or national legislation, but that supports native aquatic flora and fauna

⋅ common or widespread aquatic species or communities within the region that are not specifically protected under state or national legislation and that are relatively tolerant of a wide range of environmental conditions

negligible ⋅ common or widespread aquatic habitat within the region that is highly disturbed and rarely supports aquatic flora and fauna

⋅ highly disturbed aquatic communities, e.g. that are affected by pollution or invasion of exotic species

Table 11.2 Thresholds for magnitude of impact for aquatic ecology receptors.

Magnitude of Change

Definition

major ⋅ permanent or long-term effect on the extent or integrity of a habitat, a species or a community

⋅ likely to result in a direct effect on a habitat or a species, including mortality of a high value species that affects the viability of the population

⋅ likely to threaten the sustainability or conservation status of a habitat, a species or a community

⋅ if beneficial, likely to enhance the sustainability or conservation status of a habitat, a species or a community

moderate ⋅ permanent or long-term effect on the extent or integrity of a habitat, a species or a community

⋅ likely to result in direct effect on a habitat or a species that does not affect the viability of the population

⋅ unlikely to threaten the sustainability of a habitat, a species or a community

⋅ if beneficial, likely to enhance the sustainability of a habitat, a species or a community

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Magnitude of Change

Definition

minor ⋅ medium or short-term reversible effect on a habitat, a species or a community

⋅ may be a small but measurable indirect impact on an aquatic habitat or on a native aquatic species or community

⋅ will not threaten the sustainability of a significant habitat, species or native aquatic community

negligible ⋅ no direct impact to an aquatic habitat or a species

⋅ short-term and reversible indirect effect on habitat that is unlikely to lead to impacts on habitat integrity or a native aquatic community

no change ⋅ no direct or indirect impacts to aquatic ecology

Table 11.3 Matrix used to estimate the significance of potential impacts after mitigation.

Significance of Effect

Magnitude of Change

Major Moderate Minor Negligible No change

Attribute Value

Very high Very Large Large/Very Large

Moderate/ Large

Slight Neutral

High Large/Very Large

Moderate/ Large

Slight/ Moderate

Slight Neutral

Medium Moderate/ Large

Moderate Slight Neutral/ Slight

Neutral

Low Slight/ Moderate

Slight Neutral/ Slight

Neutral/ Slight

Neutral

Negligible Slight Neutral/ Slight

Neutral/ Slight

Neutral Neutral

Note: Shaded boxes indicate a significant effect in terms of EIA. Where a choice of two impact significance descriptors is available, only one should be chosen. This allows for professional judgement and discrimination in assessing impacts.

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11.2 Impact Assessment

Table 11.4 shows the risk assessment for potential impacts to aquatic fauna associated with the BHS project. Based on the impact assessment presented above, the following activities have the potential to result in significant impacts to aquatic ecology without mitigation and management:

⋅ fuel and contaminant spills to watercourses and wetlands

⋅ litter and waste entering high ecological significance wetlands

⋅ vegetation clearing and earthworks, resulting in increased turbidity and sedimentation

⋅ water management, including controlled and uncontrolled releases of mine-affected water, and

⋅ obstruction of fish passage as a result of constructing diversion channels and road crossings.

However, once mitigation measures are implemented, all residual impacts are considered to be slight, and are not considered to be significant impacts in accordance with the impact assessment methodology described in Section 11.1.

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ith th

e M

anua

l for

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essi

ng H

azar

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orie

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d H

ydra

ulic

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of

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ary

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with

an

ap

prop

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sto

rage

allo

wan

ce)

no o

vera

ll de

crea

se

in w

ater

qua

lity

min

imis

e im

pact

s to

aq

uatic

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itat

and

nativ

e aq

uatic

flo

ra

and

faun

a sp

ecie

s

negl

igib

le

slig

ht

⋅

decr

ease

d ha

bita

t fo

r aq

uatic

fa

una

from

co

nstru

ctio

n of

cro

ssin

gs o

r div

ersi

ons

⋅ w

orks

are

don

e in

sta

ges

over

the

life

of th

e m

ine

⋅ co

nstru

ctio

n of

cro

ssin

gs in

acc

orda

nce

with

Env

ironm

enta

l Aut

horit

y co

nditi

ons

and

best

pra

ctic

e gu

idel

ines

⋅ if

requ

ired,

cat

chin

g an

d tra

nslo

catin

g st

rand

ed a

quat

ic f

auna

in a

ccor

danc

e w

ith t

he

Fish

Sal

vage

Gui

delin

es

⋅ cr

ossi

ngs

are

desi

gned

in

acco

rdan

ce w

ith F

ish

Hab

itat

Gui

delin

e FH

G 0

01 –

Fis

h P

assa

ges

in S

tream

s, F

ishe

ries

Gui

delin

es fo

r D

esig

n of

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am C

ross

ings

(C

otte

rell

1998

)

⋅ of

fset

s im

plem

ente

d w

here

pra

ctic

able

no

loss

of

H

EV

ha

bita

t ne

glig

ible

ne

utra

l

frc e

nviro

nmen

tal

Bou

ndar

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ill E

xpan

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EIS

: Aqu

atic

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logy

13

1

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atic

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A

ttrib

ute

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ntia

l Im

pact

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itiga

tion

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agem

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col

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agni

tude

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nge

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r M

itiga

tion

Res

idua

l Im

pact

⋅

chan

ges

to f

low

reg

ime

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may

affe

ct f

auna

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clud

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fish

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ding

cue

s)

⋅ w

orks

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don

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sta

ges

over

the

life

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ine

⋅ co

nstru

ctio

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danc

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an

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prop

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rage

allo

wan

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⋅ im

plem

enta

tion

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cont

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us re

finem

ent o

f a S

ite W

ater

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agem

ent P

lan

⋅ co

ntro

lled

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es t

imed

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ural

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ce w

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el W

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or C

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n th

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emed

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inst

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ome

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ial

chan

ge

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am

flow

re

gim

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⋅

fuel

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ican

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ills

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achi

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ilabl

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⋅ a

man

agem

ent s

yste

m is

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lace

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ll sp

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atio

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ater

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ditio

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horit

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vees

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ht

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ease

d ha

bita

t fo

r aq

uatic

fa

una

thro

ugh

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ct lo

ss o

f hab

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sion

⋅

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rosi

on a

nd s

edim

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ontro

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dev

elop

ed a

nd im

plem

ente

d

⋅ di

vers

ions

sho

uld

be d

esig

ned

and

cons

truct

ed to

pro

vide

hab

itat o

f sim

ilar

char

acte

r to

that

of n

atur

al w

ater

cour

ses

in th

e ar

ea

⋅ cr

ossi

ngs

are

desi

gned

in

acco

rdan

ce w

ith F

ish

Hab

itat

Gui

delin

e FH

G 0

01 –

Fis

h P

assa

ges

in S

tream

s, F

ishe

ries

Gui

delin

es fo

r D

esig

n of

Stre

am C

ross

ings

(C

otte

rell

1998

)

no lo

ss o

f ha

bita

t or

in

crea

se i

n er

osio

n an

d tu

rbid

ity

negl

igib

le

slig

ht

⋅

incr

ease

d tu

rbid

ity a

nd s

edim

enta

tion

and

inpu

t of

nu

trien

ts

or

othe

r co

ntam

inan

ts

from

ve

geta

tion

clea

ring

and

earth

wor

ks

⋅ an

ero

sion

and

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imen

t con

trol p

lan

is d

evel

oped

and

impl

emen

ted

⋅ co

nstru

ctio

n is

und

erta

ken

in t

he d

ry s

easo

n or

app

ropr

iate

man

agem

ent

proc

edur

es

are

impl

emen

ted

in th

e w

et s

easo

n

⋅ se

dim

ent d

ams

are

cons

truct

ed b

efor

e w

orks

beg

in

no c

onta

min

atio

n of

na

tura

l w

ater

cour

ses

negl

igib

le

slig

ht

frc e

nviro

nmen

tal

Bou

ndar

y H

ill E

xpan

sion

EIS

: Aqu

atic

Eco

logy

13

2

Aqu

atic

Eco

logy

A

ttrib

ute

Pote

ntia

l Im

pact

M

itiga

tion

/ Man

agem

ent P

roto

col

Obj

ectiv

e M

agni

tude

of

Cha

nge

Afte

r M

itiga

tion

Res

idua

l Im

pact

⋅

obst

ruct

ion

of fi

sh p

assa

ge

⋅ if

requ

ired,

cat

chin

g an

d tra

nslo

catin

g st

rand

ed a

quat

ic f

auna

in a

ccor

danc

e w

ith t

he

Fish

Sal

vage

Gui

delin

es

⋅ cr

ossi

ngs

are

desi

gned

in

acco

rdan

ce w

ith F

ish

Hab

itat

Gui

delin

e FH

G 0

01 –

Fis

h P

assa

ges

in S

tream

s, F

ishe

ries

Gui

delin

es fo

r D

esig

n of

Stre

am C

ross

ings

(C

otte

rell

1998

)

min

imis

e im

pact

s to

aq

uatic

hab

itat

and

nativ

e aq

uatic

flo

ra

and

faun

a sp

ecie

s

negl

igib

le

slig

ht

frc environmental


12 Cumulative Impacts

Cumulative impacts of the BHS project on aquatic ecosystems were considered in relation to the surrounding land uses and other major projects underway or planned in the local area.

The lands surrounding the BHS project are predominately used for agricultural activities, dominated by grazing and limited cropping in the low lying areas (Henderson 2000). The BHS project area and its surrounds have been considerably modified as part of past land use practices over a period of more than 100 years.

A number of mining projects are located within the Fitzroy Basin; however, only the existing Callide Mine is within the immediate area of the BHS project. Other projects in the region that may affect aquatic ecology include the coal seam gas pipeline projects, developed to transport coal seam gas to Gladstone.

Each of these Projects have the potential to impact aquatic ecology from activities such as vegetation clearing, earthworks (grading, trenching and excavating), and construction of creek crossings. The existing Callide Mine also has the potential to impact aquatic ecology through potential contamination of water due to planned and un-planned water releases.

However, where the appropriate mitigation measures are in place, it is considered unlikely that the BHS project will result in a significant increase in cumulative adverse impacts on aquatic ecosystems when compared to the impacts expected from existing mining projects in the region and on-going regional agricultural activities (Section 11.1).

frc environmental


13 Conclusions

The current condition of freshwater aquatic ecosystems within the BHS project area is generally moderate and is consistent with the ecological condition of aquatic ecosystems throughout the wider catchment. Water quality measured in situ was moderate in the current seasonal survey, and was characterised by low pH and a low percent saturation of dissolved oxygen; however, electrical conductivity was generally above the high flow WQO and turbidity was generally below the WQO. Land use in the survey area included low intensity grazing, which is consistent with the land use of the wider Fitzroy Basin.

Aquatic biodiversity was moderate, with low diversity and cover of aquatic plants and fish, which is typical of the ephemeral waterways in the region. Macroinvertebrate indices were typically lower than those at sites monitored by DNRM and were generally below the WQOs. This is likely to be due to DNRM sites being located on more permanent watercourses. All sites were situated in quadrant 3 of the SIGNAL 2 / family bi-plot, which indicated industrial or agricultural pollution. The macroinvertebrate and fish communities present were tolerant of the varying and often harsh conditions that characterise ephemeral and intermittent streams, such as those within the BHS project area.

The freshwater waterways of the survey area may provide breeding and dry-season refuge habitat to macroinvertebrates and fish, and as such, are likely to contribute to the success of downstream populations through movement and / or migration. However, it is more likely that the downstream sites in this survey (e.g. site CBC-DS2) will be used for breeding and refuge, as they are more likely to retain water.

No listed species (under state or Commonwealth legislation) of aquatic plants or animals have been recorded from, or are likely to occur in, the freshwater waterways of the BHS project area.

The following components of the BHS project may have the potential to impact on aquatic ecology:

• construction of the new open-cut mine and associated operations

• construction of the haul road north from the new pit

• construction of new overburden area

• construction of

Of the potential impacts, the construction of the open-cut mine and haul road may result in the greatest impact to the aquatic environment. These impacts can be minimised through

frc environmental


appropriate design of waterway crossings and potentially through creek diversions. The potential impacts of the other components can be minimised if the recommended mitigation measures are implemented.

The BHS project is unlikely to impact on any listed vulnerable or endangered aquatic species or ecological communities, as listed under state or Commonwealth legislation, or habitats of conversational significance, if appropriate mitigation measures are put in place.

This risk assessment demonstrates that there will only be a slight impact to the local aquatic environments of the BHS project, and negligible regional impacts. Monitoring, which may include the use of biological indicators such as macroinvertebrates, may be required during the construction and operation of the mine to determine the impact on water quality and the aquatic ecology, if any. This monitoring would inform adaptive management of the Boundary Hill mine, but an extensive program is unlikely to be required given the nature of the watercourses and the minimisation of impacts through mitigation.

frc environmental


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frc environmental


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frc environmental


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