The State of Fish Communities Across the Eastern Mount Lofty Ranges: Condition Reporting from 2010 to 2013

The state of fish communities across the Eastern Mount Lofty Ranges: condition reporting from 2010 to 2013

Nick Whiterod and Michael Hammer

A report to the South Australian Murray-Darling Basin Natural Resources Management Board

November 2014

This report may be cited as: Whiterod, N. and Hammer, M. (2014). The state of fish communities across the Eastern Mount Lofty Ranges: condition reporting from 2010 to 2013. Report to the South Australian Murray-Darling Basin Natural Resources Management Board. Aquasave - Nature Glenelg Trust, Goolwa Beach, South Australia.

Correspondence in relation to this report contact

Nick Whiterod Senior Aquatic Ecologist Aquasave - Nature Glenelg Trust MOB: 0409023771 [email protected]

Disclaimer

Although reasonable care has been taken in preparing the information contained in this publication, neither Aquasave – Nature Glenelg Trust, nor the South Australian Murray-Darling Basin Natural Resources Management Board accept any responsibility or liability for any losses of whatever kind arising from the interpretation or use of the information set out in this publication.

State of fish communities across the EMLR, 2010 to 2013

ACKNOWLEDGEMENTS

Thanks to Mardi van der Wielen of the South Australian (SA) Department of Environment, Water and Natural Resources (DEWNR) for continued support and commitment to the fish monitoring program and funding the various components of the present study. Numerous people assisted with field monitoring (including Tom Barnes, Craig Kemp, Leanne Piller, Dylan Sortino, Mel Tucker and Cory Young over the present reporting period), and many landholders provided access to sites on their property and offered valuable insights into local conditions. Some data presented was obtained through data-sharing arrangements with Chris Bice (SARDI), Kate Mason (DEWNR), Scotte Wedderburn and Tom Barnes (University of Adelaide). The report was improved through comment by Mark Bachmann and Sylvia Zukowski (Nature Glenelg Trust). Thanks to Brett Ibbotson (DEWNR) for discussion and comment during the finalisation of the report. All sampling was undertaken in accordance with relevant South Australian permits (namely, PIRSA Fisheries research permits).

State of fish communities across the EMLR, 2010 to 2013

EXECUTIVE SUMMARY

The temporary streams of the Eastern Mount Lofty Ranges (EMLR), which contribute tributary flows at the terminal end of the Murray-Darling Basin (MDB), provide important habitat for a range of freshwater fishes. The understanding and provision of environmental water requirements (EWR) for different fish functional groups provides a solid base for sound and sustainable catchment management, ecosystem protection and biodiversity conservation. A long-running fish monitoring program aims to provide empirical knowledge in support of EWR initiatives in the region. The outcomes of this monitoring program are used to provide assessment of the condition of identified fish-related ecological assets using presence, recruitment and survivorship indicators (for single species) as well as indicators relating to diverse fish communities. This condition assessment has been undertaken in 2007, 2009 and now 2013, which is the focus of the present study. This present assessment includes enhancement toward a more objective assessment of condition.

The last condition assessment conducted in 2009 coincided with a period of critical water shortage associated with the millennium drought and serious aquatic ecosystem impacts were noted. The terminal wetland reach type was the most severely impacted through habitat loss, being virtually eliminated from the region. In other reach types there was a mix of both: (a) severe degradation or loss of refuge pools and ecological assets, and (b) some persistence of habitat types and species. Catchments of the region were deemed to be in either poor or moderate condition at this time.

During 2010-11, broad-scale rainfall led to improved regional water availability and stream flow in the EMLR. Given the severity of the millennium drought, it is now particularly important to provide an updated condition assessment for the post-drought period, during a time when fish populations are expected to exhibit characteristics of recovery. Hence the present report details monitoring data from 2010 to 2013, which includes a total of 232 site assessments across 10 stream catchments. Over this period, some 60,000 fish were recorded from 28 species (including 22 native and six alien species). Of note, threatened freshwater specialists, namely Yarra pygmy perch, remain absent from the region and the alien Gambusia dominated.

The performance of fish-related ecological assets over the reporting period, are compared with the 2009 assessment in each individual catchment and reach in Section 3 of the report. Overall, six out of 10 catchments are now in equal or better condition when compared to the last reporting period, although greater recovery was anticipated and many fish-related ecological assets remain under

State of fish communities across the EMLR, 2010 to 2013 stress (or remain absent). Indeed, all catchments are still classified as poor or moderate condition (although mid and upper reaches are faring comparatively better) at the end of the reporting period summarised here (Table i).

Table i. 2013 overall status of reaches and catchments of the EMLR – a comparison of the reach and catchment level performance against fish indicators between 2009 and 2013. Condition scores (out of 9) are defined as good (>6, xxx), moderate (3 to 6, xxx) and poor (<3, xxx). Reaches are headwaters (HW), upper pool-riffle (UC), mid pool-riffle (MC), gorge (GO), lowland (LO) and terminal wetlands (TW) with reaches not sampled highlighted (with n/s). See section 2.6 for full explanations. Condition Reach Overall No Catchment HW UC MC GO LO TW 2013 2009 1 Angas n/s 8.5 4.5 n/s 5.0 1.5 4.8 4.0 2 Bremer n/s 1.0 n/s n/s 3.0 3.0 3.0 1.0 3 Currency n/s 3.0 7.0 n/s 3.5 3.5 3.5 3.5 4 Finniss n/s 8.5 3.8 n/s 1.0 3.0 4.0 4.3 5 Inman n/s n/s 3.5 n/s n/s n/s 3.5 6.0 6 Marne n/s 7.5 0.0 0.0 2.0 n/s 1.0 0.0 7 Reedy n/s n/s 3.5 4.5 2.0 n/s 3.5 2.5 8 Salt, Premimma & Rocky Gully n/s n/s n/s n/s n/s 1.0 1.0 2.5 9 Saunders n/s n/s n/s n/s 2.0 n/s 2.0 0.0 10 Tookayerta n/s n/s 3.0 n/s 3.0 3.5 3.0 4.0

2013 n/s 7.5 3.5 2.3 2.5 3.0 3.3 2009 n/s 3.0 4.3 1.6 3.8 0.5 3.0

Notable patterns in each catchment include:

 Angas River – strong persistence and recruitment of mountain galaxias in the upper catchment, but initial recovery of terminal wetlands halted (with southern pygmy perch now absent) and the condition of southern pygmy perch in the mid-catchment declining;  Bremer River – overall improvement (reflecting extremely poor condition in 2009), but mountain galaxias populations have not returned to the upper catchment and river blackfish only persist in pools with ongoing management intervention. Mid and lowland catchment reaches along with the terminal wetlands have moderately recovered;  Currency Creek – mixed patterns, with the mid-catchment performing well but only moderate fish communities in upper and lowland reaches as well as the terminal wetland (and no Yarra pygmy perch present);  Finniss River – Upper catchment in performing very well with strong recruitment and survivorship of mountain galaxias, but mid and lowland reaches in poor condition (no Yarra pygmy perch present);

iii

State of fish communities across the EMLR, 2010 to 2013

 Inman River – condition declined considerably with only one (of three identified) ecological assets performing well. At the other two locations, the collapse of southern pygmy perch populations has been observed;  Marne River – catchment improved (just) but remains in overall poor condition, with the performance of upper catchment mountain galaxias populations the only positive. The gorge and lowland reaches are under considerable stress, with mountain galaxias not recorded since 2008 and the imminent loss of river blackfish expected;  Reedy – slight improvement of some mid and upper catchment mountain galaxias populations, but declines in others, whilst the lowlands and terminal wetlands have benefited from greater water availability;  Rocky Gully – condition of terminal wetland declined as Murray hardyhead appear to have only been temporary post-drought resident;  Saunders – The only identified ecological asset (carp gudgeon) in the catchment, recolonised but numbers are low and recruitment appears lacking; and  Tookayerta – mixed results: continued absence of upper catchment southern pygmy perch and declines of the lowlands but improvement of terminal wetland (although Yarra pygmy perch remain absent). At some mid-catchment locations, populations of mountain galaxias, river blackfish and southern pygmy perch continue to persist strongly.

As an established, long-term program, the EMLR fish monitoring program is well-positioned to track future waterway condition in response to changing flow regimes across the region, whether that be associated with climate change or ongoing water abstraction. In relation to the latter, it is worth emphasising that the impacts of water abstraction have clearly lessened the resilience of fish species in the region through impacts to their habitat. As a result, there continues to be an urgency to implement EWRs under the EMLR Water Allocation Plan (WAP).

TABLE OF CONTENTS ACKNOWLEDGEMENTS...... i EXECUTIVE SUMMARY ...... ii Section 1. INTRODUCTION ...... 1 Section 2. BACKGROUND...... 3 2.1 The Eastern Mount Lofty Ranges ...... 3 2.2 Regional hydrologic trends (2001−2013) ...... 5 2.3 Fish communities of the EMLR ...... 7 2.4 Assessment Framework ...... 13 2.5 EWRs for fish-related ecological assets ...... 14 2.6 Fish monitoring ...... 24 2.7 Reporting process ...... 26 Section 3. STATUS REPORTING ...... 30 3.1 Summary over the reporting period (2010−2013) ...... 30 3.2 Angas Catchment ...... 31 3.3 Bremer Catchment ...... 57 3.4 Currency Catchment ...... 74 3.5 Finniss Catchment ...... 90 3.6 Inman Catchment ...... 120 3.7 Marne Catchment ...... 132 3.8 Reedy Catchment ...... 151 3.9 Rocky Gully, Salt and Preamimma catchments ...... 165 3.10 Saunders Catchment ...... 172 3.11 Tookayerta Catchment ...... 178 Section 4. DISCUSSION ...... 203 4.1 Catchment and reach trends ...... 203 4.2 Fish monitoring recommendations ...... 205 4.3 Reporting process & links with EWRs ...... 206 REFERENCES...... 207

State of fish communities across the EMLR, 2010 to 2013

Section 1. INTRODUCTION

The lower reaches of the expansive Murray–Darling Basin (MDB), Australia are a hotspot for freshwater biodiversity. In particular, the temporary streams of the Eastern Mount Lofty Ranges (EMLR) that flow into the terminal Lower Lakes of the MDB offer diverse stream and swamp habitat, as well as linking habitats between riverine and lake environments, that provide important habitat for a range of freshwater fishes. However, flow regulation and water abstraction, which has led to major reductions in flow volume (critically low flows), seasonality and duration in many EMLR habitats, has significantly impacted over half of the 35 species recorded in the region that are considered threatened (Hammer et al. 2009).

Being reliant on aquatic habitat, freshwater fish are innately linked to the prevailing flow regimes of waterways (Bunn and Arthington 2002; Poff et al. 1997). Thus, an understanding and provision of environmental water requirements (EWRs) that maintain or preserve different fish functional groups provides a solid base for sound catchment management, ecosystem protection and biodiversity conservation (Hammer 2009; VanLaarhoven and van der Wielen 2009). EWRs in this context define the flow regime – magnitude, timing and quality – that allow fish species (and functional groups) persistence through recruitment, survivorship and recolonisation. The development EWRs has been advanced in the EMLR through the documentation of key fish assets and definition of associated EWRs, and through regular assessment to review the status of these assets (Hammer 2007c; Hammer 2009; SAMDBNRM Board 2013; VanLaarhoven and van der Wielen 2009). Most recently, the water allocation plan for the EMLR has set the development of EWRs in a broader context by defining the framework for achieving an equitable balance between environmental, social and economic needs when setting the principles for the taking and use of water (SAMDBNRM Board 2013). Fish-related ecological assets continue to form an integral part of this process.

This report is principally concerned with providing an updated assessment of the condition of identified fish-related ecological assets across the region. The last condition assessment was achieved in 2009 (Hammer 2009) during a period of critical water shortage (2007−2010) associated with the millennium drought (van Dijk et al. 2013), which led to broad-scale loss and drying of a range of aquatic habitats (Kingsford et al. 2011; Mosley et al. 2012). During this period, fish-related ecological assets were placed under stress and many conservation measures were undertaken in an attempt to prevent localised extinctions (Hammer et al. 2013; Lintermans 2013). Over 2010−11, broad-scale

State of fish communities across the EMLR, 2010 to 2013 rainfall led to improved stream flow and the restoration of water levels in the region. Thus, the present assessment is pertinent as it covers the post-drought period, where fish populations are expected to exhibit signs of recovery. To address this question, autumn fish monitoring data from 2010−2013 is used to assess the condition of fish-related ecological assets across the catchments of the EMLR region.

In addition to the status reporting component, this project has also enabled broader analysis of spatial patterns and temporal trends in the fish community between 2001−2013 (see Whiterod et al. in review) and exploration of the links between key fish species and metrics defining flow regimes (see Whiterod et al. in prep) across the region.

State of fish communities across the EMLR, 2010 to 2013

Section 2. BACKGROUND

2.1 The Eastern Mount Lofty Ranges

The Eastern Mount Lofty Ranges (EMLR) is a small (4693 km2), distinct and outlying region consisting of 17 catchments that flow into the terminal reach of the Murray-Darling Basin (MDB) (Figure 2-1). EMLR catchments offer diverse stream and swamp habitats, as well as linking habitats between lake and riverine environments draining into the Lower Murray River and Lower Lakes. Of these 17 catchments, only 11 contain areas of permanent surface water (Hammer 2004) and distinct river reaches, where key features have been delineated; such as: major tributaries, changes in landform, distinct geomorphology and points of regulation (see Hammer 2007c).

The region’s local catchments are influenced by a local Mediterranean type climate with moderate austral winter-spring dominated rainfall and stream flow (VanLaarhoven and van der Wielen 2009). Broader regional climatic zones (semi-arid to wet temperate) in the MDB, with accompanying high seasonal and inter-annual flow variability driven by natural periods of flood and drought, also impact the terminal river reach of the Murray River and Lower Lakes downstream of local EMLR catchments (CSIRO 2007; Walker et al. 1995). The mean annual rainfall across the EMLR region is 463mm, varying from 900mm in the west and south-west to 300mm in the north (CSIRO 2007). Representative long- term (1861−2013) mean annual rainfall for the region (Strathalbyn 489.7mm, station 023747: Bureau of Meteorology, unpublished data) indicates within-year variation is low (e.g. coefficient of variation of 0.21) (Figure 2-2). The mean annual rainfall for the study period (1999−2013, 437.1 mm, coefficient of variation = 0.15) was considerably below the long-term mean.

State of fish communities across the EMLR, 2010 to 2013

Saunders

Marne

Reedy

Salt

Bremer Rocky Preamimma Gully

Angas

Finniss

Tookayerta

Currency Deep

Inman

Figure 2-1. Temporary streams (grey lines) within assessed catchments (black lines) of the Eastern Mount Lofty Ranges (EMLR) at the terminal end of the Murray-Darling Basin (grey shade in insert figure) in south-eastern Australia. Note: The Inman catchment is in the Western Mount Lofty Ranges (WMLR) but included in this assessment due to presence of Southern Pygmy Perch which is unique to catchments in the WMLR and analogous to adjacent catchments in the EMLR.

State of fish communities across the EMLR, 2010 to 2013

1000

800

600

400

200

Mean annual rainfall (mm) rainfall annual Mean

0 1875 1900 1925 1950 1975 2000 Year Figure 2-2. Mean annual rainfall (mm, black line) at Strathalbyn (023747) between 1861 and 2013 showing long-term mean of 488.7mm (grey dashed line) (Bureau of Meteorology, unpublished data).

2.2 Regional hydrologic trends (2001−2013)

The natural flow regime of EMLR rivers incorporates winter and spring peaks in stream flow (VanLaarhoven and van der Wielen 2009), with a mean annual water availability of 120 GL year-1 across the six main catchments (CSIRO 2007). This natural flow regime has been increasingly altered over the past century, predominately through water abstraction to (or by) private dams (CSIRO 2007; SAMDBNRM Board 2013). In 2006, for instance, it was estimated that more than 8000 farms dams (with estimated storage capacity of 22 GL) act to divert 11 GL year-1 of flows; equivalent to 9% of mean annual water availability (across the six main catchments).

The impacts of water abstraction on the EMLR (and southern MDB) were exacerbated by prolonged drought from 1997–2010 (van Dijk et al. 2013), resulting in the loss of baseflow and protracted no- flow conditions (e.g. delayed onset of seasonal flows) (see Figure 2-3). Most alarmingly, critical water shortages from 2007 to 2010 led to significant reductions in water availability and level (see Figure 2-3) and the subsequent deterioration of water quality and drying (and loss) of a range of aquatic habitats across the region (Kingsford et al. 2011; Mosley et al. 2012). Over 2010-11, broad-scale rainfall across the MDB led to significant inflows to the Lower Murray, which led to improved regional

State of fish communities across the EMLR, 2010 to 2013 water availability and stream flow and the restoration of regulated water levels in the Lower Lakes (Hammer et al. 2013). In turn, reduced salinities and the inundation and reconnection of previously dry or isolated habitats was also realised across the region.

Figure 2-3. (a) Representative mean daily flow (ML day−1) for streams of the EMLR, and (b) main daily water level (m, Australian height datum AHD) in Lake Alexandrina (2001−2013). Flow data from Angas River at Weir (station A4260503) gauge; water level data from Lake Alexandrina at Milang Jetty (station A4260524) (DEWNR, unpublished data). Water level where major habitat loss occurred (0.3 m AHD) represented by dashed horizontal line.

State of fish communities across the EMLR, 2010 to 2013

2.3 Fish communities of the EMLR

Summary

In the South Australian section of the MDB, 47 freshwater fish species have been recorded (Hammer et al. 2012) of which 39 (30 native, eight introduced) occur in the EMLR (Table 2-1).

Table 2-1. List of fish species recorded in the Eastern Mount Lofty Ranges. Functional groups are: D = Diadromous; FS = Obligate freshwater, specialists stream; FW = Obligate freshwater, specialists wetland; FG = Obligate freshwater, generalist, FP = Obligate freshwater, generalist which is Potamodromous; A = alien species. Conservation status: National: VU=Vulnerable, EN=Endangered (EPBC Act 1999); State: P=Protected (Fisheries Management Act 2007); CR=Critically Endangered, EN=Endangered, Vu=Vulnerable, RA=Rare (SA Action Plan: Hammer et al. 2009). Functional National State Species Scientific name Group (EPBC Act) (Action Plan) FG Australian Smelt Retropinna semoni FG Bony herring Nematalosa erebi FG Carp gudgeon (hybrid forms)* Hypseleotris spp. FG Carp gudgeon (Midley’s)* Hypseleotris sp. 1 FG Carp gudgeon (Murray-Darling)* Hypseleotris sp. 3 FG Carp gudgeon (Western)* Hypseleotris klunzingeri FW Chanda perch Ambassis agassizii P, CR D Climbing galaxias Galaxias brevipinnis RA D Common galaxias Galaxias maculatus D Congolli Pseudaphritis urvillii VU FG Dwarf flathead gudgeon Philypnodon macrostomus FG Flathead gudgeon Philypnodon grandiceps FW Freshwater catfish Tandanus tandanus P, EN FG Lagoon goby Tasmanogobius lasti FS Mountain galaxias 1* Galaxias olidus VU FS Mountain galaxias 2 (obscure)* Galaxias sp. 1 VU FG Murray cod Maccullochella peelii VU P, EN FW Murray hardyhead Craterocephalus fluviatilis EN CR FG Murray rainbowfish Melanotaenia fluviatilis FP Murray-Darling golden perch Macquaria ambigua ambigua D Pouched lamprey Geotria australis EN FS River blackfish Gadopsis marmoratus P, EN D Shortfinned eel Anguilla australis RA D Shortheaded lamprey Mordacia mordax EN FG Silver perch Bidyanus bidyanus P, EN FG Smallmouthed hardyhead Atherinosoma microstoma FW Southern purple-spotted gudgeon Mogurnda adspersa P, CR FS Southern pygmy perch Nannoperca australis P, EN FG Unspecked hardyhead Craterocephalus stercusmuscarum FG Western bluespot goby fulvusPseudogobius olorum FW Yarra pygmy perch Nannoperca obscura VU P, CR A Brook trout Salvelinus fontinalis A Brown trout Salmo trutta A Common carp Cyprinus carpio A Gambusia Gambusia holbrooki A Goldfish Carassius auratus A Rainbow trout Oncorhynchus mykiss A Redfin Perca fluviatilis A Tench Tinca tinca *Taxonomic uncertainty presently exists for Galaxias and Hypseleotris species complexes (Adams et al. 2014; Bertozzi et al. 2000); throughout the present report, these complexes will be defined as mountain galaxias (Galaxias spp.) and carp gudgoen (Hypseleotris spp), respectively.

State of fish communities across the EMLR, 2010 to 2013

Of the species recorded in the EMLR, three are nationally threatened whereas 16 species are protected or considered threatened at state level, according to the Action Plan for SA Freshwater Fish (Hammer et al. 2009). Additionally, marine variants have been irregularly detected in the region

(e.g. sandy sprat during 2004 baseline inventory: Hammer 2004).

Functional groups

To address conceptual models and define environmental objectives, natural groupings of these fish species (ecological assets) have been made under ecologically meaningful categories, or functional groups. These were first presented in Hammer (2007c) and have been subsequently refined to encompass six groups (with alien species included as a separate group) (Table 2-2) (Hammer 2009; SAMDBNRM Board 2013; VanLaarhoven and van der Wielen 2009).

Table 2-2. Functional groups represented in the Eastern Mount Lofty Ranges. Functional group Description Example fish species Resident freshwater species Species that reside in freshwater habitats Southern pygmy perch, permanently (i.e. obligate), and that have mountain galaxias and river Obligate freshwater, particular stream habitat or environmental blackfish specialist (stream) requirements. Are often found as the only species in a reach, but are restricted to specific habitats. Species that require particular habitats or Yarra pygmy perch, Murray environments for survival. Are often found hardyhead, and southern Obligate freshwater, as rare species in diverse fish assemblages, purple-spotted gudgeon. specialist (wetland) being restricted to specific habitats within lowland or terminal stream reaches Have more generalised habitat or Includes gudgeon species, environmental requirements, being mostly numerous species from found in association with other species and terminal wetlands and occupy multiple habitats within a reach. euryhaline species like Freshwater, generalist The community composition and structure gobies. (and therefore the water requirements) is determined by the types of habitats present. Migratory species Require migration to and from the sea or Congolli, common galaxias Diadromous species estuary. and lampreys Known to make determined movements Murray-Darling golden perch Potamodromous species within freshwater systems for particular lifecycle stages

State of fish communities across the EMLR, 2010 to 2013

Population models

To better understand self-sustaining populations, information on aspects relating to recruitment and survivorship need to be based on an understanding of local species ecology. Representative population structure models for the three key EMLR obligate freshwater species (mountain galaxias, southern pygmy perch and river blackfish), the main focus for demographic data, have been previously developed to help interpret annual data (Hammer 2005; Hammer 2006c; Hammer 2007a; Hammer 2007d). These models are shown in Figure 2-4 to Figure 2-7 with age structure differentiation for each species summarised in Table 2-3.

Table 2-3. Summary population structure for threatened native fish in the Eastern Mount Lofty Ranges (see Hammer 2005; Hammer 2006c; Hammer 2007a; Hammer 2007d). Age structure (mm) Species 0+ 1+ 2+ 3+ 4+ Mountain galaxias (Galaxias olidus) – EMLR <60 60-80 80 (except Marne Catchment) Mountain galaxias (Galaxias sp. 1) – Marne <65 65-80 80 >100 Catchment River blackfish (Gadopsis marmoratus) <80 110-160 150-200 190-240 >250 Southern pygmy perch (Nannoperca australis) <45 40-55 50

These population models were used to guide interpretation of demographic data to assess recruitment and survivorship throughout the present study, noting that site and inter-annual variability may shift the relative position of breaks, and that further research will be required to more accurately validate these models (e.g. ageing studies).

State of fish communities across the EMLR, 2010 to 2013

12 0+ 1+ ≥2+ 11 0+ 1+ ≥2+ 10 9 8 7 6

Frequency 4 3 2 1

0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

5 Total length (mm)

2 Weight(g)

0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

Total length (mm)

Figure 2-4. Representative autumn population model for Mountain galaxias (Galaxias sp. 1) (note weights for two larger fish not shown), see also Hammer (2007c). Data collected on this form of mountain galaxias is best represented by smaller fish in the 45-65mm range and subsequent peaks. Hence an overall proposed general autumn population model is: 0+ fish reach a size of up to 65mm (<2g); 1+ fish 60-80mm (2-4g); 2+ and older fish >80mm (>4g); 3+ fish may represent individuals larger than 100mm TL.

State of fish communities across the EMLR, 2010 to 2013

12 11 0+ 1+ ≥2+ 0+ 1+ ≥2+ 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

Total length (mm) Figure 2-5. Representative autumn population model for mountain galaxias form occurring in the Finniss and Tookayerta catchments (true Galaxias olidus), see also Hammer (2007c)). Data collected on this form of Mountain Galaxias is heavily dominated by smaller fish in the 40-60mm range with a relatively clear indication of a strong 0+ cohort <60mm and 2g across most sites. Interpreting subsequent potential cohorts is difficult due to low numbers of larger fish without defined peaks, but nevertheless predicted breaks in length data for cohorts are tentatively 60-80mm and 3.5g for 1+ fish and >80mm for ≥2+ fish.

14 0+ 1+ ≥2+ 12

Frequency 4

0 0 10 20 30 40 50 60 70 80 90

Total length (mm)

Figure 2-6. Representative autumn population model for Southern pygmy perch in the Eastern Mount Lofty Ranges, see also Hammer (2005). Samples are often dominated by smaller with an indicative 0+ peak between 30-45mm, 1+ fish 40- 55mm and ≥2+ >50mm.

State of fish communities across the EMLR, 2010 to 2013

0+15 14 0+ 1+1+ 2+2+ 3+3+ ≥4+ 13 12 11 10 9 8 7 6

Frequency 5 4 3 2 1 0 0 50 100 150 200 250 300 350

Total length (mm)

Figure 2-7. Representative age-class structure for river blackfish in the Eastern Mount Lofty Ranges, see also Hammer (2006c). The first two size classes are fairly clear, with later sizes showing a high degree of variability between and within sites.

2.4 Assessment Framework

The integrity of water-dependent environments depends largely on the dynamics of the natural flow regime (Poff et al. 1997). In this context, environmental water requirements (EWRs) are defined as ‘water requirements that must be met in order to sustain the ecological values of that environment’ (SAMDBNRM Board 2013). Specifically, EWRs are characterised in terms of the aspects of the magnitude, timing and quality of flow that are linked to the life-history strategies of native species (Arthington et al. 2006; Poff et al. 2010). In environments where the natural flow regime has been altered, EWRs are necessary to restore and maintain native species whilst disadvantaging alien species. However, development and diversion of water resources the EMLR has taken place over such an extended period of time, and present knowledge of ecological assets has been documented so relatively recently in comparison, that the process of identifying and determining EWRs has its limitations. Namely, the process is unavoidably biased towards the identification and maintenance of known, recently documented ecological assets, rather than being a driver of change towards what may be a long-lost, assumed (but desirable), past ecological state.

In the heavily altered EMLR, the EWR process has been advanced through the documenting the following five key steps (Hammer 2007c; Hammer 2009; SAMDBNRM Board 2013; VanLaarhoven and van der Wielen 2009):

 Information collation (catchment descriptions);  Reach delineation;  Identification of ecological assets per reach;  Develop conceptual model linking ecological drivers to assets; and,  Define environmental objectives for ecological assets, and the water requirements to meet these objectives. An important aspect of the EWR process is regular assessment of the condition of identified ecological assets. In the EMLR, condition monitoring is most advanced and comprehensive for fish species (see Section 2.6) with status reports produced in 2007 (Hammer 2007c) and 2009 (Hammer 2009). These status assessments rely on an approach that is further developed in this 2013 report (having the benefit of a growing long-term dataset).

State of fish communities across the EMLR, 2010 to 2013

2.5 EWRs for fish-related ecological assets

The main functional groups were identified in section 2.3. While some habitats and locations in the landscape may only have one or two species, broad groupings of fish species with similar water requirements can also be made on the basis of habitat and reach types:

 Groundwater dependent habitat fish community.  Lowland stream and floodplain habitat fish community.  Terminal Wetland habitat fish community.  Fleurieu Swamp habitat fish community.

Environmental water requirements (EWRs) for EMLR fishes are described in terms of the dominant species (as part of functional groups) or according to the fish community groupings detailed above (Table 2-4 to Table 2-12).

Summary tables detailing these EWRs highlight: (1) the natural processes required to support environmental objectives, (2) the parts of the water regime linked to those natural processes, and (3) the monitoring approach and indicators used to assess whether these natural processes are being supported. Note that several of the objectives or water requirements implicate monitoring of environmental variables and habitat condition; fish specific techniques only are mentioned but other relevant environmental data is also routinely collected (e.g. water quality, pool depth, habitat availability), with some techniques employed that are specific to other functional groups (e.g. indicators for vegetation health).

State of fish communities across the EMLR, 2010 to 2013

Table 2-4. Working environmental water requirements and relevant monitoring methods for mountain galaxias (obligate freshwater, stream specialist) in the Eastern Mount Lofty Ranges. Environmental Objective: Fish monitoring methods Maintain or restore self- necessary at key nodes within Water Requirements sustaining populations of river reaches (with indicator in mountain galaxias brackets) Habitat Processes Habitat availability Persistence of water in pools throughout the Mapping distribution at key Low Flow Season (base flow ideal). Freshes nodes during low flow seasons during the Low Flow Season that refill pools (population extent). are important. Maintain smaller habitats and tributaries especially when exotic predators occur. Water quality Freshes during the Low Flow Season that Assessing survivorship through refresh water quality. a snapshot of demographic structure (length data). Deep pool structure Bankfull channel forming flows that occur at Mapping distribution at key a frequency and duration to maintain nodes during low flow seasons channel form. Prevent vegetation (population extent). encroachment. Clean substrate for egg Freshes during the Low Flow Season. Assessing recruitment through deposition following spawning a snapshot of demographic structure (length data), with studies of fish biology (larvae). Biodiversity Processes Recolonisation of vacant Sustained low-high flows that allow Mapping distribution at key habitats and mixing of extant movement between pools over relatively nodes in river reaches during populations long distances. low flow seasons (population extent) over time (temporal monitoring). Studies of fish biology (movement). Successful spawning Increase in flows over transitional period Assessing recruitment through between Low and High Flow Season in a snapshot of demographic June/July triggers spawning, oxygenates structure (length data). Studies riffles and allows access to new habitats of fish biology (spawning and (spawning sites). larvae). Habitat complexity and Low flows and base flow to maintain Mapping distribution at key resistance to the impacts of shallower sub-optimal habitats and pool nodes in reaches during low exotic fishes margins when exotic predatory fishes (trout flow seasons (population and redfin) occur. extent) over time (temporal monitoring). Riparian and edge vegetation Low flows and overbank flow to maintain Standardised environmental (macroinvertebrate food shallow margins and banks to encourage measures. resources, shading, cover) emergent and riparian species (e.g. sedges, amphibious woody species, redgums). Suppression of exotic species Variable flows and zero flows discourage Assessing fish community colonisation by exotic fish and favour composition (species natives. High flow disturbances can flush inventory/presence), snapshot exotics like Gambusia. of demographic structure for exotic species (length data).

State of fish communities across the EMLR, 2010 to 2013

Table 2-5. Working environmental water requirements and relevant monitoring methods for river blackfish (obligate freshwater, stream specialist) in the Eastern Mount Lofty Ranges. Environmental Objective: Fish monitoring methods Maintain or restore self- necessary at key nodes within Water Requirements sustaining populations of river river reaches (with indicator in blackfish brackets) Habitat Processes Habitat availability and quality Permanent water in pools throughout the Determining that fish remain in year (via baseflow). Maintain shallow pool the reach (presence), assessing margins or shelves for juvenile and young fish. survivorship through a snapshot of demographic structure (length data). Studies of fish biology (spawning and health). Water quality Cool and well oxygenated conditions Determining that fish remain in (extended low flows or permanent baseflow). the reach (presence), assessing survivorship through a snapshot of demographic structure (length data). Studies of fish biology (spawning and health). Deep pool structure High channel forming flows that occur at a Mapping distribution during low frequency and duration to maintain channel flow seasons (population form. extent). Minimal siltation of underwater Freshes during the Low Flow Season. Assessing survivorship through surfaces to allow feeding and a snapshot of demographic successful egg hatching structure (length data). Studies of fish biology (spawning & larvae). Biodiversity Processes Recolonisation of vacant Low flows or occasional freshes that allow Mapping distribution during low habitats and mixing of extant movement between pools over relatively flow seasons (population populations short distances. extent) over time (temporal monitoring). Studies of fish biology (movement). Spawning success Spawning and recruitment require Assessing recruitment through maintenance of shallows (larval habitat) a snapshot of demographic during spring and sustained into early structure (length data). Studies

summer (low flows and raised pool levels); of fish biology (spawning and

probably also below a salinity threshold larvae). -1 (<4000uScm ) required for successful recruitment (i.e. Freshes).

Spawning occurs in hollows or cavities with a long incubation time. Freshes and sustained flows in late spring will assist recruitment.

State of fish communities across the EMLR, 2010 to 2013

Table 2-6. Working environmental water requirements and relevant monitoring methods for southern pygmy perch (obligate freshwater, stream specialist) in the Eastern Mount Lofty Ranges. Environmental Objective: Fish monitoring methods Maintain or restore self- necessary at key nodes within Water Requirements sustaining populations of river reaches (with indicator in southern pygmy perch brackets) Habitat Processes Habitat availability. Persistence of water in pools throughout the Mapping distribution at key Low Flow Season (baseflow ideal, also early on- nodes during low flow seasons set of seasonal flows). Freshes during the Low (population extent). Flow Season that refill pools are important. Assessing recruitment through a snapshot of demographic Appropriate flow regime for maintaining structure (length data), with submerged aquatic macrophytes and riparian studies of fish biology vegetation (larvae/spawning sites /eggs). Water quality. Freshes during the Low Flow Season that Assessing survivorship through a refresh water quality but that follow naturally snapshot of demographic occurring local patterns. structure (length data). Deep pool structure. Bankfull channel forming flows that occur at Mapping distribution at key a frequency and duration to maintain nodes during low flow seasons channel form. (population extent). Biodiversity Processes Recolonisation of vacant habitats Sustained low flows that allow movement Mapping distribution at key and mixing of extant populations. between pools in local areas (the species has nodes reaches during low flow a limited dispersal ability). seasons (population extent) over time (temporal monitoring). Studies of fish biology (movement). Spawning success. Spawning and recruitment linked to lateral Assessing recruitment through a connectivity and access to edge vegetation snapshot of demographic during spring; extended period of flows at structure (length data). Studies the end of the Low Flow season to raise and of fish biology (spawning and maintain pool level in emergent and edge larvae). vegetation. Promote successful spawning of southern pygmy perch to improve population resilience to exotics. Habitat complexity resistance to Low flows and base flow maintain shallower Mapping distribution at key the impacts of exotic fishes. sub-optimal habitats and pool margins when nodes in river reaches during exotic predatory fishes occur (trout and low flow seasons (population redfin). extent) over time (temporal monitoring). Suppression of exotics Variable flows and zero flows discourage Assessing fish community colonisation by exotic fish and favour natives. composition (species Larger disturbances can flush exotics, inventory/presence). especially Gambusia.

State of fish communities across the EMLR, 2010 to 2013

Table 2-7. Working environmental water requirements and relevant monitoring methods for freshwater generalists in the Eastern Mount Lofty Ranges (includes the gudgeon species from the genera Hypseleotris and Philypnodon, numerous species from terminal wetlands, and Euryhaline species). Environmental Objective: Fish monitoring methods Maintain or restore self- necessary at key nodes within Water Requirements sustaining populations of river reaches (with indicator in gudgeons brackets) Habitat Processes Habitat availability Persistence of water in pools throughout the Mapping distribution at key nodes Low Flow Season (base flow ideal). Freshes during low flow seasons during the Low Flow Season that refill pools (population extent). are important. Water quality. Freshes during the Low Flow Season that Assessing survivorship through a refresh water quality. snapshot of demographic structure (length data). Deep pool structure. Bankfull channel forming flows that occur at a Mapping distribution at key nodes frequency and duration to maintain channel during low flow seasons form. (population extent). Biodiversity Processes Recolonisation of vacant Sustained low-high flows that allow Mapping distribution at key nodes habitats and mixing of extant movement between pools over relatively long in river reaches during low flow populations. distances. seasons (population extent) over time (temporal monitoring). Studies of fish biology (movement). Spawning success. Low flows and warmer temperatures during Assessing recruitment through a the Low Flow season, low flows to stabilise snapshot of demographic water levels. structure (length data). Studies of fish biology (spawning and larvae). Habitat complexity and Low flows and base flow maintain shallower Mapping distribution at key nodes resistance to the impacts of habitats and pool margins when exotic in river reaches during low flow exotic fishes. predatory fishes (trout and redfin) occur. seasons (population extent) over time (temporal monitoring). Discourage colonisation and Variable flows and zero flows discourage Assessing fish community establishment of exotic species colonisation by exotic fish and favour natives. composition (species inventory) (negative impacts of predation, Larger disturbances can flush exotics. or specific investigation for competition and disease) species of concern (presence), snapshot of demographic structure for exotic species (length data)

State of fish communities across the EMLR, 2010 to 2013

Table 2-8. Working environmental water requirements and relevant monitoring methods for diadromous species (e.g. lampreys, shortfinned eel, common galaxias, congolli) and migratory freshwater species (e.g. potamodromous Murray- Darling golden perch) in Eastern Mount Ranges stream habitats Fish monitoring methods Environmental Objective: necessary at key nodes within Maintain or restore populations Water Requirements river reaches (with indicator in of diadromous species brackets) Habitat Processes Habitat availability Persistence of water in pools throughout the Mapping distribution at key Low Flow Season (base flow ideal). nodes during low flow seasons Maintenance of permanent water in slow flow (population extent). areas (larval lampreys). Encourage diversity of habitat types. Water quality Freshes during the Low Flow Season that Assessing survivorship through a refresh water quality, particularly around snapshot of demographic partial barriers to dispersal that can act as structure (length data). Studies population bottlenecks (e.g. high of fish biology (movement and concentrations of fish). tolerances – in situ and experimental) Deep pool structure Bankfull channel forming flows that occur at a Mapping distribution at key frequency and duration to maintain channel nodes during low flow seasons form. (population extent). Connectivity. Large flows to provide physical disturbance and Mapping distribution at key improve pool connectivity along the stream nodes during low flow seasons corridor to the River Murray/ Lake Alexandrina (population extent). (e.g. dislodge debris). Biodiversity processes Movement Attractant flows. Mapping distribution at key nodes in river reaches during Sustained low-high flows that allow movement low flow seasons (population in and out of stream habitat, and dispersal extent) over time (temporal between pools over relatively long distances. monitoring). Studies of fish Requires appropriate timing and duration for biology (movement). different species. Assessing barriers to dispersal. Spawning success. Raises in water levels to allow access to Assessing recruitment through a emergent vegetation (e.g. common galaxias snapshot of demographic spawning lower stream reaches), appropriate structure (length data). Studies water quality, permanence and access where of fish biology (spawning and species congregate. larvae). Habitat complexity and Low flows and base flow maintain shallower Mapping distribution at key resistance to the impacts of habitats and pool margins when exotic nodes in river reaches during exotic fishes. predatory fishes (trout and redfin) occur. low flow seasons (population extent) over time (temporal monitoring). Suppress exotics Variable flows and zero flows (if natural part Assessing fish community of flow regime) to discourage colonisation by composition (species inventory) exotic fish and favour natives. Larger or species presence, snapshot of disturbances can flush (high flow) or suppress demographic structure for (no flow) exotics. exotic species, studies of fish biology.

State of fish communities across the EMLR, 2010 to 2013

Table 2-9. Working environmental water requirements for fish communities in groundwater dependent habitat fish communities (mainly stream specialists, but also generalists and diadromous functional groups) in the Eastern Mount Lofty Ranges. Environmental Objectives: Fish monitoring methods Maintain or restore diversity necessary at key nodes within and composition of fish Water Requirements: river reaches (with indicator in community (important refuges brackets) or core habitat) Habitat Processes Habitat availability. Permanent water in pools throughout the Assessing fish community year. There should be a minimum pool composition (species inventory), number and a diversity of pool or habitat determining that species types include deeper and shallower areas to diversity is maintained in a provide adequate security and resilience. reach (presence), mapping distributions during low flow seasons (population extent). Water quality. Cool and well oxygenated conditions Determining that fish remain in (extended low flows or permanent baseflow). the reach (presence), assessing Minimise salinity impacts on the tolerance survivorship through a snapshot (lethal and sub-lethal) of adult or juveniles of demographic structure stages of native fish – freshes and flushing (length data). Studies of fish flows. biology (spawning and health). Habitat diversity (prevent High flows that occur at a frequency and Mapping distribution during low encroachment of vegetation). duration to prevent vegetation encroachment. flow seasons (population extent), assessing survivorship through a snapshot of demographic structure (length data). Deep pool structure. High channel forming flows that occur at a Assessing fish community frequency and duration to maintain channel composition (species inventory) form. Biodiversity processes Recolonisation of vacant Low flows or occasional freshes that allow Mapping distribution during low habitats and mixing of extant movement between pools over relatively flow seasons (population extent) populations. short distances. over time (temporal monitoring). Studies of fish biology (movement). Suppress exotic species Variable flows and continuous flowing cool Assessing fish community water discourage exotic fish and favour composition (species inventory), natives, larger flows dislodge/flush exotics. assessing survivorship through a snapshot of demographic structure (length data). Studies of fish biology (habitat use).

State of fish communities across the EMLR, 2010 to 2013

Table 2-10. Working environmental water requirements for fish communities (generalist, diadromous, potamodromous and wetland specialist functional groups) in the lowland reaches of the Eastern Mount Lofty Ranges Environmental Objectives: Fish monitoring methods Maintain or restore diversity necessary at key nodes within Water Requirements: and composition of fish river reaches (with indicator in community brackets) Habitat Processes Habitat availability Permanent water in channel, anabranches and Assessing fish community refuges (e.g. billabongs) throughout the year. composition across habitat types (species inventory), determining that species diversity is maintained in a reach (presence), mapping distributions during low flow seasons (population extent). Water quality. Cool and well oxygenated conditions Determining that fish remain in (extended low flows or permanent baseflow). the reach (presence), assessing Minimise salinity impacts on the tolerance survivorship through a snapshot (lethal and sub-lethal) of adult or juveniles of demographic structure stages of native fish – freshes and flushing (length data). Studies of fish flows. biology (spawning and health). Habitat diversity (prevent High flows that occur at a frequency and Mapping distribution during low encroachment of emergent duration to prevent vegetation encroachment, flow seasons (population vegetation, maintain submerged shape channels, and provide water quality and extent), assessing survivorship vegetation) flow requirements for plant species. through a snapshot of demographic structure (length data). Deep pool structure and High channel forming flows that occur at a Assessing fish community availability of off channel frequency and duration to maintain form and composition (species inventory) habitats diversity of channel and off-channel habitats Biodiversity processes Provide spatial and temporal Flow related disturbance to provide a variety Assessing fish community variability in the types of habitats present (mosaic) to composition (species inventory), allow species co-existence or cater for the determining that species requirements of multiple species (including diversity is maintained in a purple-spotted gudgeon). Provision of reach (presence), mapping contrasting habitat to that of wetlands distributions during low flow associated with the River Murray and Lower seasons (population extent). Lakes Attractant flows for High flows at natural time of year (winter- Assessing fish community diadromous/ migratory fish spring) for diadromous/migratory fish. composition (species inventory), species from the River Murray. with studies of fish biology (movement). Suppress exotic species Variable flows and continuous flowing cool Assessing fish community water discourage exotic fish and favour composition (species inventory), natives, larger flows dislodge/flush exotics. assessing survivorship through a snapshot of demographic structure (length data). Studies of fish biology (habitat use).

State of fish communities across the EMLR, 2010 to 2013

Table 2-11. Working environmental water requirements for fish communities (includes stream specialist, generalist, diadromous, wetland specialist and potamodromous functional groups) in the terminal wetlands of Eastern Mount Lofty Ranges. Environmental Objectives: Fish monitoring methods Maintain and restore diversity necessary at key nodes within Water Requirements: and composition of fish river reaches (with indicator in community brackets) Habitat Processes Habitat availability. Permanent water in wetlands throughout the Assessing fish community year. composition (species inventory), determining that species diversity is maintained in a reach (presence), mapping distributions during low flow seasons (population extent). Habitat diversity (prevent High flows that occur at a frequency and Mapping distribution during low encroachment of emergent duration to prevent vegetation encroachment, flow seasons (population vegetation, maintain submerged provide water quality and flow requirements extent), assessing survivorship vegetation). for plant species. through a snapshot of demographic structure (length data). Deep pool structure. High channel forming flows that occur at a Assessing fish community frequency and duration to maintain channel composition (species inventory) form. Biodiversity processes Provide spatial and temporal Flow related disturbance to provide a variety Assessing fish community variability in the types of habitats present (mosaic) to composition (species inventory), allow species co-existence or cater for the determining that species requirements of multiple species. Tannin-rich, diversity is maintained in a clearer river waters for example provide reach (presence), mapping habitat for Yarra pygmy perch in the Lower distributions during low flow Murray. seasons (population extent). Attractant flows for High flows at natural time of year (winter- Assessing fish community diadromous/ migratory fish spring) for diadromous/migratory fish. composition (species inventory), species from the River Murray. with studies of fish biology (movement). Suppress exotic species Variable flows and continuous flowing cool Assessing fish community water discourage exotic fish and favour composition (species inventory), natives, larger flows dislodge/flush exotics. assessing survivorship through a snapshot of demographic structure (length data). Studies of fish biology (habitat use).

State of fish communities across the EMLR, 2010 to 2013

Table 2-12. Working environmental water requirements for fish communities (includes stream specialists) in Fleurieu Swamps of the Eastern Mount Lofty Ranges. Environmental Objectives: Fish monitoring methods Maintain and restore diversity and necessary at key nodes within Water Requirements composition of swamp fish river reaches (with indicator in communities. brackets) Habitat Processes Habitat availability. Permanent water in swamps throughout the Assessing fish community year (spring feeding or inflow), of a sufficient composition (species depth and quality for species requirements inventory), determining that (e.g. >0.2m depth for southern pygmy perch, species diversity is maintained baseflow for river blackfish). Not necessarily in a particular feature open water, but areas with interstitial space. (presence). Water quality. Freshes during the Low Flow Season that Assessing fish community refresh water quality but that follow composition (species naturally occurring local patterns. inventory), determining that species diversity is maintained in a particular feature (presence). Habitat diversity (prevent High flows or high water levels that occur at Mapping distribution during low encroachment of vegetation). a frequency and duration to prevent flow seasons (population vegetation encroachment. extent), assessing survivorship through a snapshot of demographic structure (length data). Biodiversity processes Recolonisation of vacant habitats Low flows or occasional freshes between Mapping distribution during low and mixing of extant populations. swamps (where applicable) that allow flow seasons (population movement between over relatively short extent) over time (temporal distances. monitoring). Studies of fish biology (movement). Provide spatial and temporal Flow related disturbance to provide a variety Assessing fish community variability. in the types of habitats present (mosaic) to composition (species allow species co-existence or cater for the inventory), determining that requirements of multiple species (where species diversity is maintained applicable). in a reach (presence), mapping distributions during low flow seasons (population extent). Successful spawning Lateral connections for accessing new Assessing survivorship through habitat and food resources for adult a snapshot of demographic conditioning, spawning sites and larval structure (length data). Studies habitat. of fish biology (larvae). Suppress exotic species Variable flows and continuous flowing cool Assessing fish community water discourage exotic fish and favour composition (species natives, larger flows dislodge/flush exotics. inventory), assessing survivorship through a snapshot of demographic structure (length data). Studies of fish biology (habitat use).

State of fish communities across the EMLR, 2010 to 2013

2.6 Fish monitoring

Summary

Fish monitoring of varying forms has occurred regularly in the EMLR since 1999. Between 1999 and 2003, a total of 98 sites were sampled through a number of projects, including a genetic assessment of southern pygmy perch (Hammer 2001) and as a result of baseline inventory sampling for the Lower Lakes (Wedderburn and Hammer 2003). In autumn 2004, comprehensive baseline sampling (>200 sites) was undertaken across the EMLR and formed the basis of a regional fish inventory (Hammer 2004). Other sampling in 2004 through to 2006, also visited 98 sites during a fish inventory of the southern Fleurieu Peninsula (Hammer 2006a), assessment of environmental water requirements (Hammer 2007c) and species-specific projects (e.g. Hammer 2005).

In 2007, existing survey results were reviewed within an EWR framework and a monitoring approach to assess the condition of fish populations and communities for different stream reaches across the different EMLR catchments was devised (Hammer 2007c). As a result, between 2007 and 2013, 50– 60 sites have been monitored annually in autumn to provide the data necessary for more informative condition reporting (Hammer 2009). In addition to the collection of annual autumn data, sampling at targeted sites was undertaken in spring 2007 in order to gain additional information on species biology and site-specific breeding performance (part of the SAMDBNRMB EMLR Flows Program). Spring monitoring of all autumn annual sites was undertaken between 2008−2010 to provide a better understanding of the status of threatened populations during the period of critical water shortage as part of the South Australian Drought Action Plan (DAP) for MDB threatened freshwater fish species (Bice et al. 2010; Bice et al. 2011; Bice et al. 2009). With the return of favourable conditions, the focus of DAP monitoring (as part of the Critical Fish Habitat project) shifted to the assessment of potential sites for reintroduction of threatened species and subsequent monitoring between 2011–2014 (Bice et al. 2013; Bice et al. 2014). Concurrent monitoring in the Lower Lakes has also been undertaken as part The Living Murray (TLM) program (Wedderburn and Barnes 2009; Wedderburn and Barnes 2011; Wedderburn and Barnes 2012; Wedderburn and Barnes 2013; Wedderburn and Barnes 2014; Wedderburn and Hillyard 2010).

Nature of monitoring

Monitoring undertaken in the EMLR has aimed to (1) document fish community composition, and (2) record the presence, population extent and demographic information for key threatened species.

State of fish communities across the EMLR, 2010 to 2013

Importantly, monitoring focuses on providing data to assess the condition, trend or occurrence of processes that maintain fish related assets (Hammer 2007c). Given the sensitive nature of fish communities in the region, all monitoring sought to minimise the impact on the fish populations studied and their habitat, whilst gathering meaningful and repeatable data. Hence sampling methods were dependent on the extent and type of habitat, and sensitivity of habitats and species to capture and disturbance (see Hammer 2004; Hammer 2005; Hammer 2006c). As a result of this approach, a wide range of sampling methods were employed, including the use of fyke nets, backpack electrofishing, seine nets and bait traps. All sampled fish were identified to species level and enumerated, with threatened native species sampled measured for length (mm, total length, TL). At each site, broad habitat (type and size, flow connectivity, water level), water quality (pH, electrical conductivity, water temperature, dissolved oxygen, transparency) were recorded along with assessment of aquatic habitat (submerged physical, biological and emergent cover).

Sampling methods – Fyke netting

State of fish communities across the EMLR, 2010 to 2013

2.7 Reporting process

Fish monitoring data is incorporated into a report carding framework to provide assessment of the condition of each fish-related ecological asset in the region. The framework for report carding was initially developed for the Marne catchment in 2006 (Hammer 2006b; Hammer 2007a), expanded across the region as part of the 2009 status assessment (Hammer 2009) and is further enhanced during the present (2013) assessment. In summary, report carding for an individual catchment reflects the condition of identified ecological assets, such as (a) populations of threatened species, (b) diverse fish communities and (c) the presence of alien species, with associated objectives (Table 2-13). The report card for a particular year is based on the preceding flow year assessed through site- based condition monitoring conducted in autumn annually (i.e. ‘2010’ assessment based winter 2009 to autumn 2010 flow period).

Table 2-13. Summary ecological assets and associated objectives for report carding in the Eastern Mount Lofty Ranges. Ecological asset Objective Threatened species (individual) Maintain or restore self-sustaining population(s) Maintain or restore diversity and composition of fish Diverse fish community community, including diadromous, specialist, threatened and generalist species Limited alien species Discourage colonisation and establishment

The assessment of individual threatened species ecological assets (scored out of 7) is based on presence and measures of recruitment and survivorship linked to previously developed categories (i.e. excellent, good, marginal or poor, including failure: SAMDBNRM Board 2013; VanLaarhoven and van der Wielen 2009) (see Table 2-14).

Table 2-14. Summary of report card scoring for each indicator for the single species ecological assets. Indicators Ecological assets – Presence Recruits (0+ fish) Survivors (>2+ fish) species (max. 1) (max. 3) (max. 3) Poor Marginal Good Excellent Poor Marginal Good Excellent 0 1 0 1 2 3 0 1 2 3 Mountain galaxias 0 1 2-9 >10 0 1 2-4 >5 River blackfish 0 1 2-4 >5 0 1 2-4 >5 Pygmy perches none >1 0 <5 6-19 >20 0 <5 6-19 >20 Murray hardyhead 0 1 2-9 >10 0 1 2-9 >10 Gudgeon species 0 <5 6-24 >25 0 <5 6-19 >20

For fish community ecological assets, assessment (again out of 7) is based on the number of freshwater specialist and diadromous species, highly threatened species (critically endangered or

State of fish communities across the EMLR, 2010 to 2013 endangered nationally) and freshwater generalists (Table 2-15). The alien species condition score is based on discouraging the colonisation and establishment of large populations, with scores assigned (out of 2; 0: if aliens account >70% of total fish numbers; 1: aliens account 30−70% of total numbers; 2: aliens numbers <30% of total numbers) at the site level (i.e. added to averaged score all ecological assets at that site).

Table 2-15. Summary of report card scoring for each indicator for the ecological assets relating to diverse fish communities as well as alien species and diverse fish community. Presence Ecological Indicators (no of species) assets 0 1 2 Diadromous species 0 1-2 >2 Diverse fish Specialist species 0 1-2 >2 community Highly threatened (CEN, EN) species nationally 0 - 1 or more Freshwater generalists 0 1 or more -

Limited alien >70% of total 30−70% of total <30% of total fish Alien species species fish numbers fish numbers numbers

Site based scores were calculated using the median of all ecological assets present at the site plus the score for alien species (maximum score 7+2=9). Where multiple sites were present in a reach the median of these sites was used to produce a reach score, which were assigned the following condition ratings: good (>7), moderate (4 to 6) and poor (<3). In turn, the median of these reach condition scores was used to provide an overall catchment score. Trends were determined by comparing corresponding score across years of the present reporting period (see sample in Figure 2-8) as well as from the 2009 assessment (with indicators that have changed since last assessment indicated by grey highlight). A sample report card is provided below (Table 2-16) as is a sample of the trend figure (see Figure 2-8).

State of fish communities across the EMLR, 2010 to 2013

9 Reach types 8 Headwaters Upper 7 Mid

6 Gorge Lowland 5 Wetlands

4 3

Condition score (out of 9) (out score Condition 1 0 2009 2010 2011 2012 2013 Year

Figure 2-8. EXAMPLE: Trend of reach scores.

State of fish communities across the EMLR, 2010 to 2013

Table 2-16. WORKED REPORT CARD EXAMPLE for the assessment of the performance against fish indicators. Notes: for each ecological asset, only relevant indicators are assessed (hence blacked out indicators). A tick ( ) represents a positive result and a cross ( ) a negative result. For the individual species ecological assets, ticks indicate a score of 1 for presence and 2 or 3 for recruitment and survivorship. For diverse fish communities, ticks indicate a presence score of 4 or greater. For alien species, ticks indicate a score of 2 (i.e. <30% of total site numbers). Condition scores for each ecological asset (out of 9) reflect the sum for each indicator (out of 7) plus an alien species score (out of 2). The median of scores for all ecological assets are used to estimate the overall catchment score. For ecological assets and overall catchment score are defined as good (>6, xxx), moderate (3 to 6, xxx) and poor (<3, xxx) 2013 ASSESSMENT for 2013 Mountain galaxias SPP YPP All native species Alien species INDICATOR

Habitat (pool Relevant site

condition, depth)

Condition

Alien species

Reach Reach score

Presence

Recruitment Survivorship

Total Recruitment (0+ fish) Survivorship (>2+ fish) Total Recruitment (0+ fish) Survivorship (>2+ fish) Total Recruitment (0+ fish) Survivorship (>2+ fish) No. of species Total numbers Freshwater specialists Diadromous Threatened (CEN, EN) Freshwater generalists No. of species Total Percent Percent of total fish ECOLOGICAL ASSET Reach 2 & 3 – Upper pool-riffle tributary creeks Low (0.6m) 88 62 7 1 88 0 0 0% McHarg Creek Rd Mountain galaxias 1 3 3 7 2 9.0 Reach 5 – Meadows Creek upper pool-riffle channel under spring influence 149 48 15 Southern pygmy perch 1 3 3 7 Concentrated (0.6m) 3 273 1 100 27% Thorn Dairy 2 8.0 23 10 1 Mountain galaxias 1 3 1 5 Reach 6 – Heterogeneous mid pool-riffle channel 1 1 0 Southern pygmy perch 1 0 0 1 Bank (1.8m) 3 36 2 92 72% ds Coles Crossing 0 2.5 11 4 2 Mountain galaxias 1 1 2 4 Reach 7 – Mid pool-riffle channel under spring influence (above waterfalls) 13 1 0 Southern pygmy perch 1 0 0 1 Bank (1.2m) 57 34 9 6 94 3 10 10% us Waterfalls Mountain galaxias 1 3 3 7 2 5.0 2 2 0 3 Diverse fish community 3 3 Reach 8 – Lowland channel and floodplain Bank (2m) 3 58 0 0 0 3 3 137 70% Railway Bridge Diverse fish community 1 1 0 1.0 Reach 9 – Terminal wetland under Lake Alexandrina influence Bank (2.1m) 3 17 0 1 0 1 0 0 0% 300m ds Winery Rd Diverse fish community 2 2 2 Bank (1.3m) 4 65 0 2 0 2 3 9 12% 500m ds Winery Rd Diverse fish community 2 2 2 3.0 0 0 0 Yarra pygmy perch 0 0 0 0 Bank (1.5m) 4 33 3 104 76% Blue Lagoon 0 0 1 0 2 Diverse fish community 2 2

Median 4.0

Monitoring data for each ecological Indicator scores automatically updated in asset entered in this sheet the report card based on indicator criteria 29

State of fish communities across the EMLR, 2010 to 2013

Section 3. STATUS REPORTING

3.1 Summary over the reporting period (2010−2013)

Over the four years of the present reporting period, a total of 232 site were sampled in autumn 2010 (62 sites), 2011 (56 sites), 2012 and 2013 (57 sites each year). In summary, some 60,958 fish from 28 species (22 native and six alien species) were recorded. In this section, the status and condition of key ecological assets is evaluated across each catchment.

Southern purple-spotted gudgeon – Finniss River, Lovejoys (top left); Murray hardyhead – Rocky Gully wetland (top right); climbing galaxias – Finniss River, us Waterfalls (middle left); river blackfish – Marne River, Black Hill Springs (b) (middle right); the high abundance of juvenile redfin (bottom left); and increases in the native Murray-Darling golden perch following the return of water (bottom right).

State of fish communities across the EMLR, 2010 to 2013

3.2 Angas Catchment

The Angas River Catchment is moderate in size (199km2) and much of the land has been cleared for stock grazing, dairy or viticulture. It is characterised by a semi-circular arc of elevated land draining towards a main waterway, the Angas River, which extends from its headwaters near Flaxley, through Strathalbyn, and to its confluence with Lake Alexandrina near Milang. A fan of tributaries including Middle/Paris, Dawson, Doctors and Burnside creeks join the Angas River in or near Strathalbyn. Under current conditions, the latter two creeks are ephemeral (no permanent pools located), and the upper Angas River and Dawson and Middle creeks are episodic stream systems. There is a large degree of geomorphic variation within the catchment and considerable hydrological variability between stream sections. Much of the catchment consists of alluvial red gum lined tributaries, with spring fed upper reaches near Macclesfield. Below Strathalbyn, the character of the Angas differs considerably, consisting of bedrock based, larger pools fringed with Phragmites and Typha. The stream gains permanent flow through much of this approximately 5km section via groundwater base flows. Further downstream, the stream becomes an ephemeral channel (significant natural barrier), meandering 13km across a lowland flat before reaching its terminus at Lake Alexandrina via a small section of river channel. Pools are generally smaller in upland areas, with a long series of deeper pools in the mid catchment.

Overall, eight distinct river reaches have been defined in the Angas River catchment (Figure 3-1), and these form the spatial basis of setting and measuring environmental flow related objectives (Table 3-1 and Table 3-2). Fish-related ecological assets identified by Hammer (2004) include a highly restricted, genetically distinct population of southern pygmy perch (reach 5), and a population of river blackfish (reach 6). Reach 2 also formerly supported populations of these two threatened species. Other assets include mountain galaxias and other diverse native fish communities including diadromous species (reaches 2-8). The environmental objectives associated with these ecological assets are also detailed in Table 3-2 and related to relevant EWR tables of section 2.5.

Over the present reporting period (2010−2013), 11 sites within five distinct river reaches were sampled annually, while others were sampled irregularly.

State of fish communities across the EMLR, 2010 to 2013

0 1.25 2.5 5 Lake Alexandrina ¯ Kilometers

Figure 3-1. River reaches of the Angas River Catchment. The main channels of the catchment (including terminal wetland) are marked as dark blue whereas smaller tributaries streams are marked light blue. Lake Alexandrina is denoted as grey

State of fish communities across the EMLR, 2010 to 2013

Table 3-1. Distribution patterns and significant environmental assets in the Angas Catchment relating to fish species and communities (plus opportunistic data for other biota). Specific asset/pattern Location EWR Table No permanent fish communities due to lack of Reach 1 NA permanent water Genetically distinct southern pygmy perch population Reaches 2 & 5 (recent local Table 2-6 (Evolutionary Significant Unit) extinctions) River blackfish Reach 6 (formerly also Reach Table 2-5 & Table 2-9 2) Mountain galaxias Reaches 2, 3, 4, 5 & 6 Table 2-4 & Table 2-9 Mid Angas diverse fish community Reaches 2, 5 & 6 Table 2-6, Table 2-8 & Table 2-11 Angas River terminal wetlands diverse fish community, Reach 8 Table 2-6, Table 2-8 & including Lake Alexandrina genetic unit southern pygmy Table 2-11 perch Presence of diadromous fish species in the Lower Angas Reach 8 (formerly also 6) Table 2-8

Table 3-2. Summary of environmental objectives by reach for fish related ecological assets in the Angas River Catchment. Asset Environmental Objective Reach 1 – Angas Catchment headwaters NA Reach 2 – Dawson Creek and Paris Creek pool/riffle channel (Table 2-4, Table 2-5 & Table 2-6) Mountain galaxias • Maintain restricted self-sustaining population Southern pygmy perch and river blackfish • Restore self-sustaining populations Reach 3 – Upper Angas pool/riffle channel (Table 2-4) Mountain galaxias • Maintain restricted self-sustaining population Reach 4 – Angas gorge and pool-riffle channel (Table 2-4) Mountain galaxias • Maintain or restore a self-sustaining population Reach 5 – Mid pool-riffle (junction us Dawson Creek) (Table 2-4 & Table 2-6) Genetically distinct southern pygmy perch population • Maintain (core pool) a self-sustaining population (Angas) Mountain galaxias • Maintain or restore a self-sustaining population Reach 6 – Lowland channel below Strathalbyn (Table 2-5, Table 2-4 &Table 2-9) Diverse native fish community including threatened • Maintain a self-sustaining populations of threatened river blackfish and mountain galaxias. Historically also species included occasional diadromous species such as • Maintain diversity and composition of fish community congolli, climbing galaxias and lampreys • Restore community of diadromous species Reach 7 – Ephemeral channel (Table 2-8) Dispersal pathway of diadromous and migratory species • Restore access for community of diadromous species (historically recorded) Reach 8 – Terminal wetland/channel under Lake Alexandrina influence (Table 2-6, Table 2-8 & Table 2-11) Diverse native fish community including threatened and • Maintain diversity and composition of fish community diadromous and migratory species Southern pygmy perch (part of Lake Alexandrina genetic • Maintain a self-sustaining population sub-population)

State of fish communities across the EMLR, 2010 to 2013

Reach 2 – Dawson & Paris creeks

This reach has previously been considered as two upper pool riffle channel sections (i.e. Figure 3-1), however review of reach types suggest that lower reaches close to junctions with the Angas should also be included which slightly changes the information reported, due to the previous presence of populations of southern pygmy perch and river blackfish (Hammer 2009). Hence the whole sub- catchments are considered to fall within reach 2, but the lower sections could also be assessed in the mid-pool channel reach type (reach 5). There has been no monitoring of the upper tributary sections (with mountain galaxias ecological objectives). Lower Dawson Creek had a population of river blackfish prior to the early 1990s, and more recent records of a self-sustaining population of mountain galaxias. Annual drying of stream sections occurred in 2003 and again from 2005-2009, and hence it is expected that the asset is locally extinct. Similarly, large numbers of southern pygmy perch were recorded in lower Middle Creek in 2001, however major pool drying has occurred since, with records of a few individuals from a single pool lasting until 2004, with no water persisting in subsequent autumns.

Hence, based on local extinctions in lower stream sections, environmental water requirements for this stream reach would appear to have been compromised for a significant period of time. However, it should be noted that (1) this reach has not been monitored since 2009 and (2) mountain galaxias in upper sections of the reach remain to be re-assessed.

Reach 3 – Upper pool-riffle channel

Two sites have been monitored annually in this reach since 2004 and 2005 (Quarry Road and Searle Street), targeting mountain galaxias in small upper–pool channel habitat. Both populations have persisted over the nine years of monitoring, but variable catches reveal some interesting observations. Firstly, the period of critical water shortage (namely 2008 and 2009) impacted abundance and survivorship, with the near absence of surviving adults at both sites, but recruitment was maintained (Figure 3.2 to Figure 3-5). With improved surface water availability, survivorship was restored, strong recruitment continued and abundance increased over 2010 and 2011. Secondly, despite the improving condition of both populations, no fish were sampled in autumn 2012 or during follow up spring monitoring of that year but high abundance was again observed in 2013. The variability in catch at the Searle Street site may be explained by water quality, as low dissolved oxygen (<2.5mgL-1) is often experienced in autumn (impact of willow leaf fall in periods when flow is low), which may be affecting catches in some years.

State of fish communities across the EMLR, 2010 to 2013

Permanent flow is recorded at both sites in autumn of most years; and whilst autumn salinity steadily increased at Quarry Road (doubled from ~2500 to 5120µScm-1) during the drought, fresh conditions returned over the present reporting period (and salinity remained low/moderate throughout at Searle Street, ~2200µScm-1). Both sites maintain suitable aquatic habitat and overall this reach is in good condition (trend = stable).

Good catch of mountain galaxias at Angas River – Searle Street, autumn 2013

State of fish communities across the EMLR, 2010 to 2013

12 11 2005, n=28 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2006, n=75 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2007, n=28 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 12 11 2008, n=11 10 9 8 7 ‘ 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

Total length (mm) Figure 3-2. Length-frequency distribution for mountain galaxias at Angas River (Quarry Road), Angas Catchment (Reach 3) from 2005 to 2008.

State of fish communities across the EMLR, 2010 to 2013

12 11 2009, n=36 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2010, n=65 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2011, n=41 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 12 11 2012, n=0 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2013, n=39 10 9 8 7 6 5 Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

Total length (mm)

Figure 3-3. Length-frequency distribution for mountain galaxias at Angas River (Quarry Road), Angas Catchment (Reach 3) from 2009 to 2013 (graphs below the dotted line denote the current reporting period).

State of fish communities across the EMLR, 2010 to 2013

12 11 2004, n=0 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2005, n=44 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2006, n=26 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 12 11 2007, n=1 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2008, n=75 10 9 8 7 6 5 Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

Total length (mm) Figure 3-4. Length-frequency distribution for mountain galaxias at Angas River (Searle St), Angas Catchment (Reach 3) from 2004 to 2008.

State of fish communities across the EMLR, 2010 to 2013

12 11 2009, n=8 10 9 8 7 6 5 Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2010, n=26 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2011, n=29 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 12 11 2012, n=0 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2013, n=76 10 9 8 7 6 5 Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

Total length (mm)

Figure 3-5. Length-frequency distribution for mountain galaxias at Angas River (Searle St), Angas Catchment (Reach 3) from 2009 to 2013 (graphs below the dotted line denote the current reporting period).

State of fish communities across the EMLR, 2010 to 2013

Reach 4 – Angas Gorge

No sampling occurred for mountain galaxias in this reach during the 2009 assessment or during the present reporting period.

Reach 5 – Angas mid-pool riffle

This reach maintains a small population of southern pygmy perch, largely confined to a string of pools between the Middle Creek and Dawson Creek junctions: a core pool at the Middle Creek junction and periodic presence in other pools downstream. Monitoring of the core pool between 1999 and 2009 highlighted a strong population, with high abundance and strong recruitment in most years (except 2004, 2007), and reasonable survivorship (Figure 3-6 and Figure 3-7). High abundances were observed in the downstream pools, although only larger fish (mostly >50mm) were recorded in 2007−2009 (Figure 3-8 and Figure 3-9).

The core pool has come under increasing environmental water related stress over the period of critical water shortage (2007−2010), culminating in an autumn water level of just 0.5m in 2009 (with EC, 5140µScm-1; dissolved oxygen, 2.91mgL-1). These conditions appear to have impacted the southern pygmy perch population with only low numbers observed in 2010. The increase in surface water realised from 2010 (water depth, 1−1.4m over present reporting period) led to population increases and survivorship, although recruitment failure has still been evident (Figure 3-8). Interestingly, abundance dropped in autumn 2013 but the strongest recruitment event of the present reporting period was observed. Salinity does fluctuate at the site between moderate and high (i.e. 2000-9000µScm-1), but habitat (cover) remains reasonable, although encroachment of Typha and Phragmites has occurred in recent years (due to lower flows).

The southern pygmy perch population in the upstream Development Pool, regularly detected up until 2010, appears to have been lost in recent years. Similarly, abundance in the downstream pools (upstream First Weir) have declined over the present reporting period (only a handful of adults in autumn 2012, 2013) as no recruits have been observed (Figure 3-9). The small weir acts to keep water level relatively stable, salinity also varies, and aquatic vegetation (Potamogeton tricarinatus) has declined, making conditions more suitable for generalists, with flathead gudgeon and carp gudgeon abundance increasing. Occasional catches of southern pygmy perch (one fish in autumn 2012) and river blackfish (four fish in autumn 2012) have occurred in the regulated pools downstream, as have introduced redfin and tench (four fish in autumn 2013).

State of fish communities across the EMLR, 2010 to 2013

Aquatic vegetation and reed encroachment at core pool (Angas River – Middle Creek junction), autumn 2013

The key ecological asset (southern pygmy perch) continues to persist in this reach, but the core population, although increasing in abundance between 2010 and 2012, is showing irregular recruitment and survivorship, and other populations (both upstream and downstream) have almost disappeared. Furthermore, mountain galaxias have been irregularly sampled across this reach but not recently (2012 and 2013). Thus, fish indicators for this reach have deteriorated since the last assessment and are now considered to be in poor condition (declining trend since 2009).

Southern pygmy perch (left) and tench (right) sampled from the reach, autumn 2013

State of fish communities across the EMLR, 2010 to 2013

20 2004 n=8 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2005 n=42 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2006 n=65 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 20 2007 n=14 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2008 n=50 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

Total length (mm)

Figure 3-6. Length-frequency distribution for southern pygmy perch at Angas River (Middle Creek junction), Angas Catchment (Reach 5) from 2004 to 2008.

State of fish communities across the EMLR, 2010 to 2013

20 2009 n=53 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2010, n=9 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2011, n=30 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 20 2012, n=46 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2013, n=20 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

Total length (mm)

Figure 3-7. Length-frequency distribution for southern pygmy perch at Angas River (Middle Creek junction), Angas Catchment (Reach 5) from 2009 to 2013 (graphs below the dotted line denote the current reporting period).

State of fish communities across the EMLR, 2010 to 2013

Angas River – upstream of First Weir (ds North Parade), autumn 2013

20 2007 n=43 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2008 n=45 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 Total length (mm)

Figure 3-8. Length-frequency distribution for southern pygmy perch at Angas River (First Weir), Angas Catchment (Reach 5) in 2007 and 2008.

State of fish communities across the EMLR, 2010 to 2013

20 2009 n=45 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2010, n=33 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2011, n=19 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 20 2012, n=2 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2013, n=3 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

Total length (mm)

Figure 3-9. Length-frequency distribution for southern pygmy perch at Angas River (First Weir), Angas Catchment (Reach 5) in 2009 to 2013 (graphs below the dotted line denote the current reporting period).

State of fish communities across the EMLR, 2010 to 2013

Reach 6 – Angas lowland channel

The lowland Angas River reach maintains a self-sustaining population of river blackfish and a diverse groundwater dependent fish community (i.e. the presence of other native fish and conversely the absence and low abundance of introduced species). Baseline survey was undertaken in 1999, with a monitoring frequency of one in two years at this site beginning in 2004, and at least annual monitoring occurring between 2008 and 2013.

The abundance of river blackfish was highest (nearly double) in the first monitoring in 2004 before dropping considerably in 2006 then remaining relatively stable between 2008 and 2011 (Figure 3-10 and Figure 3-11). Across this time, there was evidence of ongoing recruitment and reasonable survivorship, with fish between 100-150mm represented in autumn sampling each year, and a consistent spread of lager (older) fish between 150-300mm. In later years, however, there has been an aging of the population (and reducing numbers of 100−150mm fish) and abundance has declined between 2011 and 2013. The diversity of the fish community has remained relatively stable from 1999 to 2013 but a shift in composition is evident. Mountain galaxias have not been recorded since autumn 2010, flathead gudgeon are now regularly sampled (from autumn 2008 onwards) and there has been a dramatic decline in carp gudgeon abundance by an order of magnitude (100s recorded in 1999−2006, 10s from 2008−2013). No diadromous species were recorded at the site and introduced species (common carp, Gambusia and tench) are present but in low abundance.

As the prolonged drought intensified, autumn salinity increased gradually to approx. 8000µScm-1 (from 6000µScm-1 in 2004) but fresher conditions have been experienced over the present reporting period (2011−2013, 3190−7700µScm-1). Similarly, flows that declined and eventually ceased over the drought have been recovered in recent years. Whilst conditions have improved, habitat appears to have declined, firstly through the prevalence of filamentous algae smothered in black slime (in autumn 2009, 2010) and then a reduction in overall aquatic vegetation (20% in 2009-2010; 5% from 2011−2013). Hammer (2009) forecast that this community shift may represent a sign of ecosystem change that could impact upon river blackfish as a top-order predator, which was confirmed by monitoring over the present reporting period.

Fish-related ecological assets in this reach are still present but recruitment failure and declining abundance suggest that predictions of Hammer (2009) are now being realised. Thus, overall this reach is experiencing a declining trend and is considered to be in average condition.

State of fish communities across the EMLR, 2010 to 2013

Angas River - Flow gauge site, autumn 2013 (top) and large sampled river blackfish in net (bottom photo)

State of fish communities across the EMLR, 2010 to 2013

5 2004, n=58 4

Frequency

0 0 50 100 150 200 250 300 5 2005, n=0

2 Frequency 1

0 0 50 100 150 200 250 300

5 2006, n=36

Frequency

0 0 50 100 150 200 250 300

5 2007 n=0

2 Frequency

0 0 50 100 150 200 250 300

5 2008, n=24 4

Frequency

0 0 50 100 150 200 250 300

Total length (mm)

Figure 3-10. Length-frequency distribution for river blackfish at Angas River (Flow Gauge), Angas Catchment (Reach 6) between 2004 and 2008.

State of fish communities across the EMLR, 2010 to 2013

5 2009, n=26 4

Frequency

0 0 50 100 150 200 250 300

5 2010, n=28

Frequency

0 0 50 100 150 200 250 300

5 2011, n=25 4

Frequency 1

0 0 50 100 150 200 250 300 5 2012, n=18

Frequency

0 0 50 100 150 200 250 300

5 2013, n=10

2 Frequency 1

0 0 50 100 150 200 250 300 Total length (mm)

Figure 3-11. Length-frequency distribution for river blackfish at Angas River (Flow Gauge), Angas Catchment (Reach 6) between 2009 and 2013 (graphs below the dotted line denote the current reporting period).

State of fish communities across the EMLR, 2010 to 2013

Reach 7 – Angas ephemeral channel

Assessment of fish related EWR in this reach targets flow connection to evaluate migratory functional processes (e.g. appropriate periods of connectivity for migration). Primarily, linkage of the Angas River with Lake Alexandrina may allow upstream passage of diadromous fish known to historically occur (e.g. congolli). This reach maintains irregular connection with pools generally containing some water up until spring before drying over summer in almost all years. Following periods of stream flow over 2007 and 2008, several pools were sampled in spring, but no diadromous species were observed. Low numbers of mountain galaxias were recorded, which appeared to all be young-of-year juveniles <65mm, and these likely colonised through downstream drift of larvae during flows. These sites were again sampled in spring 2009 but water depth was low and no fish were observed (except one flathead gudgeon). Over the present reporting period, these sites were visited annually in autumn and were dry in 2010, 2011 and 2013. In an exception to the general trend, in 2012 this reach maintained bank level water (approx. 1.5m) and was inhabited by a range of introduced species (common carp, goldfish, gambusia). Inconsistent water availability prevents the persistence of a fish community and the lack of diadromous, eurhyaline or terminal wetland species suggests successful upstream migration through this reach does not occur. Thus, this reach remains in poor condition, as it was in the 2009 assessment.

Small runoff pool at the otherwise dry Angas River – Watson Park Road, autumn 2013

State of fish communities across the EMLR, 2010 to 2013

Reach 8 – Terminal wetland

The terminal wetland of the Angas River comprises a narrow channel before entering Lake Alexandrina, and is an important off-channel habitat having a diverse fish community, with southern pygmy perch and Murray hardyhead having been recorded there. The Angus mouth downstream of Bagley Bridge was monitored in 1999 and 2001, and every autumn since 2004 (until 2013). A diverse fish community (including southern pygmy perch in autumn 2007) was observed up until it dried in summer/autumn 2008 due to regionally low Lake Alexandrina levels. Strong recolonisation by euryhaline, diadromous and wetland generalist species occurred as the reach refilled in spring 2008 as a result of Angas River stream flow. However the site was dry again by autumn 2009 and remained dry in autumn 2010. Again, a diverse fish community was soon present (autumn 2011) following the return of water. As of autumn 2013, nine species were present, all in low abundance, with introduced species (common carp, Gambusia, goldfish, redfin) and freshwater generalists (flathead gudgoen, carp gudgeon) most common. At this time, low salinity (877µScm-1) and dead Typha was the dominant habitat (submerged aquatic vegetation was low).

Monitoring of Turveys Drain in the general area of the Angas terminal wetland, and sometimes influenced by Angas flows (directly via flooding across a lowland swamp but also by general local water quality from discharge into the Lake). Overall it is likely to mostly reflect water requirements associated with Lake Alexandrina, however monitoring data is presented here for broader reference and has the nearest population for potential recolonisation of the Angas. Southern pygmy perch has been the main ecological asset at the site, and strong recruitment and high abundance of southern pygmy perch was evident up to autumn 2006. Despite artificial watering as regional water availability declined, habitat cover remained stable but salinities did deteriorate (EC up to 7500 µScm-1 in 2010, a tenfold increase since 2001) and the population rapidly declined with only <5 fish observed each autumn between 2007 and 2010 (note that spring sampling in 2008 and 2009 detected high numbers, 50 fish) (Figure 3-12 and Figure 3-13). With the increase in lake levels, conditions improved (EC, 410- 788µScm-1 over 2012−2013 and dense Myriophyllum is maintained) and a diverse fish community has returned (seven species in autumn 2013). However, introduced Gambusia dominate and despite reintroductions (300 fish in spring 2011) only one southern pygmy perch has subsequently been detected (a recapture in autumn 2012) in autumn/spring sampling over 2011−2013 (Bice et al. 2013). Murray hardyhead were recorded over 2008 and 2009 but have not been detected since.

State of fish communities across the EMLR, 2010 to 2013

Dense Myriophyllum (top) and the last sampled southern pygmy perch (bottom) at Angas River/Lake Alexandrina – Turveys Drain, autumn 2013

The assessment of fish indicators is mixed; whilst a diverse fish community has been maintained at both sites, southern pygmy perch are now absent (with little chance of localised re-colonisation) and introduced species are particularly common. Overall this reach is considered in poor condition.

State of fish communities across the EMLR, 2010 to 2013

20 2004 n=40 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2005 n=62 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2006 n=84 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 20 2007 n=1 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2008 n=3 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 Total length (mm)

Figure 3-12. Length-frequency distribution for southern pygmy perch at Angas River/Lake Alexandrina (Turveys Drain), Angas Catchment (Reach 8) between 2004 and 2008.

State of fish communities across the EMLR, 2010 to 2013

20 2009 n=5 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2010, n=1 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2011, n=0 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 20 2012, n=1 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2013, n=0 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

Total length (mm)

Figure 3-13. Length-frequency distribution for southern pygmy perch at Angas River/Lake Alexandrina (Turveys Drain), Angas Catchment (Reach 8) between 2009 and 2013 (below the dotted line denote the current reporting period).

State of fish communities across the EMLR, 2010 to 2013

Overall performance report

In 2009, the Angas catchment was stressed but important ecological assets persisted in MODERATE condition (Figure 3-14). Improved water availability over the present reporting period only acted to enhance ecological assets (e.g. mountain galaxias) in the upper pool-riffle reach (although declines did occur in 2012) and help to maintain river blackfish in the lowland reach. However, southern pygmy perch populations declined slightly in mid pool-riffle reach and at in the terminal wetlands. Overall, the catchment was again classified as being in MODERATE condition the end of the present reporting period (Table 3-3).

9 Reach types

8 Headwaters Upper 7 Mid

6 Gorge Lowland Wetlands 5 4

Condition score (out of 9) (out score Condition 1 0 2009 2010 2011 2012 2013 Year

Figure 3-14. Trend in condition score across reach types of the Angas Catchment between 2009 and 2013. Scores for each reach type reflect the median score for all ecological assets present in that reach type (reach types that were not sampled are not presented).

State of fish communities across the EMLR, 2010 to 2013

Table 3-3. 2013 report card for the Angas catchment – a comparison of the performance against fish indicators (blacked out indicators are not relevant to that ecological asset). For each fish indicator, a tick ( ) represents a positive result (e.g. a 1 for presence, a 2 & 3 for recruitment and survivorship indicators and a score > 4 for diverse fish community), and for all other results a cross ( ) shown. For alien species, ticks indicate the desirable result was observed (i.e. <30% of total site numbers) and crosses indicate a negative result (i.e. >30 of total site numbers). Condition scores for each ecological asset (out of 9) reflect the sum for each indicator (out of 7) plus an alien species score (out of 2). The median of scores for all ecological assets are used to estimate the overall catchment score. Reach scores and overall catchment scores are defined as good (>6, xxx), moderate (3 to 6, xxx) and poor (<3, xxx). See section 2.6 for full explanations. ASSESSMENT for 2013 INDICATOR

Relevant site

Condition

Alien species

Reach Reach score

Presence

Recruitment ECOLOGICAL ASSET Survivorship Reach 3 – Upper pool-riffle channel Quarry Rd Mountain galaxias 1 3 2 6 2 8.5 Searle St Mountain galaxias 1 3 3 7 2 Reach 5 - Mid pool-riffle channel Middle Ck junction Southern pygmy perch 1 2 1 4 2 4.5 us First Weir Southern pygmy perch 1 0 0 1 2 Reach 6 – Lowland channel River blackfish 1 0 3 4 Flow Gauge 2 5.0 Diverse fish community 2 2 Reach 8 – Angas mouth (terminal wetland) Turvey Drain Southern pygmy perch 0 0 0 0 0 1.5 Angas mouth Diverse fish community 2 2 1

Median 4.8

State of fish communities across the EMLR, 2010 to 2013

3.3 Bremer Catchment

The Bremer is a large catchment (589km2) that, under certain conditions, also contributes intermittent flow to a lowland channel, Mosquito Creek (Ferris-McDonald Catchment) that branches off near Langhorne Creek. The Bremer River runs roughly north to south parallel with the base of the MLR extending from small headwaters above Harrogate, through Callington then along a lowland plain via Langhorne Creek to its junction with Lake Alexandrina. The latter sections of the River from above Langhorne Creek are today ephemeral (but historically were large spring fed pools), with a small section of permanent river channel at the junction of the Lake. Two major tributaries drain from the flank of the range east towards the Bremer River: (a) the Mt Barker Creek sub catchment that includes Mt Barker, Western Flat, Nairne and Dawesley creeks, and (b) Rodwell Creek, joining the Bremer just below Woodchester. Hence sections of the catchment contrast greatly in topography, geology, rainfall and vegetation, particularly between the Mt Barker Creek sub-catchment (high rainfall, elevation and gradient, considerable urban areas) and elsewhere (more agricultural, low rainfall and topography). Stream habitats vary accordingly in the two distinct sub-regions of the catchment, with shallower creeks in headwater areas compared to a series of deep irregular pools along the Bremer main channel. Significant pollution has occurred as a result of mining activities along-side Dawesley Creek at Brukunga and stock access is commonplace in areas that are not urbanised.

Overall, nine provisional reaches have been defined in the Bremer River Catchment (Figure 3-15). Fish related assets across these reaches, identified by Hammer (2004), are shown in Table 3-4 and Table 3-5. The priority asset in the catchment is a highly restricted and isolated remnant population of river blackfish in Rodwell Creek (Reach 2), plus mountain galaxias populations and other diverse native fish communities including diadromous and migratory species (Reaches 2−4, 6 & 8). The environmental objectives associated with these ecological assets are also detailed in Table 3-5 and related to relevant EWR tables of Section 2.5.

A range of data has been collected in this catchment opportunistically, but specific long-term monitoring sites occur at Mt Barker Creek and Rodwell Creek. Several long-term sites were initiated following the 2007 review, mainly the upper catchment at Harrogate, Mt Barker Creek, the Lowland channel (gauge station) and terminal wetland (Bremer Mouth). Over the present reporting period, nine sites in the catchment were sampled annually.

State of fish communities across the EMLR, 2010 to 2013

0 2.5 5 10 ¯ Kilometers Lake Alexandrina Figure 3-15. Map of the Bremer River Catchment. The main channels of the catchment (including terminal wetland) are marked as dark blue whereas smaller tributaries streams are marked light blue. Lake Alexandrina is denoted as grey

State of fish communities across the EMLR, 2010 to 2013

Table 3-4. Distribution patterns and significant environmental assets in the Bremer Catchment relating to fish species and communities (plus opportunistic data for other biota). Specific asset/pattern Location EWR Table River blackfish Reach 2 (historically Table 2-5 throughout catchment). Mountain galaxias Reaches 2, 3, & 4 Table 2-4 Carp gudgeons Reaches 2, 3, 5, 6 & 7 Table 2-7 Lower Bremer diverse fish community Reach 6 Table 2-10 (historically also Reach 8) Bremer & Mosquito Creek terminal wetlands diverse fish Reach 9 Table 2-6, Table 2-8 & community Table 2-11 Presence of diadromous fish species in the Lower Reaches 6, 8 & 9 Table 2-8 Bremer No permanent fish communities due to lack of Reach 1 NA permanent water

Table 3-5. Summary of environmental objectives by reach for fish related ecological assets in the Bremer River Catchment. Asset Environmental Objective Reach 1 – Bremer Catchment headwaters NA Reach 2 – Rodwell Creek pool/riffle channel under groundwater influence (Table 2-4, Table 2-5, Table 2-7 & Table 2-9) River blackfish (upper section of reach) Maintain (2 existing pools) and restore (extend range to improve security) a self-sustaining population Mountain galaxias (upper section of reach) Maintain and restore a self-sustaining population Carp gudgeons (lower section of reach) Maintain a self-sustaining population Reach 3 – Upper Bremer pool-riffle channel (Table 2-4 and Table 2-7) Mountain galaxias Restore a self-sustaining population (recent local extinctions with pool drying) Carp gudgeons Maintain a self-sustaining population Reach 4 – Upper pool-riffle tributaries (Western Flat/Mt Barker, Nairne and Dawesley creeks) (Table 2-4) Mountain galaxias Maintain or Restore a self-sustaining population (locally extinct in Dawesley Creek – mine pollution) Reach 5 – Bremer main channel above Mt Barker Creek junction (Table 2-7) Carp gudgeons Maintain a self-sustaining population Reach 6 – Bremer deep pool sequence under groundwater influence below Mt Barker Creek junction (Table 2-7 & Table 2-8, potentially Table 2-5) Diverse native fish community including carp gudgeons, Maintain diversity and composition of fish community diadromous species and migratory species Maintain community of diadromous and migratory species River blackfish and Murray cod (historic records and Maintain or restore self-sustaining natural populations if may be detected with additional sampling) located Reach 7 – Mt Barker Creek Gorge and pool-riffle channel (Table 2-7, potentially Table 2-4, Table 2-5 &Table 2-8) Carp gudgeons, historically river blackfish, mountain Maintain a self-sustaining population galaxias and diadromous congolli Restore community of rare and diadromous species Reach 8 – Ephemeral channels and floodplains (Table 2-8) Dispersal pathway of diadromous and migratory species Maintain access for diadromous and migratory species; (historically was permanent pool habitat) restore permanent populations Reach 9 – Terminal wetlands under Lake Alexandrina influence (Table 2-8 & Table 2-10) Diverse native fish community including diadromous Maintain diversity and composition of fish community and migratory species

State of fish communities across the EMLR, 2010 to 2013

Reach 2 – Rodwell Creek (upper pool-riffle channel)

The key ecological asset in this reach is a remnant population of river blackfish, known to occur in only two stretches in the reach - indeed the whole Bremer catchment (they were rediscovered in 2004 after ~50 years of no records). The sites are on two Highland Valley properties (a & b), and represent isolated spring fed pools during dry periods. Flow has become intermittent in the creek with a lack of any seasonal surface water flow in some years (2007 and 2008). The blackfish sites were sampled intensively (fyke netting) during inventory sampling in 2004, with subsequent less intensive checks performed (bait traps) annually. Sampling of site (a) from 2004 to 2007, revealed consistent signs of recruitment, albeit by annual appearance of the 2+ cohort into bait trap catches Figure 3-16. Smaller fish were sampled with fykes nets in 2004 or periodically observed with night observations. This suggests they do not become consistently catchable with bait traps at this site until they reach 150mm. Survivorship after the 2+ size class however, appears to be relatively low with only occasional individuals trapped or observed >200mm. At site (b) there was a similar pattern of regular recruitment witnessed by peaks of fish corresponding to 2+ fish in 2004−2007, with poor survivorship (i.e. few fish >250mm) (Figure 3-18).

Over the period of critical water shortage (2007 to 2010), the localised population of river blackfish persisted, undoubtedly a consequence of intensive management that was undertaken (Hammer 2010). In 2007, the reach deteriorated considerably and the water level became critical at site (a) in autumn 2008 (max depth 0.7m, general depth <0.5m) with a high risk of pool drying. In response emergency artificial watering was implemented to supplement water in the pool with bore water tanked to the site. Nine fish were also rescued from the pool into captivity as a backup in case of catastrophe. Site (b) has had consistently low dissolved oxygen levels at depths greater than 0.3m since autumn 2007, with no management intervention occurring, and fish were not recorded at the site in 2008 or 2009 (Figure 3-17). Environmental conditions at the sites over this time was variable reflecting reducing freshwater inflows (i.e. no stream flow in the 2007 and 2008 flow seasons, apparent reduction in groundwater input) with salinities at site (a) increasing from 4300µScm-1 in 2004 to 7200µScm-1 in 2008, although artificial watering has reduced salinity and improved depth and dissolved oxygen from autumn 2008 onwards (data not shown). Salinity at site (b) rose steadily from 6000 to >10,000µScm-1 between 2004 and 2009.

During autumn sampling over the present reporting period the species has been detected in low numbers at the site that was intensively managed through the period of critical water shortage and

State of fish communities across the EMLR, 2010 to 2013 recruitment appeared absent (Figure 3-17). In 2012, spring sampling of this site and nearby pools did detect greater numbers and signs of recent recruitment, however, these pools deteriorate considerably over summer months (and 3 actually dry) so the survival of these fish is not assured. The species was again detected is several pools in spring 2013 but in much lower numbers. The species has been absent from the other regularly monitored site since 2008 and poor water quality (DO <2mgL-1) typically prevails over some summer months (and during autumn sampling period).

State of fish communities across the EMLR, 2010 to 2013

10 2004, n=17 9 8 7 6 5 4

Frequency 3 2 1 0 0 50 100 150 200 250 300

10 2005, n=5 9 8 7 6 5 4

Frequency 3 2 1 0 0 50 100 150 200 250 300

10 2006, n=6 9 8 7 6 5 4

Frequency 3 2 1 0 0 50 100 150 200 250 300 10 2007 n=1 9 8 7 6 5 4

Frequency 3 2 1 0 0 50 100 150 200 250 300

10 2008, n=6 9 8 7 6 5 4

Frequency 3 2 1 0 0 50 100 150 200 250 300 Total length (mm)

Figure 3-16. Length-frequency distribution for river blackfish in Rodwell Creek (Highland Valley (a)), Bremer Catchment (Reach 2) from 2004 to 2008.

State of fish communities across the EMLR, 2010 to 2013

10 2009, n=12 9 8 7 6 5 4

Frequency 3 2 1 0 0 50 100 150 200 250 300

10 2010, n=4 9 8 7 6 5 4

Frequency 3 2 1 0 0 50 100 150 200 250 300

10 2011, n=4 9 8 7 6 5 4

Frequency 3 2 1 0 0 50 100 150 200 250 300 10 2012, n=4 9 8 7 6 5 4

Frequency 3 2 1 0 0 50 100 150 200 250 300

10 2013, n=1 9 8 7 6 5 4

Frequency 3 2 1 0 0 50 100 150 200 250 300 Total length (mm)

Figure 3-17. Length-frequency distribution for river blackfish in Rodwell Creek (Highland Valley (a)), Bremer Catchment (Reach 2) from 2009 to 2013 (graphs below the dotted line denote the current reporting period).

State of fish communities across the EMLR, 2010 to 2013

10 2004, n=8 9 8 7 6 5 4

Frequency 3 2 1 0 0 50 100 150 200 250 300

10 2005, n=0 9 8 7 6 5 4

Frequency 3 2 1 0 0 50 100 150 200 250 300

10 2006, n=9 9 8 7 6 5 4

Frequency 3 2 1 0 0 50 100 150 200 250 300 10 2007 n=4 9 8 7 6 5 4

Frequency 3 2 1 0 0 50 100 150 200 250 300

10 2008, n=6 9 8 7 6 5 4

Frequency 3 2 1 0 0 50 100 150 200 250 300 Total length (mm)

Figure 3-18. Length-frequency distribution for river blackfish in Rodwell Creek (Highland Valley (b)), Bremer Catchment (Reach 2) from 2004 to 2008.

State of fish communities across the EMLR, 2010 to 2013

Reach 3 – Upper Bremer

The Upper Bremer catchment has undergone a dramatic reduction in permanent pool habitat since 2001, impacting the presence and/or distribution of native fish species. Monitoring has been opportunistic, with more regular observations since autumn 2008. Mountain galaxias and carp gudgeons have not been recorded at sites in Harrogate since 2002 and 2004 respectively as pools have become ephemeral. Over 2008 and 2009, the Harrogate sites experienced severe water shortage and refuge pools were concentrated and saline (depth, 0.3-0.8m, 13920−15,000µScm-1), with no fish recorded during autumn sampling. Increased flow during the present reporting period, led to increases in water level (up to 1.5m) and decreases in salinity (down to 1111µScm-1 in 2010) with fish (the freshwater generalist flathead gudgeon) only recolonising from 2011. Similar habitat deterioration occurred over 2008−2009 at the Military Road site with refuge pools contracting and then drying over this period. With increased flows, carp gudgeon have not recolonised, but encouragingly a low number of mountain galaxias (5 fish) were recorded in 2010. The presence of this species was only brief and has been absent from autumn sampling since this time. In autumn 2013, high salinities (>16,910µScm-1) were once again observed at the Military Road site and no fish were recorded. This reach is stressed (as it was in 2009) with ongoing declines in water availability creating conditions that appear unsuitable for fish species to persist.

Reach 4 - Tributaries

This reach contains wetter tributaries in the Mount Barker Creek sub-catchment including Dawesley, Nairne and Mount Barker creeks. The main ecological asset identified is mountain galaxias (river blackfish also occurred historically), with a monitoring site on Mt Barker Creek just below Adelaide Road. This site has baseline data from autumn 2002 and 2004 and has been a regular monitoring site since autumn 2007. As of 2013, mountain galaxias remain present at this site, which represents a key refuge in the upper catchment. However, abundances were low with limited recruitment in autumn 2008 and 2009, with diminishing water availability and quality recorded at the site (i.e. single pools compared to continuous reach; anoxic conditions). No fish were caught in the main sampling reach in autumn 2009, with range mapping collecting fish upstream and used for length frequency analysis. Length data highlights some survivorship, particularly in spring 2008 where catchability was better due to clearer water and flow (Figure 3-19). The species was observed in low abundance over the present reporting period with a slight increase realised in autumn 2011 (Figure 3-20). Ongoing recruitment failure was evident with only a single 0+ fish observed (in 2011). At the site, salinity is

State of fish communities across the EMLR, 2010 to 2013 variable but steady (range 1300-2850µScm-1) with pool dissolved concentrations often prevailing (<2mg L-1).

Remaining small refuge pool at the Mount Barker Creek site autumn 2009

12 11 2007, n=10 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2008, n=4 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

Total length (mm) Figure 3-19. Length-frequency distribution for mountain galaxias at Mount Barker Creek, Bremer Catchment (Reach 4) from 2007 to 2008.

State of fish communities across the EMLR, 2010 to 2013

12 11 2009, n=5 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2010, n=9 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2011, n=17 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 12 11 2012, n=3 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2013, n=5 10 9 8 7 6 5 Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 Total length (mm)

Figure 3-20. Length-frequency distribution for mountain galaxias at Mount Barker Creek, Bremer Catchment (Reach 4) from 2009 to 2013 (graphs below the dotted line denote the current reporting period).

State of fish communities across the EMLR, 2010 to 2013

Reach 5- Bremer mid-channel

Sampling did not occur in this reach over the present reporting period (or 2007 to 2009).

Reach 6 – Bremer Lowland Channel

Ecological assets identified in this reach include a diverse fish community, including migratory species (both diadromous and potamodromous). Baseline data occurred in 2004, with annual monitoring being initiated in autumn 2008 at two sites, namely at the Hartley flow gauging station and just upstream of the Rodwell Creek junction (discontinued after autumn 2009). In spring 2007, fifty adult common galaxias (size rage 90−130mm) congregated below the flow gauge were sampled, however only a few individuals were recorded after this time (three common galaxias in autumn 2008, and only a single very large adult congolli). A large Murray-Darling golden perch was recorded at the Rodwell Creek site by a landholder in 2008 (angled: 425mm) indicating the presence of the potamodromous functional group in the reach (albeit with no smaller fish detected). The general diversity of the native fish community was also low, with flathead gudgeon the only other species recorded in any significant abundance. Conversely alien fishes were common in the reach, comprising juvenile and adult common carp at the flow gauge site and juvenile and adult redfin and gambusia at the Rodwell Creek junction. Salinity was moderate (1200−6000µScm-1) with a high reading at the concentrated flow gauge pool in autumn 2009 (18,500µScm-1). Due to disconnection and drying of refuge pools, the fish community was in a poor state at the end of the last reporting period (2009).

The reach was dry during autumn 2010, but following increased water availability and connectivity a fish community with seven species was observed in autumn 2011, including common galaxias. At this stage, the monitoring pool was deep (1.5m) and fresh (2480µScm-1) with reasonable habitat cover (namely snags and rocks). Since 2011, however, water availability has again declined and the monitoring pool has become progressively shallow (0.8m in 2013) and saline (14,900µScm-1 in 2013). Fish remaining in this isolated pool (when disconnected) have persisted with flathead gudgeon abundant, the alien Gambusia experiencing a boom in numbers (>4000 fish in 2012), and common carp and redfin present. Large congolli also remain in the pool but will require broader connectivity over the next couple of years to migrate downstream to complete their life cycle. At the end the present reporting period, the reach is again in a poor state, clearly suffering from reduced stream flows in the catchment.

State of fish communities across the EMLR, 2010 to 2013

Bremer flow gauge pool autumn 2013 (looking downstream)

Reach 7 – Mt Barker Creek Gorge

This reach has not been sampled as part of the EWR assessment of the present project. Yet, baseline monitoring (21 sites) of Mount Barker Creek along this reach in autumn 2013 and 2014 identified low numbers of fish across eight species (Whiterod 2014). Ecological assets include populations of mountain galaxias and the presence of diadromous congolli at downstream sites indicating unimpeded connectivity to Murray River estuary (through Lake Alexandrina and Bremer River) occurs. Moderate numbers of alien species were detected, particularly Gambusia. Across this reach salinities were typically moderate (740−1788µScm-1) but at some sites salinities in excess of 9000µScm-1 were experienced and habitat cover was generally low, with no submerged aquatic vegetation observed.

Reach 8 – Lowland floodplain

A lack of permanent water limits habitat availability and also fish sampling in this reach. Yet, opportunistic sampling during periods of low flow is necessary to investigate if suitable habitat and connectivity, which is clearly critical to the movement of diadromous species observed in upstream reaches, is maintained through this reach.

State of fish communities across the EMLR, 2010 to 2013

Recently installed flow gauge at Bremer River – Balandown Road, autumn 2013

Reach 9 – Terminal wetland

The terminal wetland of the Bremer comprises a narrow channel before entering Lake Alexandrina, and is an important off-channel habitat having a diverse community comprising freshwater generalists, diadromous, potamodromous and euryhaline species. Information for comparison was collated in 2004 inventory sampling, with annual monitoring occurring since autumn 2007. The terminal wetland maintained a diverse fish community with the threatened Murray hardyhead apparently colonising the site sometime around spring 2008 and good numbers of common galaxias occurring, including large numbers of juveniles (233 fish) in spring 2008.

This reach was impacted by reduced region inflows and subsequently dried in summer/autumn 2009 after disconnecting from Lake Alexandrina. The reach was briefly inundated (winter to early summer 2009) before drying again in autumn 2010 (some shallow (0.1m) pools persisted). In autumn 2010, no fish were recorded but with the increase in water availability and reduced salinity (below 800 µScm-1 since autumn 2011), an increasingly diverse fish community has returned (up to 11 species in 2013), albeit with most species in low abundance (except flathead gudgeon in spring 2010, 992 fish). Similar functional groups to those prior to the drying are now persisting (e.g. diadromous, estuarine species) but Murray hardyhead are yet to re-colonise following inundation of the reach (last observed in spring 2008 prior to drying). As with the terminal wetlands of the River Murray (i.e. Marne, Reedy

State of fish communities across the EMLR, 2010 to 2013 and Rocky Gully) and the Angas (see previous), regional critical water shortages led to the drying of habitat during the drought. However, with improved water availability and connectivity over the present reporting period, diverse fish communities have returned, although key threatened species have often remained absent (e.g. Murray hardyhead).

Bremer River Mouth with (autumn 2012, bottom) and without water (autumn 2009, top)

State of fish communities across the EMLR, 2010 to 2013

Overall performance report

In 2009, the Bremer Catchment was considered to be in POOR condition, with indicators or actual failure of most ecological assets (Figure 3-21). Over the present reporting period, increased flows and connectivity improved the reach scores, but many ecological assets such as river blackfish in the upper reach are experiencing ongoing decline. Overall, the catchment was classified as being in MODERATE condition the end of the present reporting period (Table 3-6).

9 Reach types

8 Headwaters Upper 7 Mid 6 Gorge Lowland 5 Wetlands

3 2

of 9) (out score Condition 1

0 2009 2010 2011 2012 2013

Year Figure 3-21. Trend in condition score across reach types of the Bremer Catchment between 2009 and 2013. Scores for each reach type reflect the median score for all ecological assets present in that reach type (reach types that were not sampled are not presented).

State of fish communities across the EMLR, 2010 to 2013

Table 3-6. 2013 report card for the Bremer catchment – a comparison of the performance against fish indicators (blacked out indicators are not relevant to that ecological asset). For each fish indicator, a tick ( ) represents a positive result (e.g. for present, a 2 & 3 for recruitment and survivorship indicators and a score > 4 for diverse fish community), and for all other results a cross ( ) shown. For alien species, ticks indicate the desirable result was observed (i.e. <30% of total site numbers) and crosses indicate a negative result (i.e. >30 of total site numbers). Condition scores for each ecological asset (out of 9) reflect the sum for each indicator (out of 7) plus an alien species score (out of 2). The median of scores for all ecological assets are used to estimate the overall catchment score. For ecological assets and overall catchment score are defined as good (>6, xxx), moderate (3 to 6, xxx) and poor (<3, xxx). See section 2.6 for full explanations. ASSESSMENT for 2013 INDICATOR

Relevant site

Condition

Alien species

Reach Reach score

Presence

Recruitment ECOLOGICAL ASSET Survivorship Reach 2 – Rodwell Creek pool-riffle channel Highland (b) River blackfish 0 0 0 0 0 2.0 Highland (a) River blackfish 1 0 1 2 2 Reach 3 – Upper Bremer pool-riffle channel Carp gudgeon 0 0 0 0 Military Rd 0 Mountain galaxias 0 0 0 0 1.0 Carp gudgeon 0 0 0 0 Harrogate main bridge 2 Mountain galaxias 0 0 0 0 Reach 4 - Upper pool-riffle tributary creeks Mt Barker footbridge Mountain galaxias 1 0 2 3 2 5.0 Reach 6 – Lowland deep pool sequence Flow gauge Diverse fish community 2 2 1 3.0 Reach 9 – Bremer mouth (terminal wetland) Mouth below bridge Diverse fish community 3 3 0 3.0

Median 3.0

State of fish communities across the EMLR, 2010 to 2013

3.4 Currency Catchment

The most southerly of the EMLR catchments, Currency Creek is a small (88km2) and heavily branched system, experiencing moderate rainfall. It drains swampy upland areas in an easterly direction through relatively steep alluvial and rocky creeks. The main stream network comprises a north and south branch that join just before a steep gorge and then flow on a gradual slope past Stuarts Bridge (Mt Compass to Goolwa Road). There is a small waterfall just above the railway bridge near the Currency Creek Township and from here Currency Creek meanders toward an extended arm of Lake Alexandrina via a river channel. Remnant vegetation in the catchment is sparse, with often only a thin riparian strip of gums present. Flow is largely intermittent in most of the catchment (today) but localised springs occur at several sites. Pools are generally small and shallow, with heavy erosion and siltation obvious in the mid catchment. Larger and deeper pools do occur in the lower section of the catchment above and below the waterfall. Cover values are generally low comprising snags and some emergent vegetation (submerged aquatic plants were rare). Some stream sections are fenced, however much of the catchment has unrestricted stock access.

Overall, seven provisional reaches have been defined in the Currency Creek Catchment (Figure 3-22). Fish related assets identified by Hammer (2004) are shown in Table 3-7 and Table 3-8. These include patchy populations of mountain galaxias and diverse native fish communities in lowland and terminal wetland habitat (Reaches 6 & 7). Yarra pygmy perch have been recorded historically from Reach 7 and Reach 8 (edge of Goolwa Channel) (Hammer 2007b) and river blackfish and southern pygmy perch may have once occurred above the waterfall. The environmental objectives associated with these ecological assets are also detailed in Table 3-8 and related to relevant EWR tables of Section 2.5.

Sampling was infrequent in this catchment between 2001 and 2007, but following the 2007 review, long-term monitoring sites were established (based on sites from the 2004 baseline inventory) across four different reaches. Over the present reporting period (2010−2013), five sites were monitored across these four reaches.

State of fish communities across the EMLR, 2010 to 2013

0 1.25 2.5 5 Goolwa channel ¯ Kilometers Figure 3-22. Map of the Currency Creek Catchment. The main channels of the catchment (including terminal wetland) are marked as dark blue whereas smaller tributaries streams are marked light blue. The River Murray (Goolwa Channel) is denoted as grey.

Table 3-7. Distribution patterns and significant environmental assets in the Currency Creek Catchment relating to fish species and communities. Specific asset/pattern Location EWR Table No permanent fish communities due to lack of Reach 1 N/A permanent water Mountain galaxias Reaches 2, 3, 4 (marginal) Table 2-4 & 5 Flathead gudgeon Reaches 3-7 Table 2-7 River blackfish potentially occurred historically Possibly reaches 4 & 5 Table 2-5 and Table 2-9 Lower Currency/terminal wetland diverse fish Reach 6 & 7 Table 2-11 community Potential for diadromous fish species (congolli, common Reach 9 Table 2-8 and Table 2-11 galaxias, lamprey) to colonise lower Currency Creek

State of fish communities across the EMLR, 2010 to 2013

Table 3-8. Summary of environmental objectives by reach for fish related ecological assets in the Currency Creek Catchment. Asset Environmental Objective Reach 1– Currency headwaters N/A Reach 2 – Upper pool-riffle channel (EWR Table 2-4) Mountain galaxias (restricted and declining populations) Maintain or restore self-sustaining population Reach 3 – Upper pool-riffle channel (EWR Table 2-4) Mountain galaxias (restricted and declining populations) Maintain or restore self-sustaining population Reach 4 – Currency Creek main channel and gorge (EWR Table 2-4 and Table 2-7) Mountain galaxias (longer term objective) Restore self-sustaining population Flathead gudgeon Maintain a self-sustaining population Reach 5 – Mid pool-riffle channel above waterfall (EWR Table 2-4 and Table 2-7) Mountain galaxias Maintain or restore self-sustaining population Flathead gudgeon Maintain or restore self-sustaining population Maintain or restore self-sustaining population (if River blackfish possibly occurs identified) Reach 6 – Lowland large pool-riffle sequence (EWR Table 2-7, Table 2-8 and Table 2-10) Diverse native fish community including gudgeons, Maintain and restore diversity and composition of fish diadromous species and River Murray species. community (including gudgeon spp.)

Diadromous species (congolli, common galaxias and Maintain community of diadromous species possibly lampreys) Reach 7 – Terminal wetland under Lake Alexandrina influence (EWR Table 2-7 and Table 2-11) Diverse native fish community including diadromous Maintain and restore diversity and composition of fish species. Yarra pygmy perch at junction with Goolwa community Channel

State of fish communities across the EMLR, 2010 to 2013

Reach 2 – South arm

Baseline sampling identified mountain galaxias at some sites in this arm of Currency Creek, but no recent monitoring has occurred.

Reaches 3 & 4 – North arm

Two native species were recorded as part of the 2004 baseline inventory of the EMLR: mountain galaxias (common but patchy) and flathead gudgeon (rare). Since this time, monitoring has occurred annually (with exception of 2006) at the Kilchoan site, which has been identified as a key upland refuge for the mountain galaxias. The species has persisted at the site, but in increasingly low abundance since 2007 (Figure 3-23). In 2007, only surviving adults were detected in refuge pools, and looking further back, recruitment and survivorship were both reasonable in 2004 (not shown) and 2005. As prolonged drought across the region intensified between 2007 and 2009, increasingly diminished surface water was experienced and in autumn of each year the sampling site consisted of fewer than five small and shallow pools. Yet, strong successful spawning was detected in spring 2008 (not presented), however, there was largely recruitment failure as only a small pulse of 0+ juveniles (and no adults as well) where observed in the following autumn (2009) (Figure 3-24). It is presumed that conditions were suitable for spawning in winter/early spring 2008, but deteriorated rapidly over the summer 2008/2009 and were largely unsuitable for the species by autumn 2009.

In response to improved surface water in the first year of the present reporting period, a reasonable recruitment event occurred (Figure 3-24). Whilst these individuals appear to have survival in the next autumn (2010), numbers have declined and recruitment has not been detected since this time. The site is again experiencing concentrated conditions by autumn months and mountain galaxias numbers have declined, with no fish observed in 2012 and only a small number of 1+ fish in 2013. Gambusia remain common in remaining water at the site. Salinity has remained relatively low ranging from 751-1664µScm-1 and consistent levels of moderate cover were maintained over the present reporting period. Mountain galaxias have persisted over the reporting period but as was the conclusion in 2009, the reach is highly stressed with (increasingly) low flow periods testing the resilience of local populations.

State of fish communities across the EMLR, 2010 to 2013

12 11 2005, n=16 10 9 8 7 6 5 Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2006, n=0 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2007, n=4 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 12 11 2008, n=1 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

Total length (mm) Figure 3-23. Length-frequency distribution for mountain galaxias in Currency Creek (Kilchoan), Currency Catchment (Reach 3 & 4) from 2005 to 2008.

State of fish communities across the EMLR, 2010 to 2013

12 11 2009, n=6 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2010, n=31 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2011, n=46 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 12 11 2012, n=0 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2013, n=10 10 9 8 7 6 5 Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 Total length (mm)

Figure 3-24. Length-frequency distribution for mountain galaxias in Currency Creek (Kilchoan), Currency Catchment (Reach 3 & 4) from 2009 to 2013 (graphs below the dotted line denote the current reporting period).

State of fish communities across the EMLR, 2010 to 2013

Reach 5 – Mid pool riffle channel

Larger refuge pools occur in the mid-Currency Creek catchment and are occupied by mountain galaxias and flathead gudgeon (plus alien species). A refuge site at Stuarts Bridge was examined in 2004 baseline sampling and opportunistically in 2005 (environmental data only), and has formed part of annual monitoring since 2007. A generally large population of mountain galaxias occurs at Stuarts Bridge. Recruitment occurs regularly as observed in autumn 2008 and 2009 sampling, the latter occurring after the dry 2008 flow season (note: spring 2008 data not presented shows strong spawning) (Figure 3-25). Strong persistence of the species was also noted by the presence of older fish (>70mm). At the end of 2009, the site remained in good condition even through the recent dry conditions, acting as a key catchment refuge for mountain galaxias, and appears to have a level of natural disturbance that discourages alien species.

Stagnant pool at Currency Creek – Stuarts Bridge, autumn 2012

There was not a strong recruitment response to improved surface water in 2010 and 2011, but abundance (up to 284 fish in 2010) increased markedly and survivorship remained high (fish up to 110 mm) (Figure 3-26). However, since 2011 the site has experienced a rapid reduction in surface water and salinities have increased sharply (2640 µScm-1 in 2010; 6820 µScm-1 in 2013) with only low numbers of mountain galaxias detected. Low numbers of Gambusia continue to represent the only alien fish recorded at the site, despite brown trout recorded and heavily stocked upstream.

State of fish communities across the EMLR, 2010 to 2013

18 2004, n=45 15

Frequency 6

0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

18 2008, n=23 15

Frequency 6

0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 Total length (mm)

Figure 3-25. Length-frequency distribution for mountain galaxias in Currency Creek (Stuarts Bridge), Currency Catchment (Reach 5) in 2004 and 2008.

State of fish communities across the EMLR, 2010 to 2013

18 2009, n=118

Frequency 6

0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

18 2010, n=99 15

Frequency 6

0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

18 2011, n=117 15

Frequency 6

0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

18 2012, n=9 15

Frequency 6

0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

18 2013, n=14 15

Frequency 6

0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

Total length (mm)

Figure 3-26. Length-frequency distribution for mountain galaxias in Currency Creek (Stuarts Bridge), Currency Catchment (Reach 5) from 2009 to 2013 (graphs below the dotted line denote the current reporting period).

State of fish communities across the EMLR, 2010 to 2013

Reach 6 – Lowland channel

A small lowland channel occurs downstream of Currency Creek Waterfalls to just past Goolwa Road. This reach maintains diverse native fish community including several diadromous species. Baseline data was collected in 2003 and 2004, with annual monitoring of two nearby sites (Lions Park, downstream of Goolwa Road), initiated in autumn 2008.

High water levels below the Goolwa Bridge (autumn 2012)

The fish community in the reach remained relatively diverse over 2008 and 2009 and over the present reporting period (Figure 3-27). From 2003/2004 to 2008/2009 a slight shift in composition to exclude three wetland generalist (bony herring, smelt and unspecked hardyhead) and to include two euryhaline species (bluespot goby and Tamar goby) was observed. Over the present reporting period, both of these functional groups were largely absent for the fish community but diadromous species were common. The catch of diadromous common galaxias was variable, but generally highly abundant, from 2008 to 2013. Only larger adult fish (≥100mm) observed in autumn 2009 but a large cohort of juveniles (50-85mm) was observed in autumn 2010 and recruitment occurred consistently between 2011 and 2013 (Figure 3-27). Similar patterns were evident for the other diadromous species observed, congolli, which were present as larger individuals (>150mm) in autumn 2009 and even autumn 2010 but experienced strong recruitment in 2011 (Figure 3-28). Over the present reporting period, juveniles were detected from a diverse number of species. Whilst relatively few

State of fish communities across the EMLR, 2010 to 2013 alien species have been recorded at the site, there were booms in Gambusia (1000 fish in 2010), juvenile and also larger redfin (in 2011, 805 fish at Lions Park, 347 fish at ds Goolwa Road) and common carp (191 fish in 2010) at various times across the present reporting period. Salinities in the reach increased steady from 4000 µScm-1 in autumn 2003 to 8500 µScm-1 in autumn 2009, declining briefly to pre-2004 concentrations (3940 µScm-1) in 2010 before increasing to 6820 µScm-1 in 2013. Across the habitat at this site, cover always remained moderate to high, but was influenced by declining water levels over 2008 and 2009.

Juvenile redfin that have prevailed in the reach

The disconnection from Lake Alexandrina and subsequent change in character influenced the species composition at lower Currency Creek (i.e. loss of freshwater wetland elements and addition of estuarine species) and appeared to force a shift in the demographic structure of diadromous species (no juveniles). Increased water availability in the region saw this reach reconnect with Lake Alexandrina and strong recruitment was observed in diadromous species but also alien species (namely redfin). This reach remains as an important lowland habitat and refuge but is clearly linked to connectivity with Lake Alexandrina.

State of fish communities across the EMLR, 2010 to 2013

20 2009, n=94 18 16 14 12 10 8

Frequency 6 4 2 0 0 50 100 150 200

20 2010, n=95 18 16 14 12 10 8

Frequency 6 4 2 0 0 50 100 150 200

20 2011, n=66 18 16 14 12 10 8

Frequency 6 4 2 0 0 50 100 150 200 20 2012, n=52 18 16 14 12 10 8

Frequency 6 4 2 0 0 50 100 150 200

20 2013, n=26 18 16 14 12 10 8

Frequency 6 4 2 0 0 50 100 150 200 Total length (mm)

Figure 3-27. Length-frequency distribution for common galaxias in Currency Creek (Lions Park and ds Goolwa Road), Currency Catchment (Reach 6) from 2009 to 2013 (graphs below the dotted line denote the current reporting period).

State of fish communities across the EMLR, 2010 to 2013

10 2009, n=7

Frequency

0 0 50 100 150 200 250 300 350

10 2010, n=95

Frequency

0 0 50 100 150 200 250 300 350

10 2011, n=20

Frequency 2

0 0 50 100 150 200 250 300 350 10 2012, n=38

Frequency

0 0 50 100 150 200 250 300 350

10 2013, n=32

4 Frequency 2

0 0 50 100 150 200 250 300 350 Total length (mm)

Figure 3-28. Length-frequency distribution for congolli in Currency Creek (Lions Park and ds Goolwa Road), Currency Catchment (Reach 6) from 2009 to 2013 (graphs below the dotted line denote the current reporting period).

State of fish communities across the EMLR, 2010 to 2013

Reach 7 – Terminal wetland

The extended Currency Creek arm of Lake Alexandrina stretches from just downstream of Goolwa Road to the Goolwa Channel near Laffin point. Baseline sampling in 2003 identified a diverse fish community including diadromous species, with the threatened Yarra pygmy perch and Murray hardyhead recorded in 2007 and 2008 respectively. As the prolonged drought intensified across the region, this reach underwent extensive drying (from summer 2007), with surface water mostly absent by autumn 2009. At Laffin point the fish community has changed markedly in recent years, shifting from a diverse freshwater community including threatened Yarra pygmy perch in 2003−2007, to a near estuarine community in autumn 2008, and to have no fish (dry) in autumn 2009. As water returned over 2010 and but in autumn 2011 unfavourable conditions still persisted (e.g. EC, 17700µScm-1) and freshwater generalists (flathead gudgeon and dwarf flathead gudgeon) and diadromous congollis were present. With sustainable inflows, the reach freshened (1419µScm-1) but the similar, generalist species prevailed. In subsequent years, an increasingly diverse fish community has returned (eight species in autumn 2012, 13 species in autumn 2013), yet freshwater generalists still dominate. Recently, Murray hardyhead were detected at several locations along the lower Currency Creek (Wedderburn 2014), but Yarra pygmy perch have not been sampled in the terminal wetland despite bi-annual monitoring since water returned (Bice et al. 2014).

Currency Creek junction (terminal wetland) in autumn 2009

State of fish communities across the EMLR, 2010 to 2013

Overall performance report

At the end of the 2009 reporting period, the condition of the Currency catchment in MODERATE condition with the mid pool-riffle reach (reach 5) was performing well but other reaches (e.g. terminal wetlands) were in poor condition (Figure 3-29). Over the present reporting period, increased water availability and connectivity has and some fish indicators have improved (e.g. terminal wetland now inundated and supports relatively diverse fish community) but others had not (e.g. reach 7) and the strong mountain galaxias population in reach 5 has declined (i.e. limited recruitment, considerable drop in numbers). Overall, the catchment was classified as being in MODERATE condition the end of the present reporting period (Table 3-9).

9 Reach types

8 Headwaters Upper 7 Mid

6 Gorge Lowland Wetlands 5 4

Condition score (out of 9) (out score Condition 1 0 2009 2010 2011 2012 2013 Year

Figure 3-29. Trend in condition score across reach types of the Currency Catchment between 2009 and 2013. Scores for each reach type reflect the median score for all ecological assets present in that reach type (reach types that were not sampled are not presented).

State of fish communities across the EMLR, 2010 to 2013

Table 3-9. 2013 report card for the Currency Catchment – a comparison of the performance against fish indicators (blacked out indicators are not relevant to that ecological asset). For each fish indicator, a tick ( ) represents a positive result (e.g. for present, a 2 & 3 for recruitment and survivorship indicators and a score > 4 for diverse fish community), and for all other results a cross ( ) shown. For alien species, ticks indicate the desirable result was observed (i.e. <30% of total site numbers) and crosses indicate a negative result (i.e. >30 of total site numbers). Condition scores for each ecological asset (out of 9) reflect the sum for each indicator (out of 7) plus an alien species score (out of 2). The median of scores for all ecological assets are used to estimate the overall catchment score. For ecological assets and overall catchment score are defined as good (>6, xxx), moderate (3 to 6, xxx) and poor (<3, xxx). See section 2.6 for full explanations. ASSESSMENT for 2013 INDICATOR

Relevant site

Condition

Alien species

Reach Reach score

Presence

Recruitment ECOLOGICAL ASSET Survivorship Reach 3 & 4 – Upper pool-riffle channel (north arm) Kilchoan Mountain galaxias 1 0 2 3 0 3.0 Reach 5 – Mid pool-riffle channel Stuarts Bridge Mountain galaxias 1 1 3 5 2 7.0 Reach 6 – Lowland channel Lions Park Diverse fish community 2 2 2 3.5 ds Goolwa Rd Diverse fish community 2 2 1 Reach 7 – Terminal wetland (junction) Yarra pygmy perch 0 0 0 0 Currency junction 2 3.5 Diverse fish community 3 3

Median 3.5

State of fish communities across the EMLR, 2010 to 2013

3.5 Finniss Catchment

In contrast to other EMLR catchments the Finniss is relatively well vegetated, with significant patches of remnant vegetation in the mid-section of the catchment. Nevertheless, agricultural pursuits are a common land use, with increased presence of horticulture in lower sections. Much of this large catchment (372km2) experiences medium to high rainfall and has steep topography through its middle section. The upper Finniss Catchment is a complex blend of tributaries, with the main arm an extension of the alluvial Meadows Creek which is then subsumed by the Finniss River and takes a sharp turn to the east through a constrained bedrock defined or loose rock dominated watercourse. A small swamp section originating from near Mt Compass (known today as Finniss Creek) also joins near Yundi. Major tributaries Bull Creek and Blackfellows Creek all join the main stem before Ashbourne. Downstream of Ashbourne is generally an intermittent reach through summer, except where a small region of base flow occurs just before a substantial waterfall. Below the waterfall, the stream is a lowland meander through to braided channel and into an extensive area of wetland that forms the upper section of an extended arm of Lake Alexandrina. Stream habitat in the Finniss Catchment is highly variable, with considerable heterogeneity at broad (i.e. geomorphic zones) and local scales with sites in close proximity often having contrasting habitat and hydrology – with corresponding fish capture patterns. Small to medium intermittent stream pools are the predominant habitat, with areas of peat swamp (e.g. Finniss Creek), rocky riffles (e.g. Finniss River above the waterfall) and long lowland pools and river channel (below the waterfall) also occurring. Occasional large and deep pools are located on the main stem of the Finniss River.

Nine provisional reaches have been defined in the Finniss River Catchment (Figure 3-30) with fish related assets, identified by Hammer (2004), including:  a genetically distinct population of southern pygmy perch in small patches of different stream reaches,  one of two populations of Yarra pygmy perch on the Murray-Darling Basin occurring in the Finniss terminal wetland (Reach 9),  mountain galaxias populations, which along with Tookayerta, represent a different species to other EMLR catchments (SA Museum unpublished), and diverse native fish communities in the lower Finniss and wetland (Table 3-10 and Table 3-13). A historical ecological asset (southern purple-spotted gudgeon) has been reintroduced into the catchment and short-term survival is evident (Bice et al. 2013). The environmental objectives associated with these ecological assets are also detailed in Table 3-13) and related to relevant EWR

State of fish communities across the EMLR, 2010 to 2013 tables of Section 2.5. Since 2001, long-term monitoring of most reaches in the catchment has occurred and 9−10 sites were sampled annually over the present (2009−2013) reporting period.

¯ Goolwa channel Figure 3-30. Map of the Finniss River Catchment. The main channels of the catchment (including terminal wetland) are marked as dark blue whereas smaller tributaries streams are marked light blue. The River Murray (Goolwa Channel) is denoted as grey.

State of fish communities across the EMLR, 2010 to 2013

Table 3-10. Distribution patterns and significant environmental assets in the Finniss Catchment relating to fish species and communities. Specific asset/pattern Location EWR Table Genetically distinct Finniss southern pygmy perch Reaches 4, 5, 6 and 7 Table 2-6, Table 2-9 & (fragmented populations) Table 2-12 Mountain galaxias (Finniss and Tookayerta catchments Reaches 2-8 have different species from rest of EMLR) Table 2-4 & Table 2-9 Mid Finniss diverse fish community Reaches 6 & 7 Table 2-9 Fleurieu Swamp fish community Reach 4 Table 2-12

Finniss River lowland stream and floodplain diverse fish Reach 8 community Table 2-8& Table 2-10 Finniss River terminal wetland diverse fish community Reach 9 including Yarra pygmy perch Presence of diadromous fish species in the Lower Finniss Reaches 7, 8 & 9 Table 2-8 River blackfish potentially present (historic records) Formerly Reaches 2, 3, 5, 6 Possibly Table 2-5 & 8 No permanent fish communities due to lack of Reach 1 NA permanent water

State of fish communities across the EMLR, 2010 to 2013

Table 3-11. Summary of environmental objectives by reach for fish related ecological assets in the Finniss River Catchment. Asset Environmental Objective Reach 1 – Finniss Catchment headwaters NA (possibly mountain galaxias) Reach 2 – Meadows Creek upper pool/riffle channel (Table 2-4) Mountain galaxias Maintain self-sustaining populations Reach 3 – Blackfellows Creek and Bull Creek upper pool/riffle channel (Table 2-5) Mountain galaxias Maintain self-sustaining populations (brown trout structuring populations) Reach 4 – Finniss Creek spring fed swamp section (Table 2-4, Table 2-6 & Table 2-12) Genetically distinct Finniss southern pygmy perch Maintain or restore restricted self-sustaining population population Mountain galaxias Maintain a self-sustaining population Reach 5 – Meadows Creek pool/riffle channel under spring influence (Table 2-4, Table 2-6, & Table 2-9) Genetically distinct Finniss southern pygmy perch Maintain restricted self-sustaining population population (population structured by trout and redfin) Mountain galaxias Maintain or restore a self-sustaining population Reach 6 – Heterogeneous mid-channel (Table 2-4, Table 2-6, Table 2-7 & Table 2-9) Diverse native fish community including threatened Maintain a self-sustaining populations of threatened southern pygmy perch and mountain galaxias, plus three species gudgeon species. Historically also included river Maintain diversity and composition of fish community blackfish. Reach 7 – Finniss pool/riffle channel under spring influence above waterfall (Table 2-4, Table 2-6, Table 2-9 & Table 2-11) Genetically distinct Finniss southern pygmy perch Maintain restricted self-sustaining population population Mountain galaxias Maintain a self-sustaining population Diadromous species (common galaxias and potentially Maintain restricted access of diadromous species lampreys – natural waterfall acts to limit access) Reach 8 – Lowland channel and floodplain (Table 2-4, Table 2-8 & Table 2-10, potentially Table 2-5 & Table 2-6) Diverse native fish community including mountain Maintain and restore diversity and composition of fish galaxias, diadromous species (common galaxias, congolli community and lampreys) and migratory species (Murray-Darling golden perch. Formerly (and potentially with further Maintain a self-sustaining population of mountain investigation) also southern purple-spotted gudgeon, galaxias (populations structured by natural competitors) southern pygmy perch, Murray rainbowfish, river blackfish, silver perch, Murray cod and freshwater catfish) Reach 9 – Terminal wetland under Lake Alexandrina influence (Table 2-11) Diverse native fish community including threatened Maintain and restore diversity, demographics and species (Yarra pygmy perch and southern pygmy perch) composition of fish community and diadromous and migratory species (as above). Historically community was richer including southern Maintain self-sustaining populations of threatened purples-spotted gudgeon, chanda perch, Murray pygmy perches hardyhead, freshwater catfish and Murray rainbowfish

State of fish communities across the EMLR, 2010 to 2013

Reaches 2 & 3 – Upper-pool riffle channels

This is a broad grouping of upper pool-riffle channel sections of the catchment, including upper Meadows Creek, Giles, Blackfellows and Bull creeks. Baseline data identified mountain galaxias as the main ecological asset in these areas (diadromous common galaxias also in Giles Creek). Annual monitoring has occurring in Bull Creek since 2004, and has shown high abundance and peaks that indicate strong recruitment and survivorship across all years (except perhaps autumn 2007) and including the present reporting period (Figure 3-31 and Figure 3-32). Conditions at the site have remained fairly consistent with cool flowing water and moderate levels of submerged physical and aquatic cover, although flow did decrease (down to a seep) and salinity did increase (up to 2970µScm- 1) at the height of the drought in 2008 and 2009. This site represents a key perennial refuge, which has been maintained through the dry climatic period experienced across the region.

Small refuge pool at McHarg Creek Road site on Bull Creek autumn 2013

State of fish communities across the EMLR, 2010 to 2013

15 14 2004 n=61 13 12 11 10 9 8 7 6 Frequency 5 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

15 14 2005, n=0 13 12 11 10 9 8 7 6

Frequency 5 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

15 14 2006, n=129 13 12 11 10 9 8 7 6

Frequency 5 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 15 14 2007, n=44 13 12 11 10 9 8 7 6

Frequency 5 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

15 14 2008, n=100 13 12 11 10 9 8 7 6

Frequency 5 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 Total length (mm)

Figure 3-31. Length-frequency distribution for mountain galaxias in Bull Creek (McHarg Creek Road), Finniss Catchment (Reach 3) between 2004 and 2008.

State of fish communities across the EMLR, 2010 to 2013

15 14 2009, n=114 13 12 11 10 9 8 7 6

Frequency 5 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

15 14 2010, n=150 13 12 11 10 9 8 7 6

Frequency 5 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

15 14 2011, n=76 13 12 11 10 9 8 7 6

Frequency 5 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 15 14 2012, n=62 13 12 11 10 9 8 7 6

Frequency 5 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

15 14 2013, n=88 13 12 11 10 9 8 7 6

Frequency 5 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 Total length (mm)

Figure 3-32. Length-frequency distribution for mountain galaxias in Bull Creek (McHarg Creek Road), Finniss Catchment (Reach 3) between 2009 and 2013 (graphs below the dotted line denote the current reporting period).

State of fish communities across the EMLR, 2010 to 2013

Reach 4 – Finniss Creek swamps

In 2004, a small population of southern pygmy perch was located in an in-stream dam in this swampy tributary to the Finniss River, however, no monitoring has occurred since.

Reach 5 – Meadows Creek

Lower Meadows Creek has a highly restricted population of threatened southern pygmy perch and mountain galaxias, under constant threat from large predatory introduced fishes – hence, site objectives relate to maintaining sustaining populations of natives and suppressing introduced species. Monitoring of the reach (at Thorn Dairy site) has occurred annually since 2001. The extent of surface water availability at the site decreased dramatically in autumn 2008 and 2009 with severe contraction to small pools. Autumn salinity was moderate with values ranging between 2000- 4000µScm-1 between 2001 and 2007, with higher readings in the last two autumns (up to 6840µScm- 1). With the end of the prolonged drought in 2010, surface water increased and conditions improved (EC, 2830µScm-1), however surface water has declined again in subsequent years.

Monitoring revealed mountain galaxias in only low abundance up until spring 2007, with a large increase in relative abundance, relating to successive strong recruitment events, observed in 2008 and 2009 (Figure 3-33). Abundance dropped over the present reporting period although recruitment was still evident, perhaps reflecting a large decline in population numbers (after autumn 2009) before the return of water. Since 2001, the southern pygmy perch has experienced fluctuating abundance; mostly low but with occasional higher catches (i.e. autumn 2004, 2009 and 2013) and comparatively high numbers over the present reporting period (Figure 3-34 and Figure 3-35). This translates to generally low recruitment with some better intermittent years, and ongoing low survivorship. Interestingly, a broad size class spread was observed in autumn 2013, possibly suggesting protracted or extended spawning and recruitment, an atypical feature more commonly observed in populations from the Tookayerta catchment. Adult introduced predatory brown trout and redfin have been sampled in low abundance from different pools since 2001 (normally one large predator in a pool). Low stream flow connectivity limiting colonisation, and poor conditions in concentrated pools during the prolonged drought (as well as localised predator removal effort) adversely impacted introduced predators, with no fish observed in spring 2008 and autumn 2009. Introduced predators have not recolonised the site (only one redfin in 2013) following increased surface flows. This may help to explain the increase in southern pygmy perch observed over the present reporting period.

State of fish communities across the EMLR, 2010 to 2013

Fish indicators for EWR assessment indicate an overall good condition of the site (as was the case in 2009), as a result of it enabling persistence of key ecological assets through time, especially in low flow periods and with the general absence of introduced predators. With the current apparent trend of declining surface water, it will be important to track the persistence of mountain galaxias and southern pygmy perch at this site in future annual sampling.

Meadows Creek – Thorn Dairy, autumn 2013

State of fish communities across the EMLR, 2010 to 2013

12 11 2009, n=53 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2010, n=5 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2011, n=13 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 12 11 2012, n=2 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2013, n=20 10 9 8 7 6 5 Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 Total length (mm)

Figure 3-33. Length-frequency distribution for mountain galaxias at Meadows Creek (Thorn Dairy), Finniss Catchment (Reach 5) from 2009 to 2013 (graphs below the dotted line denote the current reporting period).

State of fish communities across the EMLR, 2010 to 2013

20 2004 n=84 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2005 n=14 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2006 n=14 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 20 2007 n=3 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2008 n=17 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 Total length (mm)

Figure 3-34. Length-frequency distribution for southern pygmy perch at Meadows Creek (Thorn Dairy), Finniss Catchment (Reach 5) from 2004 to 2008.

100

State of fish communities across the EMLR, 2010 to 2013

20 2009 n=37 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2010, n=24 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2011, n=48 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 20 2012, n=29 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2013, n=99 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

Total length (mm)

Figure 3-35. Length-frequency distribution for southern pygmy perch at Meadows Creek (Thorn Dairy), Finniss Catchment (Reach 5) from 2009 to 2013 (graphs below the dotted line denote the current reporting period).

101

State of fish communities across the EMLR, 2010 to 2013

Reach 6 – Heterogeneous mid-pool channel

This reach is extensive and has strong site-based heterogeneity in the types of pools and geomorphology. There is widespread baseline sampling in the reach, with a site downstream of Coles Crossing having restricted populations of southern pygmy perch and mountain galaxias, which have been monitored since 2001. The core southern pygmy perch habitat consists of a series of smaller pools, representing a habitat type created and maintained by flow as a small refuge within larger pools that have introduced predatory fish (downstream is a large weir-pool created by an illegal in stream dam in 2003) (see Hammer 2005). The relative abundance and recruitment of southern pygmy perch was high between 2003 and 2005, but recruitment and survivorship has since been poor and few fish (<2 fish) have been recently recorded at the site (and no fish in autumn 2009 and 2012) (Figure 3-36 and Figure 3-37). Mountain galaxias are patchily distributed at the site (one core pool) and reasonable recruitment and survivorship was evident up until 2009, but a similar decline in abundance has been realised (Figure 3-38 and Figure 3-39). Introduced species have remained in low abundance in smaller pools (larger pools are not efficiently sampled for predatory species with backpack electrofishing), aside from a peak in juveniles observed in autumn 2009.

Environmental conditions remained relatively stable at the monitoring site between 2001 and 2009 (1500-2500µScm-1), but reduced water availability led to the concentration, then drying, of the core southern pygmy perch pool and several small pools in the reach had black water and low dissolved oxygen. This flow stress reduced the resilience of the southern pygmy perch and mountain galaxias populations in the reach by reducing heterogeneity in local habitat, causing the loss of key refuge habitat, and creating generally poor water quality in remaining pools. The fish EWR indicators are in extremely poor condition - as population recovery has been minimal - despite improved stream flow and connectivity experienced over recent years. Resident (and nearby) populations of introduced species may be influencing these patterns.

102

State of fish communities across the EMLR, 2010 to 2013

20 2004 n=94 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2005 n=86 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2006 n=19 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 20 2007 n=5 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2008 n=19 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 Total length (mm)

Figure 3-36. Length-frequency distribution for southern pygmy perch at Finniss River (ds Coles Crossing), Finniss Catchment (Reach 6) from 2004 to 2008.

103

State of fish communities across the EMLR, 2010 to 2013

20 2009 n=0 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2010, n=1 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2011, n=2 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 20 2012, n=0 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2013, n=1 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

Total length (mm)

Figure 3-37. Length-frequency distribution for southern pygmy perch at Finniss River (ds Coles Crossing), Finniss Catchment (Reach 6) from 2009 to 2013 (graphs below the dotted line denote the current reporting period).

104

State of fish communities across the EMLR, 2010 to 2013

12 11 2005, n=49 10 9 8 7 6 5 Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2006, n=0 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2007, n=0 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 12 11 2008, n=65 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

Total length (mm) Figure 3-38. Length-frequency distribution for mountain galaxias at Finniss River (ds Coles Crossing), Finniss Catchment (Reach 6) from 2005 to 2008.

105

State of fish communities across the EMLR, 2010 to 2013

12 11 2009, n=42 10 9 8 7 6 5 Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2010, n=22 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2011, n=0 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 12 11 2012, n=1 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2013, n=8 10 9 8 7 6 5 Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

Total length (mm)

Figure 3-39. Length-frequency distribution for mountain galaxias at Finniss River (ds Coles Crossing), Finniss Catchment (Reach 6) from 2009 to 2013 (graphs below the dotted line denote the current reporting period).

106

State of fish communities across the EMLR, 2010 to 2013

Reach 7 – Mid pool-riffle channel with spring influence

This stream reach represents a small section of the mid-channel under the influence of baseflow and situated above a waterfall. A localised diverse native fish community has been documented (and monitored since 2001) in shallow rocky pools including southern pygmy perch, mountain galaxias and occasional common galaxias. This reach has acted as a strong catchment refuge for a genetically distinct sub-population of southern pygmy perch, with high to very high relative abundance and strong recruitment recorded from 2001-2007 (Figure 3-40). Perennial baseflow has traditionally been recorded at the site, but stopped briefly in January 2008, before an extended period of cease-to-flow conditions in January and February 2009 in the peak of the drought. During this time extensive habitat drying and desiccation occurred, and remaining pools had poor water quality (e.g. low dissolved oxygen). Over this period, less recruits (i.e. 25-45mm) were noted (in autumn 2008), and in autumn 2009 only a single fish was recorded with population collapse evident (Figure 3-41). Whilst improved conditions were experienced from 2010 onwards, eight individuals were recorded in spring 2009, and only one individual was recorded in autumn 2010 (no fish in 2011, 2012). Encouragingly, however, the species was again observed, albeit in low numbers, in autumn 2013, indicating recolonisation of the site. It remains to be seen if the population is capable of naturally re-establishing to pre-2007 numbers. Over the present reporting period, mountain galaxias remained relatively abundant with regular recruitment (Figure 3-42). A diverse fish community has been maintained at the site over time (until autumn 2009, five native species; six native species in 2013), except at the end of the period of critical of water shortage (2009-2010). In 2013, a single juvenile climbing galaxias (89mm) was sampled, a species that is considered rare regionally (SA Action Plan) with no previously verified records after 1990 in the EMLR. The species is either diadromous or can complete their life cycle wholly in freshwater (e.g. Lower Lakes recruitment or marine dispersal) so it is unclear if this individual migrated upstream over the waterfalls or is a product of local recruitment.

The prolonged drought led to the loss of baseflow at this site caused catastrophic decline in habitat condition with a matching crash in southern pygmy perch and native fish diversity. As of 2009, one of the previously best performing sites in the EMLR declined within a very short time. Despite this past, documented rapid decline and the subsequent slow recovery of southern pygmy perch populations, as of 2013, this site is considered to be in good condition. Continued baseflow is the key attribute that underpins the ongoing recovery of the site.

107

State of fish communities across the EMLR, 2010 to 2013

Rapid pool drying following the cessation of baseflow (in autumn 2009, top) and restored water levels (in autumn 2013, bottom).

108

State of fish communities across the EMLR, 2010 to 2013

20 2004 n=53 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2005 n=118 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2006 n=53 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 20 2007 n=112 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 20 2008 n=48 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

Total length (mm)

Figure 3-40. Length-frequency distribution for southern pygmy perch at Finniss River (us Waterfalls), Finniss Catchment (Reach 7) from 2004 to 2008.

109

State of fish communities across the EMLR, 2010 to 2013

20 2009 n=1 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2010, n=1 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2011, n=0 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 20 2012, n=0 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2013, n=13 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

Total length (mm)

Figure 3-41. Length-frequency distribution for southern pygmy perch at Finniss River (us Waterfalls), Finniss Catchment (Reach 7) from 2009 to 2013 (graphs below the dotted line denote the current reporting period).

110

State of fish communities across the EMLR, 2010 to 2013

12 11 2009, n=15 10 9 8 7 6 5 Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2010, n=10 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2011, n=52 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 12 11 2012, n=10 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2013, n=52 10 9 8 7 6 5 Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

Total length (mm)

Figure 3-42. Length-frequency distribution for mountain galaxias at Finniss River (us Waterfalls), Finniss Catchment (Reach 7) from 2009 to 2013 (graphs below the dotted line denote the current reporting period).

111

State of fish communities across the EMLR, 2010 to 2013

Reach 8 – Lowland channel (with floodplain)

The section of lowland stream between the waterfalls and Winery Road is very heterogeneous, particularly the lower section which has floodplain and braided channel habitat. The reach supports a diverse native fish community including three diadromous species. Historically many other species were also recorded including river blackfish, Murray cod, southern purple-spotted gudgeon, and Yarra pygmy perch. Baseline sampling has been undertaken at several sites, with annual monitoring taking place at the railway bridge from 2009 onwards. The diversity of native fish at this site remained similar between 2004 and 2009, however the 2009 total (n=6) excluded the previously recorded mountain galaxias which was collected from riffles interconnecting pools in 2004 (two hybrid Philypnodon were recorded in 2009 only). The relative abundance of native fish remained relatively constant, but with the reduction in surface water and habitat towards the end of the prolonged drought (2009), numbers dropped considerably. This was particularly the case for common galaxias, with the relative length-frequency data suggesting that a lack of recruitment may be contributing to this decline, as all common galaxias captured were large adults >100mm (not shown). Likewise, no juvenile congolli were captured, with the few fish captured all being >170mm and in 2010, only congolli >250mm were observed (Figure 3-43). Following the return of stream flow and improved connectivity, however, there was an influx of juvenile congollis (50−130mm), which would have migrated upstream from the estuary environment. Since this time, the gradual aging of the population, with only low numbers of juveniles observed, has been evident. The type and relative abundance of alien species was similar between 2004 and 201, including redfin in low abundance.

The site maintains high levels of heterogeneity, including a mosaic of small and large pools and interconnecting shallow riffles, even during dry periods due to local spring flows. Across the monitoring range (2004 to 2013), low-moderate salinity (i.e. 2000−3000µScm-1) and moderate underwater cover were recorded, although edge vegetation had declined owing to heavy stock access (note fencing had been erected shortly before sampling). The diversity of aquatic plants is an important feature of the site (e.g. patches of Vallisneria and an array of amphibious species), and more intensive sampling identified patches of Ottelia, Myriophyllum and Ceratophyllum; all species that are rare or not seen elsewhere in EMLR streams, and have declined broadly from the region following desiccation of fringing habitats around the Lower Lakes.

112

State of fish communities across the EMLR, 2010 to 2013

Large refuge pool at the railway bridge, autumn 2013

Another site downstream (Lovejoy) has maintained similar habitat quality and has been deemed suitable for the reintroduction of southern purple-spotted gudgeon. Across four rounds of reintroduction (2011−2013), over 1000 fish were released with a handful of recaptures, indicating short-term survival (Bice et al. 2013).

Vegetated stream habitat where southern purple-spotted gudgeon have been released (as of autumn 2013)

113

State of fish communities across the EMLR, 2010 to 2013

During the period of critical water shortage across the region, the reach performed comparatively well with the maintenance the diversity of the fish community, save for the loss of the freshwater specialist, mountain galaxias. Diadromous species were vulnerable over this period, but have responded positively to improved stream flow and connectivity in recent years. Furthermore, southern purple-spotted gudgeon have been re-established into the reach and initial signs are positive. Overall, this reach represents a core tributary refuge upstream of the influence of Lake Alexandrina, which is a priority to be maintained and, if possible, improved over coming years.

114

State of fish communities across the EMLR, 2010 to 2013

10 2009, n=8

Frequency

0 0 50 100 150 200 250 300 350

10 2010, n=5

Frequency

0 0 50 100 150 200 250 300 350

10 2011, n=14 8

Frequency 2

0 0 50 100 150 200 250 300 350 10 2012, n=19

Frequency

0 0 50 100 150 200 250 300 350

10 2013, n=22

4 Frequency 2

0 0 50 100 150 200 250 300 350 Total length (mm)

Figure 3-43. Length-frequency distribution for congolli at Finniss River (Railway Bridge), Finniss Catchment (Reach 8) from 2009 to 2013 (graphs below the dotted line denote the current reporting period).

115

State of fish communities across the EMLR, 2010 to 2013

Reach 9 – Terminal wetland

The Finniss terminal wetland contains key habitats including (1) pool transition between the Finniss and Lake Alexandrina just below Winery Road, (2) a series of off channel wetlands including Blue Lagoon, (3) a deep river channel with dense fringing vegetation, and locations with dense submerged aquatic vegetation (mainly Ceratophyllum), and (4) junction point where the a deep channel opens out into Lake Alexandrina joining the Tookayerta (Black Swamp). These habitats collectively have recorded a high diversity of fishes including three threatened species in recent years (i.e. Yarra pygmy perch, southern pygmy perch and Murray hardyhead), and a range of other species historically. Data is mostly opportunistic for this reach aside from 2004 baseline sampling (Hammer 2001; Hammer 2004; Wedderburn and Hammer 2003), as part of intensive efforts to locate Yarra pygmy perch as Lake Levels lowered after summer 2007 and again during subsequent assessment of potential reintroduction sites for the species. Monitoring of two sites just downstream of Winery Road were initiated in 2007. The Black Swamp area is covered under Tookayerta terminal wetland.

The diversity of fishes in the reach declined considerably as extensive drying and isolation of habitat occurred during low Lake Alexandrina levels. At Blue Lagoon, Yarra pygmy perch were initially recorded in dense Ceratophyllum and Myriophyllum, however the species declined with the gradual loss of this habitat, with no fish seen since spring 2004 and complete drying occurring by spring 2008. Despite the inundation of the site in 2010 and fish reintroductions, no Yarra pygmy perch have been observed; perhaps reflecting the subdued recovery of aquatic vegetation (e.g. Myriophyllum). Monitoring of other previous Yarra pygmy perch sites at and just downstream of Wallys Wharf have not recorded the species following its drying during 2009. A relatively stable fish community was observed at sites immediately downstream of Winery Road, with the community relatively stable and diverse (nine species, including Murray hardyhead) over 2008 and 2009 monitoring. These sites were somewhat buffered from decline in water availability and habitat experienced across this region due to a small disconnection point that prevents complete exposure to regional water levels; instead they are maintained mostly by Finniss flows. As such, the fish community was largely preserved during the prolonged drought, although Murray hardyhead have not been observed in recent years. Alien species have been present in low to moderate relative abundance across the reach.

116

State of fish communities across the EMLR, 2010 to 2013

Finniss River – 500m ds Winery Road, autumn 2013

As for other EMLR terminal wetlands the condition of the lower sections of this reach suffered drastically during the period of low flows and has not yet recovered, but sites further upstream were fairly well maintained and continue to support diverse fish communities.

Overall performance report

At the end of the 2009 reporting period, some upper catchment areas performed well, but the mid and lower catchment were in decline, and overall catchment condition was MODERATE (Figure 3- 44). Over the present reporting period, mountain galaxias and southern pygmy perch populations mostly maintained across the catchment. Whilst improved water availability and connectivity saw positive responses in fish communities in the lower reaches, although Yarra pygmy perch remain absent (despite reintroductions: Bice et al. 2014) Overall, the catchment classified as being in MODERATE condition the end of the present reporting period (Table 3-12).

117

State of fish communities across the EMLR, 2010 to 2013

9 Reach types

8 Headwaters Upper 7 Mid 6 Gorge Lowland 5 Wetlands

4 3

Condition score (out of 9) (out score Condition 1 0 2009 2010 2011 2012 2013 Year

Figure 3-44. Trend in condition score across reach types of the Finniss Catchment between 2009 and 2013. Scores for each reach type reflect the median score for all ecological assets present in that reach type (reach types that were not sampled are not presented).

118

State of fish communities across the EMLR, 2010 to 2013

Table 3-12. 2013 report card for the Finniss Catchment – a comparison of the performance against fish indicators (blacked out indicators are not relevant to that ecological asset). For each fish indicator, a tick ( ) represents a positive result (e.g. for present, a 2 & 3 for recruitment and survivorship indicators and a score > 4 for diverse fish community), and for all other results a cross ( ) shown. For alien species, ticks indicate the desirable result was observed (i.e. <30% of total site numbers) and crosses indicate a negative result (i.e. >30 of total site numbers). Condition scores for each ecological asset (out of 9) reflect the sum for each indicator (out of 7) plus an alien species score (out of 2). The median of scores for all ecological assets are used to estimate the overall catchment score. For ecological assets and overall catchment score are defined as good (>6, xxx), moderate (3 to 6, xxx) and poor (<3, xxx). See section 2.6 for full explanations. ASSESSMENT for 2013 INDICATOR

Relevant site

Condition Alien species Reach score ECOLOGICAL ASSET Presence Recruitment Survivorship Reach 2 & 3 – Upper pool-riffle tributary creeks McHarg Creek Rd Mountain galaxias 1 3 3 7 2 9.0 Reach 5 – Meadows Creek upper pool-riffle channel under spring influence Southern pygmy perch 1 3 3 7 Thorn Dairy 2 8.0 Mountain galaxias 1 3 1 5 Reach 6 – Heterogeneous mid pool-riffle channel Southern pygmy perch 1 0 0 1 ds Coles Crossing 0 2.5 Mountain galaxias 1 1 2 4 Reach 7 – Mid pool-riffle channel under spring influence (above waterfalls) Southern pygmy perch 1 0 0 1 us Waterfalls Mountain galaxias 1 3 3 7 2 5.0 Diverse fish community 3 3 Reach 8 – Lowland channel and floodplain Railway Bridge Diverse fish community 1 1 0 1.0 Reach 9 – Terminal wetland under Lake Alexandrina influence 300m ds Winery Rd Diverse fish community 2 2 2 500m ds Winery Rd Diverse fish community 2 2 2 3.0 Yarra pygmy perch 0 0 0 0 Blue Lagoon 0 Diverse fish community 2 2

Median 4.0

119

State of fish communities across the EMLR, 2010 to 2013

3.6 Inman Catchment

The Inman River Catchment is not within the defined EMLR region as it occurs outside the geopolitical boundaries of the Murray-Darling Basin (i.e. in the SA Gulf Drainage Division and AMLR NRM region). However, as it has faunal similarities with the MDB (shared obligate freshwater fish species implying historic connectivity with the Murray: Hammer 2001) and has been included in recent monitoring of other EMLR species (southern pygmy perch: Hammer 2005). A brief review is included as data may assist interpretations in the EMLR and contribute to local EWR processes in the Inman Catchment.

The Inman catchment is situated on the southern Fleurieu Peninsula discharging into the Southern Ocean at Victor Harbor. The catchment is complex having a combination of tributaries arising in, and flowing through, contrasting elevations and geological formations (and hence are also hydrologically diverse). For example, the Back Valley Creek comprises extensive glacial sands and swampy creek sections, whereas the Boundy Creek in the upper catchment is a perennial flowing stream originating from upland headwaters. Remnant vegetation is reasonable but patchy with extensive grazing and irrigation in the catchment.

Overall, seven provisional reaches have been defined in the Inman River Catchment (Only broad baseline sampling has occurred across these reaches with detail on ecological assets still requiring further investigation (Hammer 2006a) (Figure 3-45). Nevertheless fish related assets identified to date (Hammer 2001; Hammer 2006a) are shown in Table 3-13 and Table 3-14. These include genetically distinct sub-populations of southern pygmy perch, Murray-Darling carp gudgeon and diadromous species (climbing galaxias and common galaxias). There are historical reports of mountain galaxias, and further sampling is required to assess this species’ status.

Opportunistic sampling has occurred throughout the catchment, but long-term monitoring (since 2001) has focused on Back Valley Creek (reach 4) with three sites sampled annually over the present reporting period (2010−2013).

120

State of fish communities across the EMLR, 2010 to 2013

0 1.25 2.5 5 ¯ Kilometers

Figure 3-45. Map of the Inman River Catchment. The main channels of the catchment are marked as dark blue whereas smaller tributaries streams are marked light blue. The Southern Ocean is denoted as grey.

Table 3-13. Initial information on distribution patterns and significant environmental assets in the Inman River Catchment relating to fish species and communities. Specific asset/pattern Location EWR Table Southern pygmy perch Reaches 3 & 4 Table 2-4, Table 2-9 and Table 2-12 Murray-Darling carp gudgeon Reaches 4, 5 & 6 Table 2-7 & Table 2-10 Mountain galaxias and river blackfish potentially could Reaches 3, 5 & 6 Possibly Table 2-4 & Table occur 2-5 Lower Inman diverse fish community Reaches 6 Table 2-10

Presence of diadromous fish species Reaches 2-7 Table 2-8 No permanent fish communities due to lack of Reach 1 NA (possibly Table 2-4, permanent water (populations may occur in perched Table 2-6 & Table 2-12) Fleurieu swamps)

121

State of fish communities across the EMLR, 2010 to 2013

Table 3-14. Summary of environmental objectives by reach for fish related ecological assets in the Inman River Catchment. Asset Environmental Objective Reach 1 – Inman Catchment headwaters NA Reach 2 – Upper Back Valley Creek and Hall Creek Pool/riffle channel (Table 2-8, possibly Table 2-4) Freshwater and diadromous galaxias previously known Restore self-sustaining populations Reach 3 – Upland pool/riffle channel under spring influence (Table 2-6, Table 2-8& Table 2-9) Inman genetic sub-population of southern pygmy perch Maintain or restore self-sustaining population Climbing galaxias (diadromous) Maintain or restore self-sustaining population Reach 4 – Back Valley Creek swampy pool channel (Table 2-6) Inman genetic sub-population of southern pygmy perch Maintain or restore self-sustaining population Climbing galaxias Maintain or restore self-sustaining population Mountain galaxias possibly occurs Maintain or restore self-sustaining population Reach 5 – Mid-catchment pool/riffle channel meander (Table 2-4 & Table 2-7, possibly Table 2-5) Murray-Darling carp gudgeon Maintain or restore self-sustaining population Climbing galaxias and common galaxias (possibly Maintain community of diadromous species lampreys) River blackfish may occur Maintain or restore self-sustaining population Reach 6 – Large pool/riffle channel above estuary (Table 2-7, Table 2-8 & Table 2-10, possibly Table 2-5) Diverse fish community including Murray-Darling Maintain and restore diversity, demographics and gudgeon, estuarine species (western bluespot goby) and composition of fish community diadromous species (common and climbing galaxias) River blackfish possibly occurs Maintain or restore self-sustaining population Reach 7 – Terminal wetland (estuary) (Table 2-8 & Table 2-10) Little known, highly polluted. At least a pathway for the Maintain and restore diversity and composition of fish access of diadromous species, but potentially habitat for community estuarine species. Maintain access for diadromous species

122

State of fish communities across the EMLR, 2010 to 2013

Reach 4 – Back Valley Creek

The monitoring targets in Back Valley Creek are southern pygmy perch and diadromous species (namely common galaxias). Three sites are monitored, two in the upper sub-catchment (Kirk Road and Kirk property since 2001) and one in the mid sub-catchment (Robertson property since 2008).

Small refuge pool on Back Valley Creek - Kirk property, autumn 2013

Southern pygmy perch persisted at the two upper sub-catchment sites between 2001 and 2009. The Kirk property has a string of shallower pools, so assessment here tests general resilience, while Kirk Road is a deep pool and so the condition of a key refuge is monitored here. At the Kirk property strong recruitment was noted in 2004, but subsequent declines to very low numbers occurred through to 2007 (few pools, no recruitment) (Figure 3-46 and Figure 3-47). In autumn 2008 and 2009, some recovery in recruitment and distribution was evident. Over the present reporting, however, abundance has again declined with less than two fish recorded annually in 2011 to 2013. A similar pattern of recovery was noted at Kirk Road with very strong recruitment and abundance noted in autumn 2009 before rapid declines over 2010 to 2013 (Figure 3-48 and Figure 3-49). At the Robertson property, strong recruitment was detected in autumn 2008, with both strong recruitment and survivorship (population recovery) occurring in autumn 2009 (Figure 3-50). Unlike the other two sites, strong and ongoing recruitment continued at the Robertson property site over the present reporting period and good numbers remain. Introduced species remain absent from this reach, despite historic

123

State of fish communities across the EMLR, 2010 to 2013 reports of redfin in the stream including at Kirk Road, and presence of both redfin and Gambusia in connected sections of the Inman River. Diadromous species are also absent, reflecting impeded connectivity through the catchment.

Environmental data is variable across sites and years, with a common factor being low transparency, humic-stained, water. At the Kirk property, autumn salinity has fluctuated between 613-5870µScm- 1, and cover values have been low to moderate, especially with pool contraction over the period of critical water shortage. Conditions at Kirk Road have been more consistent (1250-3420µScm-1, moderate cover), but with low dissolved oxygen (as low as 1.3mgL-1 in autumn 2013) in recent assessments. Robertson property maintains high habitat cover, moderate to high salinity (~3000- 5300µScm-1) and low dissolved oxygen (as low as 0.9mgL-1 in autumn 2013).

The Inman sub-catchment retains important ecological assets but environmental conditions (e.g. reduced flow, increasing salinity and declining oxygen over summer/autumn) have deteriorated to the point that populations of southern pygmy perch at two of the monitoring sites are on the brink of localised extinction. Similar conditions at the third site have yet to adversely impact population numbers but declines can be expected in the coming years. The lack of water and connectivity ensures that the diadromous species has not been met although the absence of introduced species is positive.

The present stronghold site on Back Valley Creek – Robertson property, autumn 2013

124

State of fish communities across the EMLR, 2010 to 2013

20 2004, n=75 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2005, n=41 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2006, n=21 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 20 2007, n=2 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2008 n=32 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 Total length (mm)

Figure 3-46. Length-frequency distribution for southern pygmy perch in Back Valley Creek (Kirk Property), Inman Catchment (Reach 4) from 2004 to 2009.

125

State of fish communities across the EMLR, 2010 to 2013

20 2009 n=23 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2010, n=10 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2011, n=2 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 20 2012, n=0 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2013, n=2 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

Total length (mm)

Figure 3-47. Length-frequency distribution for southern pygmy perch in Back Valley Creek (Kirk Property), Inman Catchment (Reach 4) from 2009 to 2013 (graphs below the dotted line denote the current reporting period).

126

State of fish communities across the EMLR, 2010 to 2013

20 2004, n=7 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2005, n=11 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2006, n=114 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 20 2007, n=15 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2008 n=33 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 Total length (mm)

Figure 3-48. Length-frequency distribution for southern pygmy perch in Back Valley Creek (Kirk Road), Inman Catchment (Reach 4) from 2004 to 2008.

127

State of fish communities across the EMLR, 2010 to 2013

20 2009 n=101 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2010, n=19 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2011, n=10 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 20 2012, n=1 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2013, n=0 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 Total length (mm)

Figure 3-49. Length-frequency distribution for southern pygmy perch in Back Valley Creek (Kirk Road), Inman Catchment (Reach 4) from 2009 to 2013 (graphs below the dotted line denote the current reporting period).

128

State of fish communities across the EMLR, 2010 to 2013

20 2009 n=80 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2010, n=125 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2011, n=47 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 20 2012, n=25 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2013, n=100 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 Total length (mm)

Figure 3-50. Length-frequency distribution for southern pygmy perch in Back Valley Creek (Robertson property), Inman Catchment (Reach 4) from 2009 to 2013 (graphs below the dotted line denote the current reporting period).

129

State of fish communities across the EMLR, 2010 to 2013

Overall performance report

In 2009, the Inman catchment - based on information from one reach (the Back Valley Creek reach) – was deemed to be in MODERATE condition (Figure 3-51). Assessment of the present reporting period revealed sharp declines in the condition of two fish indicators, and no diadromous species were detected across the reach. Encouragingly, one site in the reach continues to maintain a self- sustaining population of southern pygmy perch. Overall, the catchment has declined but was still considered to be in MODERATE condition the end of the present reporting period (Table 3-15). Again, broader assessment of the Inman Catchment was not possible given the ongoing deficiency of sampling.

Table 3-15. 2013 report card for the Inman Catchment – a comparison of the performance against fish indicators (blacked out indicators are not relevant to that ecological asset). For each fish indicator, a tick ( ) represents a positive result (e.g. for presence, a 2 & 3 for recruitment and survivorship indicators and a score > 4 for diverse fish community), and for all other results a cross ( ) shown. For alien species, ticks indicate the desirable result was observed (i.e. <30% of total site numbers) and crosses indicate a negative result (i.e. >30 of total site numbers). Condition scores for each ecological asset (out of 9) reflect the sum for each indicator (out of 7) plus an alien species score (out of 2). The median of scores for all ecological assets are used to estimate the overall catchment score. For ecological assets and overall catchment score are defined as good (>6, xxx), moderate (3 to 6, xxx) and poor (<3, xxx). See section 2.6 for full explanations. ASSESSMENT for 2013 INDICATOR

Relevant site

Condition Alien species Reach Reach score

Presence Recruitment ECOLOGICAL ASSET Survivorship Reach 4 – Back Valley Creek Kirk Property Southern pygmy perch 1 0 0 1 2 Kirk Rd Southern pygmy perch 0 0 0 0 2 3.5 Robertson Property Southern pygmy perch 1 3 3 7 2 Combined (3 sites) Diverse fish community 2 2 2

Median 3.5

130

State of fish communities across the EMLR, 2010 to 2013

9 Reach types

8 Headwaters Upper

7 Mid Gorge 6 Lowland 5 Wetlands

4 3

Condition score (out of 9) (out score Condition 1 0 2009 2010 2011 2012 2013 Year

Figure 3-51. Trend in condition score across reach types of the Inman Catchment between 2009 and 2013. Scores for each reach type reflect the median score for all ecological assets present in that reach type (reach types that were not sampled are not presented).

131

State of fish communities across the EMLR, 2010 to 2013

3.7 Marne Catchment

The Marne River Catchment covers ~500km2 being a direct tributary to the River Murray, situated north east of Adelaide. Its headwaters originate in higher rainfall areas east of the apex of the Mount Lofty Ranges, with a catchment area spreading between Springton, Eden Valley and Keyneton, north east of Adelaide. The upland catchment area or “Hills Zone” spills through a confined gorge before exiting onto the “Plains Zone”. The lower zone contains an ephemeral river red gum Eucalyptus camaldulensis lined channel through much drier lowland areas until it reaches the township of Black Hill. The stretch following here forms a unique ecological scenario for the EMLR, with harsh Mallee terrain sliced by a lush valley supported by a spring fed stream. Historically this stream stretch was continuous through to a deep clear wetland at the Marne Mouth near Wongulla (around 20km upstream of Mannum) before flowing into the River Murray. Surface water connection between the upper and lower sections is only facilitated by flows and flood spates with sufficient magnitude to traverse the ephemeral channel. Both Marne River flows and River Murray flooding can inundate the Marne Mouth wetland.

Overall nine distinct river reaches can be defined in the catchment based on distinction in geomorphic character (MREFTP 2003; Figure 3-52), and these form the spatial basis of setting and measuring environmental flow related objectives. Fish related ecological assets identified by Hammer (2002) and summarised in MREFTP (2003) include Mountain galaxias populations, a highly significant population of river blackish and other native fish communities (Table 3-16). The environmental objectives associated with these ecological assets are also detailed in Table 3-17.

Over the present reporting period (2010−2013), five sites within four distinct river reaches have been sampled annually and the Marne Mouth was sampled in 2012.

132

State of fish communities across the EMLR, 2010 to 2013

0 2.5 5 10 Kilometers River Murray Figure 3-52. Map of the Marne River Catchment. The main channels of the catchment (including terminal wetland) are marked as dark blue whereas smaller tributaries streams are marked light blue. The River Murray is denoted as grey.

Table 3-16. Distribution patterns and significant environmental assets in the Marne River Catchment relating to fish species and communities (adapted from MREFTP 2003). Specific asset/pattern Location EWR Table Mountain galaxias Reaches 2, 5 Table 2-4 River blackfish (local extinctions due to some springs drying Reach 8 Table 2-5 & Table 2-9 out) Lower Marne diverse fish community Reach 8 Table 2-9 Lower Marne/Murray backwater diverse fish community Reach 9 Table 2-11 Potential for diadromous fish species (congolli, common Reach 9 Table 2-8 & Table 2-11 galaxias, lamprey) to colonise lower Marne River No permanent populations present due to lack of summer Reach 4 Table 2-4 refuge, connectivity and water quality (but mountain galaxias occurs intermittently) No permanent fish communities due to lack of Reach 6 NA permanent water. Mountain galaxias may be opportunistically present washed in from upstream, but unlikely to be sustainable Little aquatic habitat present. Unlikely to ever have Reaches 1, 3, 7 NA sustainable populations

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State of fish communities across the EMLR, 2010 to 2013

Table 3-17. Summary of environmental objectives by reach for fish related ecological assets in the Marne Catchment (Hammer 2006c). Asset Environmental Objective Reach 1, 3, 6, 7 – Marne & North Rhine headwaters, Alluvial Fan & Floodplain from Cambrai to Black Hill NA Reach 2 – Upper Marne pool/riffle channel (EWR Table 2-4) Mountain galaxias Maintain or Restore a self-sustaining population Reach 4 – North Rhine main channel (EWR Table 2-4) Mountain galaxias (longer term objective) Restore self-sustaining population Reach 5 – Marne Gorge (EWR Table 2-4) Mountain galaxias Maintain or Restore a self-sustaining population Reach 8 – Lower Marne under spring influence (EWR Table 2-5, Table 2-7 and Table 2-9) Maintain a self-sustaining population. River blackfish Restore a self-sustaining population (to springs in Reach that have dried out) Maintain diversity, demographics and composition of fish Lower Marne fish community community Reach 9 – Marne under Murray influence (EWR Table 2-8 and Table 2-11) Lower Marne/Murray backwater fish community Maintain diversity and composition of fish community Rare/endangered chanda perch and diadromous congolli Restore community of diadromous/rare species and Common galaxias were historically recorded)

134

State of fish communities across the EMLR, 2010 to 2013

Reach 2 – Upper Marne River

Two sites are sampled for mountain galaxias in this reach, one in the upper reach (Vigars Rd) and one in the lower reach (Jutland Rd). Previous monitoring has highlighted the strong link between mountain galaxias populations and water availability at these two sites (Figure 5-2 and 5-3). In 2006, for instance, greater water availability resulted in increased abundance and strong recruitment (Hammer 2007a). However, reduced water availability in the subsequent three-years (2007-2009) lead to dramatic declines to zero in these populations, which tested the resilience of mountain galaxias in this reach (and catchment) (Hammer 2009).

Increased water availability over the present study period (2010-2013) has seen recolonisation of both sites and gradual increases in population numbers (Figure 3-56). At Vigars Road, there were only four fish in autumn 2010, none in autumn 2011, but then 11 fish in 2012 and most recently a large population increase to 109 fish (2013) was realised. Similarly at Jutland Road, initial numbers were low (3 fish, 2010; 4 fish, 2011) before increasing in 2012 (32 fish), but slight decline in 2013 (16 fish). In both the peak years at each site, there was strong recruitment (0+ fish between 40-65mm) and survivorship. Yet, despite these improvements, declining trends in water availability (At Vigars Road, 1m in 2010 to 0.6m in 2013) and water quality (At Vigars Road, EC 2320µScm-1 in 2010 to 6130µScm- 1 in 2013) between 2010 and 2013, once again raises concern over the ongoing resilience of these important populations.

135

State of fish communities across the EMLR, 2010 to 2013

12 11 2004, n=53 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2005, n=114 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2006, n=52 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2007, n=13 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 12 11 2008, n=0 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

Total length (mm)

Figure 3-53. Length-frequency distribution for mountain galaxias at Vigars Road, Marne Catchment (Upper Reach 2) from 2004 to 2008 (graphs below the dotted line denote the current reporting period).

136

State of fish communities across the EMLR, 2010 to 2013

12 11 2009, n=0 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2010, n=4 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2011, n=0 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 12 11 2012, n=11 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2013, n=109 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 Total length (mm)

Figure 3-54. Length-frequency distribution for mountain galaxias at Vigars Road, Marne Catchment (Upper Reach 2) from 2009 to 2013 (graphs below the dotted line denote the current reporting period).

137

State of fish communities across the EMLR, 2010 to 2013

12 11 2004, n=53 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2005, n=114 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2006, n=52 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 12 11 2007, n=13 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2008, n=0 10 9 8 7 6 5 Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

Total length (mm)

Figure 3-55. Length-frequency distribution for mountain galaxias at Jutland Road, Marne Catchment (Upper Reach 2) from 2004 to 2008.

138

State of fish communities across the EMLR, 2010 to 2013

12 11 2009, n=0 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2010, n=3 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2011, n=4 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 12 11 2012, n=32 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2013, n=16 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 Total length (mm) Total length (mm)

Figure 3-56. Length-frequency distribution for mountain galaxias at Jutland Road, Marne Catchment (Upper Reach 2) from 2009 to 2013 (graphs below the dotted line denote the current reporting period).

139

State of fish communities across the EMLR, 2010 to 2013

Reach 4 – North Rhine River

Recolonisation of adult mountain galaxias was recorded in this reach in autumn 2006 after extended seasonal flow conditions and/or a high flow event in November 2005. Monitoring on five occasions between 2006 and 2009, however, failed to detect the species, not surprising, given the major decline in water availability (e.g. in autumn 2009 only a small pool with depth 0.3m remained and had a salinity of >10,000µScm-1) experienced over this period. Despite improved water availability and habitat condition since 2010, the species has not recolonised and remains absent from the site.

North Rhine River - Pine Hutt Road, autumn 2013

Reach 5 – Marne Gorge

The Marne Gorge site represents a key measure of mountain galaxias population resilience in the upstream catchment (relies on flows and fish from upstream). It is evident that the species experiences local extinction followed by subsequent recolonisation events during favourable conditions. For instance, a pulse of juvenile fish (0+) and potentially some 1+ adult fish were recorded in autumn 2008, yet a year later (autumn 2009) conditions for survival were poor (e.g. heavily concentrated shallow pool with salinity >25,000µScm-1) and local extinction was again evident (Figure 5-6 and 5-7). Over the present reporting period (2010-2013), the population did not exhibit the characteristic boom and bust in numbers, but rather local extinctions in 2011 and most recently in 2013 where interspersed with small peaks in numbers (2010, 7 fish; 2012, 2 fish), perhaps indicating

140

State of fish communities across the EMLR, 2010 to 2013 a period of sustained decline in upstream population resilience (Figure 3-58).

Marne River – Marne Gorge, autumn 2013

141

State of fish communities across the EMLR, 2010 to 2013

12 11 2004, n=0 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2005, n=44 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2006, n=38 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 12 11 2007, n=0 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2008, n=23 10 9 8 7 6 5 Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 Total length (mm)

Figure 3-57. Length-frequency distribution for mountain galaxias at Marne Gorge, Marne Catchment (Upper Reach 2) from 2004 to 2008.

142

State of fish communities across the EMLR, 2010 to 2013

12 11 2009, n=0 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2010, n=7 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2011, n=0 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 12 11 2012, n=2 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2013, n=0 10 9 8 7 6 5 Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

Total length (mm)

Figure 3-58. Length-frequency distribution for mountain galaxias at Marne Gorge, Marne Catchment (Upper Reach 2) from 2009 to 2013 (graphs below the dotted line denote the current reporting period).

143

State of fish communities across the EMLR, 2010 to 2013

Reach 8 – Lower Marne

Ecological assets of the Lower Marne relate primarily to one river blackfish population (at Black Hill Springs), as well as the general condition of a diverse groundwater dependent fish community. It is clear that the river blackfish population is in decline with no recruitment and presence of large aging individuals (>200mm TL) observed over 2002-2009 (Figure 3-59) (Hammer 2009). Over the present report period (2009-2013), the declining trend in the river blackfish population continued, with few larger fish (<4 fish) observed up to 2012 and no fish sampled in 2013 (although one large individual was visually observed) (Figure 3-60). At this site, the river ceased to flow in January 2012 highlighting the threat posed to the species. This river blackfish population has not recruited since 2002 and is undoubtedly on the brink of localised extinction. Intervention measures, suggested in 2009, remain necessary (but logistically difficult) to secure the population (e.g. wild egg harvest for rearing if this occurs, fish rescue and captive breeding) and there is an urgent need to address the reduction in stream flow and subsequent poor water quality in the lower half of pools.

Marne River – Black Hill Springs, autumn 2013

The presence of other native fish has been confirmed in the present reporting period (2010−2013) with low numbers of carp gudgeon and dwarf flathead gudgeon. Yet, mountain galaxias were not detected over the present reporting period (only large adults (>100mm) were observed from 2007−2009) as was the case with flathead gudgeon.

144

State of fish communities across the EMLR, 2010 to 2013

5 2004, n=7

Frequency

0 0 50 100 150 200 250 300

5 2005, n=10

Frequency 1

0 0 50 100 150 200 250 300 5 2006, n=3

2 Frequency 1

0 0 50 100 150 200 250 300

5 2007 n=0 4

3 No sampling (visual observations only) 2

Frequency

0 0 50 100 150 200 250 300

5 2008, n=5

Frequency

0 0 50 100 150 200 250 300 Total length (mm)

Figure 3-59. Length-frequency distribution for River blackfish at Black Hill Springs, Marne Catchment (Reach 8) from 2004 to 2008.

145

State of fish communities across the EMLR, 2010 to 2013

5 2009, n=1

Frequency

0 0 50 100 150 200 250 300

5 2010, n=4

Frequency

0 0 50 100 150 200 250 300

5 2011, n=1 4

Frequency 1

0 0 50 100 150 200 250 300 5 2012, n=1

Frequency

0 0 50 100 150 200 250 300

5 2013, n=0

2 Frequency 1

0 0 50 100 150 200 250 300 Total length (mm)

Figure 3-60. Length-frequency distribution for River blackfish at Black Hill Springs, Marne Catchment (Reach 8) from 2009 to 2013 (graphs below the dotted line denote the current reporting period).

146

State of fish communities across the EMLR, 2010 to 2013

Reach 9 – Marne under Murray influence (terminal wetland)

The Marne River terminates at its junction with the River Murray near Wongulla. The Marne Catchment environmental objectives for fish relate to the input of water to create a variable wetland capable of supporting a diverse fish community including diadromous and rare species.

Marne River – Marne Mouth, autumn 2008 (top) and autumn 2012 (bottom)

Flow from the Marne has not reached the terminal wetland for about a decade, but rather River

147

State of fish communities across the EMLR, 2010 to 2013

Murray flows determine water availability and level at this site. Throughout the period of critical water shortage (2007−2010) in the region, the terminal wetland was disconnected from the River Murray and was subsequently dry during monitoring in 2009. Since 2010, improved regional water availability help to reconnect the terminal wetland to the River Murray. The site was sampled in 2012 whilst under flood and native species were in low numbers but relatively diverse (4 native species) and only one introduced species (common carp) was observed.

148

State of fish communities across the EMLR, 2010 to 2013

Overall performance report

The Marne catchment was considered to be in POOR condition in 2009 as fish indicators declined for ecological assets in river reaches upstream of Black Hill Springs (and the Marne Mouth site was dry) (Hammer 2009) (Figure 3-61). Over the present reporting period, there was improvement in ecological assets in the upper catchment and to a lesser extent the Marne mouth (as it received inundation) but the mid reaches continue to decline (Table 6-3). Overall, the catchment was classified as being in POOR condition at the end of the present reporting period.

9 Reach types

8 Headwaters Upper

7 Mid Gorge 6 Lowland 5 Wetlands

4 3

Condition score (out of 9) (out score Condition 1 0 2009 2010 2011 2012 2013 Year

Figure 3-61. Trend in condition score across reach types of the Marne Catchment between 2009 and 2013. Scores for each reach type reflect the median score for all ecological assets present in that reach type (reach types that were not sampled are not presented).

149

State of fish communities across the EMLR, 2010 to 2013

Table 3-18. 2013 report card for the Marne Catchment – a comparison of the performance against fish indicators (blacked out indicators are not relevant to that ecological asset). For each fish indicator, a tick ( ) represents a positive result (e.g. for present, a 2 & 3 for recruitment and survivorship indicators and a score > 4 for diverse fish community), and for all other results a cross ( ) shown. For alien species, ticks indicate the desirable result was observed (i.e. <30% of total site numbers) and crosses indicate a negative result (i.e. >30 of total site numbers). Condition scores for each ecological asset (out of 9) reflect the sum for each indicator (out of 7) plus an alien species score (out of 2). The median of scores for all ecological assets are used to estimate the overall catchment score. For ecological assets and overall catchment score are defined as good (>6, xxx), moderate (3 to 6, xxx) and poor (<3, xxx). See section 2.6 for full explanations. ASSESSMENT for 2013 INDICATOR

Relevant site

Condition Alien species Reach score ECOLOGICAL ASSET Presence Recruitment Survivorship Reach 2 – Upper pool-riffle channel Vigars Rd Mountain galaxias 1 3 1 5 2 7.5 Jutland Rd Mountain galaxias 1 3 2 6 2 Reach 5 - Mid pool-riffle channel Pine Hutt Rd Mountain galaxias 0 0 0 0 0 0.0 Reach 5 - Gorge Marne gorge Mountain galaxias 0 0 0 0 0 0.0 Reach 7 – Lowland channel River blackfish 1 0 1 2 Black Hill Springs 0 2.0 Diverse fish community 2 2 Reach 8 – Marne terminal wetland Marne mouth Diverse fish community n/s

Median 1.0

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State of fish communities across the EMLR, 2010 to 2013

3.8 Reedy Catchment

The Reedy Creek catchment is a large, complex catchment (314km2), reasonably elevated in its upper half which experiences moderate rainfall. Two main sub-catchments drain this upper section: Dairy/Baker Creek and Harrison Creek with an area stretching between Mount Torrens, Tungkillo and the Mt Pleasant-Sedan Road. These drainage networks transcend through very steep rocky sections (numerous natural rock barriers and waterfalls) as they converge towards a point above the Palmer to Mannum Road. Below the junction, Reedy Creek is a lowland stream containing interspersed pools (the small Loxton/Gorge Creek sub catchment joins the main channel in this section), before reaching the Mannum waterfalls. Below the Murray Bridge to Mannum Road crossing, the channel enters an extensive shallow wetland with an opening to the River Murray near Caloote. Stream habitats are highly variable based on the distinct catchment sections. The section above Palmer has a general lack of large and deep permanent pools (long term refuges). There were some springs, but most pools have highly variable water levels, with significant contraction over summer. Spring discharge is apparent in a small section below Palmer. Stock access to watercourses is common in the catchment, with fenced areas highly contrasting in appearance to unfenced sites elsewhere (e.g. thick and diverse riparian vegetation on Bryce Creek).

Overall eight provisional reaches have been defined in the Reedy Creek Catchment (Figure 3-62). Fish related assets identified (by Hammer 2004; and expanded by Smith 2006) include an isolated population of dwarf flathead gudgeon above the Mannum waterfalls (Reaches 5 & 6) and other native fish communities, including estuarine and diadromous in lower reaches (Reaches 7 & 8) (Table 3-19 and Table 3-20). Monitoring of the dwarf flathead gudgeon in spring 2008 identified mountain galaxias in the catchment for the first time, an important new asset for consideration (additional targeted sampling identified them in Reach 4 & 5) (Hammer 2009). The environmental objectives associated with these ecological assets are detailed in Table 3-20.

Over the present reporting period (2010−2013), four sites within three distinct river reaches have been sampled annually and the Lowland Wetland site (in reach 9) was sampled in 2012.

151

State of fish communities across the EMLR, 2010 to 2013

River Murray

Figure 3-62. Map of the Reedy Creek Catchment. The main channels of the catchment (including terminal wetland) are marked as dark blue whereas smaller tributaries streams are marked light blue. The River Murray is denoted as grey.

152

State of fish communities across the EMLR, 2010 to 2013

Table 3-19. Distribution patterns and significant environmental assets in the Reedy Creek Catchment relating to fish species and communities (plus opportunistic data for other biota). Specific asset/pattern Location EWR Table Isolated population of mountain galaxias Reaches 4 & 5 Table 2-4 Isolated population of dwarf flathead gudgeon Reaches 5 & 6 Table 2-7 &Table 2-9 Diadromous fish species Reaches 7 & 8 Table 2-8, Table 2-10 & Table 2-11 No permanent populations present due to lack of summer Reaches 2, 3 Potentially Table 2-4 refuge, natural isolation and water quality (but mountain galaxias may have occurred historically) No permanent fish communities due to lack of Reach 1 NA permanent water Lower Reedy diverse fish community Reaches 7 & 8 Table 2-7, Table 2-10 & Table 2-11

Table 3-20. Summary of environmental objectives by reach for fish related ecological assets in the Reedy Creek Catchment. Asset Environmental Objective Reach 1 –headwaters NA Reach 2 & 3 – Dairy, Bryce & Harrison creeks upper pool/riffle channel (potentially Table 2-4) NA Reach 4 – Gorge 1 (EWR Table 2.3.1) Core refuge of isolated population of Mountain galaxias Maintain and restore self-sustaining population Isolated population of dwarf flathead gudgeon Maintain and restore self-sustaining population Reach 5 – Reedy Creek mid channel (Table 2-4 &Table 2-7) Isolated population of dwarf flathead gudgeon Maintain and restore self-sustaining population Isolated population of mountain galaxias Restore a self-sustaining population (improve from periodic presence) Reach 6 – Mid channel under spring influence (Table 2-7 & Table 2-9) Isolated population of dwarf flathead gudgeon Maintain a self-sustaining population

Reach 7 – Gorge 2 & lowland channel (Table 2-7 & Table 2-10) Diverse fish community of gudgeon species Maintain diversity, demographics and composition of (Philypnodon spp. and Hypseleotris spp.) and fish community diadromous common galaxias Reach 8 – Reedy Creek terminal wetland (Table 2-8 & Table 2-11) Lower Reedy/Murray backwater fish community Maintain diversity and composition of fish community including diadromous species (common galaxias) and Maintain community of diadromous/rare estuarine isolated populations of estuarine species species. (smallmouthed hardyhead and western bluespot goby*) * Estuarine species have rarely been observed outside the Lower Lakes region

153

State of fish communities across the EMLR, 2010 to 2013

Reaches 2 and 3 – upland tributaries

No native fish were recorded in these upland tributaries in 2004, however mountain galaxias were probably present historically. Opportunistic checks for native species presence were made in spring 2008 (Dairy Creek and Talbot Creek), with no fish recorded. These reaches were not sampled over the present reporting period.

Reach 4 – Gorge 1

This reach was sampled in 2004, and although there were permanent pools, no fish were recorded. The discovery of juvenile mountain galaxias in the downstream reach in spring 2008 led to a more detailed investigation that subsequently (later in spring 2008) documented mountain galaxias from several pools in Reedy Creek (Delfabro property) proper and in the southern branch of Baker Creek (Bakers Creek gorge site) where dwarf flathead gudgeon have also been observed.

Bakers Creek – Bakers Creek Gorge, autumn 2009

In spring 2008, Mountain galaxias showed strong spawning at the Reedy Creek (Delfabro property) site (Figure 3-63), however this translated to only low recruitment (40-65mm TL 0+ fish) in autumn 2009.

154

State of fish communities across the EMLR, 2010 to 2013

16 15 2008, n=106 14 13 12 11 10 9 8 7 6 Frequency 5 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 16 15 2008, n=16 14 13 12 11 10 9 8 7 6 Frequency 5 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

Total length (mm)

Figure 3-63. Length-frequency distribution for Mountain galaxias at Reedy Creek (Delfabro property, top) and Bakers Creek (Bakers Creek Gorge), Reedy Catchment (Reach 4) in spring 2008.

Sampling in autumn 2009 saw a dramatic decline in surface water from a series of pools to singular pools in both arms of the reach. There was a matching contraction in range extent of both mountain galaxias and dwarf flathead gudgeon species to a single pool on Baker Creek (Baker Creek Gorge) (Figure 3-64 and Figure 3-65). At this site reasonable survivorship of mountain galaxias (2+ fish, >80mm) and dwarf flathead gudgeon (fish >45mm are likely ≥1+) was revealed. These findings indicate that the Bakers Creek (Baker Creek Gorge) site is likely the key refuge for both mountain galaxias and dwarf flathead gudgeon in the catchment.

The dynamic changes in water availability and the response of mountain galaxias were further highlighted over the present reporting period. Improved water availability was observed in 2010 and the species responded quickly in the refuge pool (Bakers Creek Gorge) with strong recruitment observed. Another recruitment event was observed in 2012 following another flow event in 2011 (with subsequent freshening of the pool, 4010µScm-1). The species was not observed at the Reedy Creek (Delfabro property) site in 2010 but the population gradually increased to 2012 (up to 41 fish) before declining in 2013 (9 fish) but no recruitment was observed. Over the present reporting period, good numbers of dwarf flathead gudgeon were recorded persisting in the Bakers Creek (Bakers Creek Gorge) site (up to 253 fish in 2010) but were absent from the Reedy Creek (Delfabro property) site. Again reasonable survivorship of both species was evident.

155

State of fish communities across the EMLR, 2010 to 2013

16 15 2009, n=0 14 13 12 11 10 9 8 7 6 Frequency 5 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

16 15 2010, n=0 14 13 12 11 10 9 8 7 6 Frequency 5 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

16 15 2011, n=6 14 13 12 11 10 9 8 7 6 Frequency 5 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

16 15 2012, n=41 14 13 12 11 10 9 8 7 6 Frequency 5 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 16 15 2013, n=9 14 13 12 11 10 9 8 7 6 Frequency 5 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

Total length (mm)

Figure 3-64. Length-frequency distribution for Mountain galaxias at Reedy Creek (Delfabro property), Reedy Catchment (Reach 4) from 2009 to 2013 (graphs below the dotted line denote the current reporting period).

156

State of fish communities across the EMLR, 2010 to 2013

16 15 2009, n=29 14 13 12 11 10 9 8 7 6 Frequency 5 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

16 15 2010, n=53 14 13 12 11 10 9 8 7 6 Frequency 5 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

16 15 2011, n=14 14 13 12 11 10 9 8 7 6 Frequency 5 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

16 15 2012, n=101 14 13 12 11 10 9 8 7 6 Frequency 5 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

16 15 2013, n=32 14 13 12 11 10 9 8 7 6 Frequency 5 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 Total length (mm) Figure 3-65. Length-frequency distribution for Mountain galaxias at Bakers Creek (Bakers Creek Gorge), Reedy Catchment (Reach 4) from 2009 to 2013 (graphs below the dotted line denote the current reporting period).

157

State of fish communities across the EMLR, 2010 to 2013

Reach 5 – Mid pool-riffle channel (no springs)

The mid-pool riffle stream between the two gorges on Reedy Creek contains a low gradient section with two reaches, differentiated by the presence or absence of spring discharge. Reach 5 has no spring input and so fluctuates widely in different seasons, representing an important area to test the resilience or survivorship of populations. Monitoring at the Palmer Rd site, recorded mountain galaxias juveniles in spring 2008 but not in autumn of 2008 or 2009 (nor 2004) (Figure 3-66). It is likely that presence in the reach is currently based on immigrants from upstream spawning, which failed to recruit or survive in this reach under the conditions of the 2007 and 2008 flow seasons. Salinity was moderate in spring 2008 when mountain galaxias were recorded (9900µScm-1) but was consistently extremely high (>30,000µScm-1). For dwarf flathead gudgeon there were similar, if less obvious patterns. At this site, as seen in Baker Creek, recruitment was indicated by good representation of 25-40mm fish is spring, and moderate spawning indicated by a pulse of <25mm size fish in autumn 2009. The additional insight of autumn 2008 supports this pattern, and suggest strong spawning in spring/summer 2007.

12 11 2008, n=20 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 Total length (mm)

Figure 3-66. Length-frequency distribution for Mountain galaxias at Reedy Creek (Palmer Rd), Reedy Catchment (Reach 5) in spring 2008.

Annual sampling over the reporting period further supports the pattern of colonisation by upstream recruits, but that largely fail to survive and persist at the site: juvenile mountain galaxias were present in most years (except 2012) but there was only a single fish (90mm) above 60mm (e.g. 1+ fish) (Figure 3-67). Dwarf flathead gudgeon were recorded each year but the numbers declined from 2010 and 2011 (≈100 fish each year) to 2012 and 2013 (≈30 fish each year) as were gambusia (up to 1100 fish in 2010). Salinities were ≈25,000µScm-1 in 2010 before dropping markedly in 2011 (3120µScm-1) due to improved water availability before gradually increasing (2012, 13,200µScm-1; 2013, 24,480µScm- 1) as flows diminished.

158

State of fish communities across the EMLR, 2010 to 2013

16 15 2009, n=0 14 13 12 11 10 9 8 7 6 Frequency 5 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

16 15 2010, n=7 14 13 12 11 10 9 8 7 6 Frequency 5 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

16 15 2011, n=1 14 13 12 11 10 9 8 7 6 Frequency 5 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 12 11 2012, n=24 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2013, n=7 10 9 8 7 6 5 Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

Total length (mm)

Figure 3-67. Length-frequency distribution for Mountain galaxias at Reedy Creek (Palmer Rd), Reedy Catchment (Reach 5) from 2009 to 2013 (graphs below the dotted line denote the current reporting period).

159

State of fish communities across the EMLR, 2010 to 2013

Reach 6 – Mid pool-riffle channel (springs)

Only basic monitoring occurred in this reach, with resources focused on upstream reaches. Available data indicated that the ongoing presence of dwarf flathead gudgeon (to autumn 2009), consistent moderate-high salinity (≈15,000µScm-1) and dense charophytes. This reach was not visited over the present reporting period so it is unclear how populations of the species have responded to changes in water quality.

Reach 7 – Gorge 2 and lowland channel

The second major gorge in the Reedy Creek catchment occurs near its junction with the Murray at the Mannum waterfalls. The gorge itself is steep and difficult to sample but is integrated with a small section of lowland stream before reaching the terminal wetland. The ecological assets of this reach are a diverse lowland fish community including gudgeons and the diadromous common galaxias.

Reedy Creek – downstream Waterfalls, autumn 2013

Regular sampling of this reach between 2001 and 2009 (autumn 2001, 2004, 2008 and 2009, plus an additional spring 2008) has shown that the diversity and abundance of native fish has steadily declined, cumulating in autumn 2009 when only 25 flathead gudgeon were recorded in the refuge pool. Common galaxias have not utilised the area in the same abundance since 2001 (only four fish seen in 2008), smelt have not been recorded since 2001 and carp gudgeons have declined. Flathead gudgeon did remain in similar abundance until autumn 2009. These declines have been attributed to

160

State of fish communities across the EMLR, 2010 to 2013 the general contraction of available habitat from poor stream flow, associated deterioration in water quality (i.e. steady increase in salinity by 300% since 2001 to >21,000 µScm-1 in 2009), and much reduced connectivity with the River Murray through poor Reedy Creek flow and desiccation of the terminal wetland.

Regional increases in water availability over 2010/11 acted to increase Reedy Creek flow and connectivity with the River Murray. Over this time, a greater area of habitat became available and water quality improved with salinities declining markedly (5900µScm-1 in 2011). In autumn 2010, five species were recorded, including good numbers of dwarf flathead gudgeon (500 fish) and flathead gudgeon (850 fish), and gambusia dominated the catch (1950 fish). Reflecting the greater connectivity with the River Murray, common carp and common galaxias were observed, although only in low numbers. Similar catches were observed in 2011. Since this time, however, the reach has undergone considerable habitat contraction and in 2012 and 2013 only the refuge pool persisted. In autumn 2012, five species remained but numbers had diminished, and as habitat and water quality further deteriorated in the refuge pool no fish were observed in autumn 2013. These patterns, emphasising the strong links between this reach and broader water availability, shed light on the likely consequences of drier and warmer conditions under some suggested climate change scenarios.

Reach 8 – Terminal wetland (under Murray influence)

Environmental objectives for the terminal wetland relate to the input of water to create a variable wetland capable of supporting a diverse fish community including diadromous, euryhaline and rare species. The terminal wetland is largely governed by regulated water levels in the Lower Murray with only episodic flows from Reedy Creek. With reduced Lower Murray water availability, the terminal wetland dried in 2007 and subsequent monitoring (2007 to 2009) has observed the site to either consist of only small isolated pools or be once again dry (in autumn 2009). Over this time, only minimal fish were observed (e.g. 41 fish in 2008). Over 2010−11, the terminal wetland flooded in response improved River Murray flow, and monitoring in autumn 2012 revealed a diverse fish community (12 species), including glathead gudgeon (226 fish), congolli (11 fish), Murray-Darling golden perch (3 fish) and aliens: gambusia and common carp.

161

State of fish communities across the EMLR, 2010 to 2013

Overall performance report

In 2009, the catchment was evaluated as being in POOR condition, with the failure of a key indicator, mountain galaxias, highlighted warning signs of potential decline, and the lower catchment was considered in poor condition as it was dry (Hammer 2009) (Figure 3-68). Since this time, mountain galaxias populations have recolonised several sites mid catchment sites but recruitment is generally lacking. Dwarf flathead gudgeon populations have declined across the catchment whilst the terminal wetland improved with inundation associated with the River Murray. Overall, the catchment was classified as being in MODERATE condition at the end of the present reporting period (Table 3-21).

9 Reach types

8 Headwaters Upper 7 Mid 6 Gorge Lowland 5 Wetlands

3 2

of 9) (out score Condition 1

0 2009 2010 2011 2012 2013 Year

Figure 3-68. Trend in condition score across reach types of the Reedy Catchment between 2009 and 2013. Scores for each reach type reflect the median score for all ecological assets present in that reach type (reach types that were not sampled are not presented).

162

State of fish communities across the EMLR, 2010 to 2013

163

State of fish communities across the EMLR, 2010 to 2013

Table 3-21. 2013 report card for the Reedy Catchment – a comparison of the performance against fish indicators (blacked out indicators are not relevant to that ecological asset). For each fish indicator, a tick ( ) represents a positive result (e.g. for present, a 2 & 3 for recruitment and survivorship indicators and a score > 4 for diverse fish community), and for all other results a cross ( ) shown. For alien species, ticks indicate the desirable result was observed (i.e. <30% of total site numbers) and crosses indicate a negative result (i.e. >30 of total site numbers). Condition scores for each ecological asset (out of 9) reflect the sum for each indicator (out of 7) plus an alien species score (out of 2). The median of scores for all ecological assets are used to estimate the overall catchment score. For ecological assets and overall catchment score are defined as good (>6, xxx), moderate (3 to 6, xxx) and poor (<3, xxx). See section 2.6 for full explanations. ASSESSMENT for 2013 INDICATOR

Relevant site

Condition

Alien species

Reach Reach score

Presence

Recruitment ECOLOGICAL ASSET Survivorship Reach 4 – Gorge Dwarf flathead gudgeon 1 0 0 1 Bakers Gorge 2 Mountain galaxias 1 0 3 4 4.5 Dwarf flathead gudgeon 0 0 0 0 Delfabro property 2 Mountain galaxias 1 0 3 4 Reach 5 - Mid pool-riffle channel Dwarf flathead gudgeon 1 2 1 4 Palmer Road 0 3.5 Mountain galaxias 1 2 0 3 Reach 7 – Lowland channel Mannum waterfalls Diverse fish community 1 1 1 2.0 Reach 8 – Reedy creek terminal wetland Lowland wetland Diverse fish community n/s

Median 3.5

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State of fish communities across the EMLR, 2010 to 2013

3.9 Rocky Gully, Salt and Preamimma catchments

The Salt Creek Catchment is a medium-sized catchment (199km2) at the extremities of the EMLR (small split of the Range on the eastern edge of the Bremer Valley). As a consequence it has low topography and low, highly variable rainfall. Much of the catchment comprises plains, with only a small defined elevated section of channel in the upper sections stretching from near Bondleigh to Tepko (i.e. Salt Creek and Long, Mitchell, Gum and Flag gullies). From below the Murray Bridge to Wellington Road the main ephemeral channel is shallow and poorly defined. Stream habitat is restricted to irregular pools along defined channels and given the dry, warm landscape, permanent pools are clearly maintained by vertical connectivity to groundwater sources. While there is not a great number of permanent pools (as of 2004), it is surprising to note some are quite large and up to 1.5m deep (e.g. Round Waterhole), serving as drought refuges. Several core refuges are fenced, otherwise stock access is common along watercourses in the catchment. Water conductivities are very high (as the creek name suggest, between 15,000-30,000µScm-1). Rocky Gully and Preamimma creeks are almost devoid of pool habitat, with some minor spring soakage in mid-upper catchment areas, plus wetlands and some pools in the lower terminal ends of catchments under Murray influence.

Overall five provisional reaches have been defined for the grouped Salt, Preamimma and Rocky Gully creek catchments (Figure 3-69). A recent scarcity of water, high salinity and general isolation meant that few fish related ecological assets were identified by Hammer (2004), however Smith (2006) and Hammer (unpublished data) identified important species and native fish communities in terminal wetland areas of the Rocky Gully and Salt/Preamimma stream channels. Assets include a diverse native fish community including isolated population of Murray hardyhead, freshwater catfish juveniles, isolated populations of estuarine species, and diadromous species (Table 3-25 and Table 3-23) and these match fish related ecological assets identified to the relevant EWR tables of Section 2.

Over the present reporting period (2010−2013), only the terminal wetland (Rocky Gully wetland) was sampled annually.

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State of fish communities across the EMLR, 2010 to 2013

River Murray

0 1.25 2.5 5 ¯ Kilometers Figure 3-69. Map of the Salt, Preamimma and Rocky Gully creek catchments. The main channels of the catchment (including terminal wetland) are marked as dark blue whereas smaller tributaries streams are marked light blue. The River Murray is denoted as grey.

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State of fish communities across the EMLR, 2010 to 2013

Table 3-22. Distribution patterns and significant environmental assets in Salt, Preamimma and Rocky Gully creek catchments relating to fish species and communities (plus opportunistic data for other biota). Specific asset/pattern Location EWR Table Isolated population of Murray hardyhead (Rocky Gully Reach 5 Table 2-11 (spatial Creek terminal wetland) variation in salinity compared to other Murray wetlands) Lower Rocky Gully Creek diverse fish community Reach 5 Table 2-11 including juveniles of threatened freshwater catfish and rare estuarine species Diadromous fish species in lower Rocky Gully Creek Reach 5 Table 2-8 & Table 2-11 Native fish present (flathead gudgeon) in pools on lower Reach 5 Table 2-8 & Table 2-11 Salt/Preamimma creeks No permanent populations present due to lack of summer Reaches 2, 3 & 4 NA refuge, natural isolation and/or water quality No permanent fish communities due to lack of Reach 1 NA permanent water

Table 3-23. Summary of environmental objectives by reach for fish related ecological assets in the Salt, Preamimma and Rocky Gully creek catchments. Asset Environmental Objective Reach 1 –headwaters NA Reach 2 – Salt Creek pool/riffle channel NA Reach 3 – Under spring influence - deeper spring fed pools on Salt Creek, small section of surface baseflow on Preamimma Creek NA Reach 4 – Ephemeral main channels NA Reach 5 – Terminal wetlands under Murray Influence (Table 2-7, Table 2-8 & Table 2-11) Rocky Gully Creek/Murray backwater diverse fish Maintain diversity and composition of fish community community including Murray hardyhead, juvenile Maintain spawning habitat of freshwater catfish freshwater catfish, diadromous species (common Maintain community of diadromous/rare estuarine galaxias), and isolated populations rare estuarine species. species (lagoon goby, western bluespot goby and smallmouthed hardyhead*) Isolated population of Murray hardyhead (Rocky Gully Maintain a self-sustaining population Creek terminal wetland) Population of native fish (flathead gudgeon) present Maintain a self-sustaining population (Salt/Preamimma creeks) * Estuarine species are rare outside the Lower Lakes being recorded only at a handful of sites along the lower River Murray

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State of fish communities across the EMLR, 2010 to 2013

Reach 5 – Terminal wetland (under Murray influence)

Environmental objectives for the reach relate to the input of water to create a variable wetland capable of supporting a diverse fish community including threatened species, diadromous and euryhaline species. Previous sampling has focused on Rocky Gully where both Murray hardyhead and freshwater catfish have been previously reported (forming self-sustaining populations) in the wetland and channel. Moreover, Smith (2006) reported some 16 native species in baseline surveys including isolated upstream populations of several eurhayline species.

Rocky Gully wetland (channel) in autumn 2012

Sampling between 2007 and 2009, showed that the wetland retained a diverse fish community up until dramatic water level lowering from 2007 in the Lower Murray which lead to drying of the channel below the control structure and disconnecting the remaining channel and wetland from the River Murray. After disconnection (i.e. autumn 2008 and 2009 data) species diversity declined dramatically, to the point that only Murray hardyhead and smallmouthed hardyhead were recorded in autumn 2009. Salinity in the wetland increased significantly (>50,000µScm-1) and general water quality conditions (e.g. dissolved oxygen at depth) became critical. The abundance of Murray hardyhead suffered a major reduction, testing the recovery of a self-sustaining population. In autumn 2010, salinity remained high (>37,000µScm-1) and smallmouthed hardyhead were the only fish species present (Murray hardyhead were absent). Substantial inflows (from River Murray) led to considerable freshening of the terminal wetland (only 2296µScm-1) and a diverse fish community has

168

State of fish communities across the EMLR, 2010 to 2013 been observed during annual sampling since this time. In autumn 2011, Flathead gudgeon (1072 fish) dominated and the rarer species Freshwater catfish (38 fish) and Murray-Darling rainbowfish (17 fish) were present. Significantly, Murray hardyhard were once again recorded in the wetland (14 fish). In autumn 2012 and 2013, a high number of species were again observed (9 species, 2012; 10 species, 2013) but only a single Murray hardyhard, perhaps reflecting the freshness of the site (e.g. as low as 1450 µScm-1 in 2013). Flathead gudgeon populations in Salt and Preamimma catchments were not assessed over the present reporting period.

169

State of fish communities across the EMLR, 2010 to 2013

Overall performance report

In 2009, these catchments were considered to be in POOR condition with obvious signs of stress from an altered River Murray environment and connection (Figure 3-70). Increased inflows initially led to the return of Murray hardyhead and a more diverse fish community in the terminal wetland. However, in recent years (2012, 2013), Murray hardydhead has not been detected and fish community has deteriorated (i.e. increasing number of Gambusia). Overall, these catchments were classified as being in POOR condition at the end of the present reporting period (Table 3-27).

9 Reach types

8 Headwaters Upper 7 Mid

6 Gorge Lowland 5 Wetlands 4

Condition score (out of 9) (out score Condition 1

0 2009 2010 2011 2012 2013

Year

Figure 3-70. Trend in condition score across reach types of the Salt, Preamimma and Rocky Gully catchments between 2009 and 2013. Scores for each reach type reflect the median score for all ecological assets present in that reach type (reach types that were not sampled are not presented).

170

State of fish communities across the EMLR, 2010 to 2013

Table 3-24. 2013 report card for the Salt, Preamimma and Rocky Gully catchments – a comparison of the performance against fish indicators (blacked out indicators are not relevant to that ecological asset). For each fish indicator, a tick ( ) represents a positive result (e.g. for present, a 2 & 3 for recruitment and survivorship indicators and a score > 4 for diverse fish community), and for all other results a cross ( ) shown. For alien species, ticks indicate the desirable result was observed (i.e. <30% of total site numbers) and crosses indicate a negative result (i.e. >30 of total site numbers). Condition scores for each ecological asset (out of 9) reflect the sum for each indicator (out of 7) plus an alien species score (out of 2). The median of scores for all ecological assets are used to estimate the overall catchment score. For ecological assets and overall catchment score are defined as good (>6, xxx), moderate (3 to 6, xxx) and poor (<3, xxx). See section 2.6 for full explanations. ASSESSMENT for 2013 INDICATOR

Relevant site

Condition

Alien species

Reach Reach score

Presence

Recruitment ECOLOGICAL ASSET Survivorship Reach 5 – Terminal wetland under Murray influence Murray hardyhead 0 0 0 0 Rocky Gully Wetland 0 1.0 Diverse fish community 2 2

Median 1.0

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State of fish communities across the EMLR, 2010 to 2013

3.10 Saunders Catchment

The Saunders Creek Catchment is of moderate size (222km2); being a narrow, long area stretching from near Springton through to the River Murray north east of Mannum. Only a small section of the catchment extends into higher elevations and hence rainfall is low and irregular across most of the catchment (and even here there appears to be a significant rain shadow effect). Its headwaters comprise two small tributary streams that flow in a northerly direction, before both turn to the east and join just before a steep rocky gorge. From below the gorge, the Saunders Creek is an ephemeral channel that meanders in a roughly south easterly direction until reaching a small section of spring fed, permanent pools lined with red gum and Phragmites in the region of Lenger Reserve (~5km upstream from the River Murray). Below here, the channel is once again ephemeral and shallow, with no significant defined wetland area where the Creek joins the Murray. There is little permanent stream habitat in the catchment today, with only a few pools upstream of and in the Saunders Gorge, and the small string of pools near Lenger Reserve. Stock access is common across considerable sections of the Catchment, however, where water occurs some areas have been fenced or have no stock (e.g. Saunders Gorge Sanctuary and some areas upstream from here; Lenger Reserve and upstream pools). In-stream habitat values are low, with generally ~20-30% submerged physical cover (rock, snags), no submerged aquatic vegetation (with the exception of Chara recorded from a small spring on Kinappa Creek, a small gully near Saunders Gorge) and only small amounts of submerged Typha or Phragmites at a few sites. Autumn water conductivity values are moderate to high (e.g. 5780−10,030μScm-1 in 2004).

Six provisional rivers reaches are defined in the Saunders Catchment (Figure 3-71) and only one ecological asset – a single Murray-Darling carp gudgeon population restricted to the small section of permanent pools at or above Lenger Reserve (Reach 5), has been identified in the catchment (Table 3-25) (Hammer 2004). The environmental objectives associated with this, and other potential, ecological assets are also detailed in Table 3-23.

Monitoring of this catchment has been periodic, occurring in 2009 at two sites in Reach 5 and as opportunistic checks for native species in the upper catchment. Over the present reporting period (2010−2013), the Lenger Reserve site was not monitored in 2010 but was visited annually between 2011 and 2013.

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State of fish communities across the EMLR, 2010 to 2013

River 0 1.25 2.5 5 Kilometers Murray

Figure 3-71. Map of the Saunders Creek Catchment. The main channels of the catchment (including terminal wetland) are marked as dark blue whereas smaller tributaries streams are marked light blue. The River Murray is denoted as grey.

Table 3-25. Distribution patterns and significant environmental assets in the Saunders Creek Catchment relating to fish species and communities (plus opportunistic data for other biota). Specific asset/pattern Location EWR table Isolated population of carp gudgeon Reach 5 Table 2-7 & Table 2-9 No permanent populations present due to lack of summer NA, but potentially Table refuge, isolation and water quality (but mountain galaxias Reach 2, 3 2-4 may have been present historically) No permanent fish communities due to lack of Reaches 1 and 4, and NA permanent water possibly Reach 6 Diverse terminal wetland fish community potentially Reach 6 Table 2-11 present

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State of fish communities across the EMLR, 2010 to 2013

Table 3-26. Summary of environmental objectives by reach for fish related ecological assets in the Saunders Creek Catchment. Asset Environmental Objective Reach 1 Saunders Creek headwaters and minor tributaries NA Reach 2 – Upper Saunders pool/riffle channel (potentially EWR Table 2-4) NA Reach 3 – Saunders Gorge (potentially EWR Table 2-4) NA Reach 4 – Ephemeral channel NA Reach 5 – Lower Saunders under spring influence (EWR Table 2-7 & Table 2-9) Isolated population of carp gudgeon Maintain or restore self-sustaining population Reach 6 – Saunders under Murray influence (potentially EWR Table 2-11) Lower Saunders/Murray backwater fish community (if Restore diversity and composition of fish community present)

Reach 5 – Lower Saunders under spring influence

Monitoring of this reach in 2004 revealed a stable carp gudgeon population with high abundances and juveniles, and gambusia were also present in high numbers (Hammer 2004). Yet, in autumn 2009, low numbers of carp gudgeon and no signs of recent recruitment (all fish >40mm) were observed, whilst gambusia remained very common (observations of mixed sizes including juveniles) and a single adult common carp (480mm) was recorded (Hammer 2009). Over the present reporting period (2010−2013), the decline of the carp gudgeon population continued with no fish in 2011 and low abundance in the other years (<12 fish) whereas large fluctuations in gambusia were realised (415−5347 fish). Salinities >10,000µScm-1 were experienced over the past two years, which helps to explain the low numbers of carp gudgeon, and fresher conditions will be necessary to promote recruitment and survivorship (and expansion) of the population. Overall this reach is considered in moderate condition as it was no longer dry (as was the case during the 2009 assessment).

174

State of fish communities across the EMLR, 2010 to 2013

Saunders Creek – Lenger Reserve, autumn 2013

175

State of fish communities across the EMLR, 2010 to 2013

Overall performance report

In 2009, the Saunders Creek catchment was evaluated as being in a POOR condition with obvious signs of stress as a consequence of the dry climatic period (e.g. the long-term monitoring site has dry in autumn 2009) (Hammer 2009) (Figure 3-72). Over the present reporting period, the lower reaches of the catchment benefited from regional water availability but remained stressed (e.g. salinities >10,000µScm-1 at the long-term monitoring site) and although carp gudgeon did recolonise the long- term monitoring site, only minimal recovery in condition was evident (Table 3-27). Overall, the catchment was again classified as being in POOR condition at the end of the present reporting period (2013).

9 Reach types 8 Headwaters Upper 7 Mid

6 Gorge Lowland Wetlands 5 4

Condition score (out of 9) (out score Condition 1 0 2009 2010 2011 2012 2013 Year

Figure 3-72. Trend in condition score across reach types of the Saunders Catchment between 2009 and 2013. Scores for each reach type reflect the median score for all ecological assets present in that reach type (reach types that were not sampled are not presented).

176

State of fish communities across the EMLR, 2010 to 2013

Table 3-27. 2013 report card for the Saunders Catchment – a comparison of the performance against fish indicators (blacked out indicators are not relevant to that ecological asset). For each fish indicator, a tick ( ) represents a positive result (e.g. for present, a 2 & 3 for recruitment and survivorship indicators and a score > 4 for diverse fish community), and for all other results a cross ( ) shown. For alien species, ticks indicate the desirable result was observed (i.e. <30% of total site numbers) and crosses indicate a negative result (i.e. >30 of total site numbers). Condition scores for each ecological asset (out of 9) reflect the sum for each indicator (out of 7) plus an alien species score (out of 2). The median of scores for all ecological assets are used to estimate the overall catchment score. For ecological assets and overall catchment score are defined as good (>6, xxx), moderate (3 to 6, xxx) and poor (<3, xxx). See section 2.6 for full explanations. ASSESSMENT for 2013 INDICATOR

Relevant site

Condition

Alien species

Reach Reach score

Presence

Recruitment ECOLOGICAL ASSET Survivorship

Reach 5 - Lowland Lenger Reserve Carp gudgeon 1 0 1 2 0 2.0

Median 2.0

177

State of fish communities across the EMLR, 2010 to 2013

3.11 Tookayerta Catchment

Characterised by glacial sands, peat, swamp heath vegetation and high rainfall, the Tookayerta Creek Catchment is highly contrasting to other catchments in the EMLR and indeed elsewhere in the state and Murray-Darling Basin. It is a small catchment (100km2) perched in a low gradient basin with headwaters originating on either side of the Mount Compass Township. However, these are not headwaters in the traditional sense, rather a series of interconnected swamps (under natural conditions) along shallow depressions. The catchment is Y shaped with basically three main arms: the Nangkita Creek and upper Tookayerta Creek (forming the branches of the Y) and a smaller tributary, Swampy Creek. These unite to form a continuous lower Tookayerta Creek section eventually connecting with the Finniss River arm of Lake Alexandrina. Stream habitats are generally heavily associated with swampy littoral areas or disappear into swamp vegetation (e.g. tea tree) or large beds of Phragmites along stream sections. The Swampy Creek area (and indeed much of the catchment) would have once been a semi-continuous swamp, however, clearance (physical and by stock), excavation and drainage now means that fragments of swamps are interconnected by channels or dams. Creek lines are modified or artificial in many areas but there are still true lotic habitats, particularly in upper Tookayerta Creek. There is stock access in places of the catchment, but considerable areas are fenced or have alternate land use.

Eight provisional reaches have been defined in the Tookayerta Creek Catchment, and these need some revision in line with broader geomorphologic review; however, this does not affect current monitoring sites (Figure 3-73). Fish related assets identified by Hammer (2004) are shown in Table 3-28 and Table 3-29 along with associated environmental objectives. These include:

 a patchy but secure population of river blackfish in unique swampy habitat,  two genetically distinct populations of southern pygmy perch (a Tookayerta sub-population in the upper catchment and a Lake Alexandrina sub-population in the terminal wetland: Hammer 2001),  mountain galaxias populations which along with the Finniss represent a different species to other EMLR catchments (SA Museum unpublished),  one of only two populations of Yarra pygmy perch in the Murray-Darling Basin occurring in the Tookayerta/Finniss terminal wetland (Reach 8), and  diverse native fish communities in the terminal wetland. Long-term monitoring has occurred in several reaches since 2001 and over the present reporting period (2010−2013), between 5−7 sites across five reaches were sampled annually.

178

State of fish communities across the EMLR, 2010 to 2013

Finniss River

0 1.25 2.5 5 Kilometers ¯ Figure 3-73. Map of the Tookayerta Creek Catchment. The main channels of the catchment (including terminal wetland) are marked as dark blue whereas smaller tributaries streams are marked light blue. The Finniss River is denoted as grey

Table 3-28. Distribution patterns and significant environmental assets in the Tookayerta Catchment relating to fish species and communities. Specific asset/pattern Location EWR Table Genetically distinct Tookayerta southern pygmy perch Reaches 2 (marginal Table 2-6, Table 2-9 & population) 3, 4, 5, 6 & 7. Table 2-12 River blackfish Reaches 4, 5, 6 & 7 Table 2-5, Table 2-9 & Table 2-12 Mountain galaxias (Finniss and Tookayerta catchments Reaches 2-6 Table 2-4, Table 2-9 & different species from rest of EMLR) Table 2-12 Lower Tookayerta/terminal wetland diverse fish Reach 8 Table 2-10 & Table 2-11 community Yarra pygmy perch Reach 8 Table 2-11 Presence of diadromous fish species Reach 8 Table 2-8 No permanent fish communities due to lack of Reach 1 (patchy NA (possibly Table 2-4, permanent water populations may be present Table 2-5 & Table 2-12) in perched swamps)

179

State of fish communities across the EMLR, 2010 to 2013

Table 3-29. Summary of environmental objectives by reach for fish related ecological assets in the Tookayerta Creek Catchment. Asset Environmental Objective Reach 1 – Tookayerta Catchment headwaters NA Reach 2 – Upland pool/riffle channel (Table 2-4, Table 2-5& Table 2-6) Mountain galaxias Maintain or restore self-sustaining population Southern pygmy perch and river blackfish Maintain or restore self-sustaining population Reach 3 – Upper catchment spring fed Fleurieu Swamps (Table 2-12) Mountain galaxias Maintain or restore self-sustaining population Genetically distinct Tookayerta southern pygmy perch Maintain (e.g. Square Waterhole) and restore (School Swamp) self-sustaining populations Reach 4 – Swampy Creek spring fed swamp section (Table 2-6 & Table 2-12) Genetically distinct Tookayerta southern pygmy perch Maintain or restore self-sustaining population Mountain galaxias Maintain or restore self-sustaining population Reach 5 – Spring fed pool/riffle sequence (Table 2-4, Table 2-5, Table 2-6 & Table 2-9) Genetically distinct Tookayerta southern pygmy perch Maintain or restore self-sustaining population River blackfish Maintain or restore self-sustaining population Mountain galaxias Maintain or restore self-sustaining population Reach 6 – Perennial (spring influence) high flow pool-riffle sequence (Table 2-4, Table 2-5& Table 2-9) River blackfish Maintain or restore self-sustaining population (population potentially structured by brown trout) Mountain galaxias Maintain or restore self-sustaining population (population structured by brown trout) Reach 7 – Lowland pool and swamp sequence (potentially under spring influence) (Table 2-5, Table 2-6 & Table 2-12) Genetically distinct Tookayerta southern pygmy perch Maintain or restore self-sustaining population population River blackfish Maintain or restore self-sustaining population Reach 8 – Black swamp and terminal wetland under Lake Alexandrina influence (Table 2-8, Table 2-10 & Table 2-11) Yarra pygmy perch Maintain or restore self-sustaining population Diverse native fish community including threatened Maintain or restore diversity and composition of fish southern pygmy perch (Lake Alexandrina sub-population community – Black Swamp and terminal wetland)

180

State of fish communities across the EMLR, 2010 to 2013

Reach 2 – Nangkita upper pool-riffle channel

Baseline sampling identified mountain galaxias and southern pygmy perch in this reach, but it has not been monitored since (but may be comparable to the inter-connected spring fed reach 5).

Reaches 3 & 4 – Fleurieu swamps

The Tookayerta Catchment is unique among other EMLR catchments in containing areas of the nationally threatened (and EPBC Act 1999 listed) Fleurieu Swamp ecological community. Baseline sampling indicated this habitat type is occupied by several native species in different areas of the catchment with southern pygmy perch a key ecological asset. One swamp section, Swamp Creek, has had a long-term monitoring site at Brawley’s Swamp. From 2007 to 2009, southern pygmy perch relative abundance remained low (<25 fish) and low levels of recruitment were observed, with occasional better years - such as that observed from autumn 2008 data (Figure 3-74). The extreme summer of 2009 lead to the cessation of base flow and drying of most surface water in the swamp, with a matching loss of fish fauna detected in the subsequent autumn.

Shallow, densely vegetated Fleurieu Swamp habitat at Swamp Creek (autumn 2009)

Sampling in autumn of each year over the present reporting period has indicated that the species has failed to recolonise the site despite the return of conditions, similar to those prior to 2009, which are capable of sustaining small populations. It appears that the lack of nearby source populations or impaired connectivity have limited the ability of the species to recolonise the site.

181

State of fish communities across the EMLR, 2010 to 2013

20 2004, n=4 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2005, n=0 18 16 14 12 No sampling 10 8 undertaken

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2006, n=3 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 20 2007, n=3 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2008 n=28 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

Total length (mm)

Figure 3-74. Length-frequency distribution for southern pygmy perch in Fleurieu Swamps (Brawleys Swamp), Tookayerta Catchment (Reach 3 and 4) between 2004 and 2008.

182

State of fish communities across the EMLR, 2010 to 2013

Reach 5 – Nangkita spring fed upper pool-riffle channel

This perennial stream reach has high ecological value containing populations of three threatened freshwater specialists, and has been monitored at least annually between 2001 and 2013. Mountain galaxias show variable abundance but with strong recruitment and survivorship in most years (Figure 3-75 and Figure 3-76). Abundance has been down slightly over the past three years, but recruitment (and survivorship) is still evident. River blackfish are more difficult to monitor owing to dense cover and dark substrate, but even so, ongoing recruitment and moderate survivorship has been noted (Figure 3-77 and Figure 3-78). Strong recruitment was particularly evident over the present reporting period, with the largest recruitment event over the 2001-2013 period occurring in 2011. Southern pygmy perch have persisted strongly, particularly from 2007 onwards (with 61 fish in 2013) (Figure 3-79 and Figure 3-80). Broad population structure size was observed over the present reporting period, and further supports the likelihood of protracted or extended spawning and recruitment atypical to that seen in other populations. No introduced species were observed over the present reporting period, having only been occasionally observed prior to 2010. Environmental data has remained fairly consistent at this site, with low salinity (<500µScm-1), cool flowing water, and moderate levels of submerged physical and emergent cover.

Willowburn Road site on Nangkita Creek autumn 2013

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State of fish communities across the EMLR, 2010 to 2013

12 11 2004, n=17 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2005, n=17 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2006, n=5 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 12 11 2007, n=6 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2008, n=18 10 9 8 7 6 5 Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

Total length (mm)

Figure 3-75. Length-frequency distribution for mountain galaxias in Nangkita Creek (us Willowburn Road), Tookayerta Catchment (Reach 5) between 2004 and 2008.

184

State of fish communities across the EMLR, 2010 to 2013

12 11 2009, n=48 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2010, n=35 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2011, n=4 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130 12 11 2012, n=13 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

12 11 2013, n=21 10 9 8 7 6 5 Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 100 110 120 130

Total length (mm)

Figure 3-76. Length-frequency distribution for mountain galaxias in Nangkita Creek (us Willowburn Road), Tookayerta Catchment (Reach 5) between 2009 and 2013 (graphs below the dotted line denote the current reporting period).

185

State of fish communities across the EMLR, 2010 to 2013

12 11 2004, n=4 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 50 100 150 200 250 300

12 11 2005, n=4 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 50 100 150 200 250 300

12 11 2006, n=0 10 9 8 7 No sampling 6 5 undertaken

Frequency 4 3 2 1 0 0 50 100 150 200 250 300 12 11 2007 n=7 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 50 100 150 200 250 300

12 11 2008, n=7 10 9 8 7 6 5 Frequency 4 3 2 1 0 0 50 100 150 200 250 300 Total length (mm)

Figure 3-77. Length-frequency distribution for river blackfish in Nangkita Creek (us Willowburn Road), Tookayerta Catchment (Reach 5) between 2004 and 2008.

186

State of fish communities across the EMLR, 2010 to 2013

12 11 2009, n=7 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 50 100 150 200 250 300

12 11 2010, n=10 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 50 100 150 200 250 300

12 11 2011, n=58 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 50 100 150 200 250 300 12 11 2012, n=10 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 50 100 150 200 250 300

12 11 2013, n=27 10 9 8 7 6 5 Frequency 4 3 2 1 0 0 50 100 150 200 250 300 Total length (mm)

Figure 3-78. Length-frequency distribution for river blackfish in Nangkita Creek (us Willowburn Road), Tookayerta Catchment (Reach 5) between 2009 and 2013 (graphs below the dotted line denote the current reporting period).

187

State of fish communities across the EMLR, 2010 to 2013

20 2004, n=16 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2005, n=17 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2006, n=18 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 20 2007, n=48 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2008 n=42 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 Total length (mm)

Figure 3-79. Length-frequency distribution for southern pygmy perch in Nangkita Creek (us Willowburn Road), Tookayerta Catchment (Reach 5) between 2004 and 2008.

188

State of fish communities across the EMLR, 2010 to 2013

20 2009 n=24 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2010, n=21 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2011, n=38 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 20 2012, n=22 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2013, n=61 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

Total length (mm)

Figure 3-80. Length-frequency distribution for southern pygmy perch in Nangkita Creek (us Willowburn Road), Tookayerta Catchment (Reach 5) between 2009 and 2013 (below the dotted line denote the current reporting period).

189

State of fish communities across the EMLR, 2010 to 2013

Reach 6 – Tookayerta spring fed upper pool-riffle channel

This reach has strong perennial flow with a core population of river blackfish and occasional other native species (mountain galaxias and southern pygmy perch). A site free from brown trout (the species is common in the reach) has been monitored since 2004. Low numbers of blackfish have been consistently recorded within a small stretch of habitat, but importantly this has included young of year (0+) fish in most years, including 2011 and 2012 (Figure 3-81 and Figure 3-82). The increasing numbers of mountain galaxias and southern pygmy perch observed at the site from 2007 to 2009 have not continued over the present reporting period. Whilst introduced species are uncommon, single large redfin (>150mm) have been recorded, possibly accounting for reduced native fish abundance in the small monitoring pool. Environmental conditions have been stable with low salinity (<350µScm-1), cool, flowing water and moderate levels of cover and, as of 2012, the site remained in good condition. However, landowner access to the site was not granted in 2013 and it may be necessary to establish a new monitoring site within this reach.

Compass Cabins site on Tookayerta Creek autumn 2012

190

State of fish communities across the EMLR, 2010 to 2013

12 11 2004, n=5 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 50 100 150 200 250 300

12 11 2005, n=3 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 50 100 150 200 250 300

12 11 2006, n=6 10 9 8 7 6 5 Frequency 4 3 2 1 0 0 50 100 150 200 250 300

12 11 2007 n=3 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 50 100 150 200 250 300

12 11 2008, n=4 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 50 100 150 200 250 300 Total length (mm)

Figure 3-81. Length-frequency distribution for river blackfish in Tookayerta Creek (Compass Cabins), Tookayerta Catchment (Reach 6) between 2004 and 2008.

191

State of fish communities across the EMLR, 2010 to 2013

12 11 2009, n=4 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 50 100 150 200 250 300

12 11 2010, n=4 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 50 100 150 200 250 300

12 11 2011, n=5 10 9 8 7 6 5 Frequency 4 3 2 1 0 0 50 100 150 200 250 300

12 11 2012, n=4 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 50 100 150 200 250 300

Total length (mm)

Figure 3-82. Length-frequency distribution for river blackfish in Tookayerta Creek (Compass Cabins), Tookayerta Catchment (Reach 6) between 2009 and 2012 (note: no access in 2013).

192

State of fish communities across the EMLR, 2010 to 2013

Reach 7 – Tookayerta lowland channel

The lowland reach of the Tookayerta Creek contains larger pools interspersed with sections of swamp, which has been identified as core habitat for southern pygmy perch, with less abundant river blackfish and mountain galaxias. Monitoring at Deep Creek Road since 2001 has recorded southern pygmy perch in moderate to high abundance up to 2008, with fewer fish recorded in autumn 2009 and low numbers (<12 fish each year) over the present reporting period (Figure 3-83 and Figure 3-84). Ongoing recruitment and survivorship has been observed (even as abundance has declined), and the broad population structure has revealed length frequency data that indicates a likely protracted spawning associated with cool base flows (similar to Willowburn Road site). Electrofishing data for 2006 onwards recorded low and variable numbers of river blackfish, however spikes correlating to young of year fish (<80mm) are noted in most years, including all of those of the present reporting period (Figure 3-85 and Figure 3-86). Gambusia were recorded in low abundance over the prior to 2010, but no introduced species were sampled over the present reporting period.

Deep Creek Road site on Tookayerta Creek autumn 2005

Environmental data at this site has been consistent, with low salinity (<900µScm-1) and low to medium flow recorded in all autumns. Flow at the site was observed to have ceased in summer 2008 and 2009 but flows appear to have returned to the site over the present reporting period. The levels of emergent cover have been steadily increasing since 2001, and conversely depth has been

193

State of fish communities across the EMLR, 2010 to 2013 decreasing, mainly through the encroachment of Phragmites and concentration of silt, Azolla and Callitriche within its stems. This was been particularly apparent in the low flow conditions experienced over 2008 and 2009. Through the present reporting period, slightly increased depth (1.3−1.8m over 2010−2013) has been observed but vegetation encroachment and siltation was still evident, suggesting that flows have not returned to pre-critical water shortage levels. Overall, the sites remains in good condition as it allows persistence of key ecological assets through time, especially over low flow periods. However, the decline in southern pygmy perch since the last assessment and changes possibly attributed to reducing flows suggest a declining trend in condition.

Deep Creek Road site on Tookayerta Creek autumn 2013

194

State of fish communities across the EMLR, 2010 to 2013

20 2004, n=80 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2005, n=46 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2006, n=28 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 20 2007, n=28 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2008 n=31 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

Total length (mm)

Figure 3-83. Length-frequency distribution for southern pygmy perch in Tookayerta Creek (Deep Creek Road), Tookayerta Catchment (Reach 7) between 2004 and 2008 (below the dotted line denote the current reporting period).

195

State of fish communities across the EMLR, 2010 to 2013

20 2009 n=13 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2010, n=5 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2011, n=12 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 20 2012, n=8 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90

20 2013, n=6 18 16 14 12 10 8

Frequency 6 4 2 0 0 10 20 30 40 50 60 70 80 90 Total length (mm)

Figure 3-84. Length-frequency distribution for southern pygmy perch in Tookayerta Creek (Deep Creek Road), Tookayerta Catchment (Reach 7) between 2009 and 2013 (graphs below the dotted line denote the current reporting period).

196

State of fish communities across the EMLR, 2010 to 2013

12 11 2006, n=7 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 50 100 150 200 250 300

12 11 2007, n=0 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 50 100 150 200 250 300

12 11 2008 n=7 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 50 100 150 200 250 300 Total length (mm)

Figure 3-85. Length-frequency distribution for river blackfish in Tookayerta Creek (Deep Creek Road), Tookayerta Catchment (Reach 7) between 2006 and 2008.

197

State of fish communities across the EMLR, 2010 to 2013

12 11 2009 n=5 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 50 100 150 200 250 300

12 11 2010, n=16 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 50 100 150 200 250 300

12 11 2011, n=8 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 50 100 150 200 250 300 12 11 2012, n=4 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 50 100 150 200 250 300

12 11 2013, n=6 10 9 8 7 6 5 Frequency 4 3 2 1 0 0 50 100 150 200 250 300 Total length (mm)

Figure 3-86. Length-frequency distribution for river blackfish in Tookayerta Creek (Deep Creek Road), Tookayerta Catchment (Reach 7) between 2009 and 2013 (graphs below the dotted line denote the current reporting period).

198

State of fish communities across the EMLR, 2010 to 2013

Reach 8 – Terminal wetland (Black Swamp)

The terminal wetland of Tookayerta Creek is quite extensive including a large section of swamp downstream of Winery Road extending into a small open water wetland at the junction of the Finniss River in Lake Alexandrina. The swamp section contains southern pygmy perch, diadromous species and some wetland generalists, while the wetland section additionally contains wetland specialists such as Yarra pygmy perch. Access is generally limited in this reach, however a site in the swamp has been monitored most years since 2001 (Protea farm) and the wetland section (Black Swamp) has been monitored opportunistically after baseline sampling in 2003 and 2004 (Hammer 2004). Low to moderate numbers of southern pygmy perch were recorded at the Protea farm up until 2007, when the site dried due to critical water shortage (and the site has not been monitored since). The terminal wetland (Black Swamp) initially contained a diverse fish community but was also severely impacted by low Lake Alexandrina levels during the drought, such that only one southern pygmy perch was recorded in 2007 (no Yarra pygmy perch) and the site subsequently dried. Surface water was restored to this reach at the beginning of the present reporting period (2010) but water quality was initially poor (EC, 11,340 µScm-1; DO, 0.7mgL-1). Despite, water depth increasing and water quality improving (EC, 1452µScm-1; DO, 7.11mgL-1 in 2012), submerged aquatic habitat has not returned. A relatively diverse fish community, albeit in low abundance, has re-colonised the site but not southern pygmy perch or Yarra pygmy perch.

In spring 2008 and autumn 2009, at the height of the period of critical water shortage, a site just upstream of Winery Road was sampled as it represented the nearest section of permanent water to the dried Black Swamp site, recording southern pygmy perch and a single diadromous common galaxias (as well as river blackfish and mountain galaxias), albeit with massive seasonal fluctuations in abundance (Figure 3-87). Over the reporting period, annual fluctuations of a similar magnitude have been observed, with no southern pygmy perch recorded in 2010 or 2013 (and only 2 fish in 2012), but high abundance of the species (but no sign of recent recruitment) were observed in 2011. Similarly low and variable numbers of other species (such as mountain galaxias and river blackfish) have been observed over the present reporting period. These patterns may reflect a decline in habitat quality resulting from reduced flow, but dense emergent vegetation occurring at the site also makes sampling difficult. This reach is in much better condition than at the preceding assessment period (2009) largely due to the surface water.

199

State of fish communities across the EMLR, 2010 to 2013

12 11 2009 n=0 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90

12 11 2010, n=0 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90

12 11 2011, n=50 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90 12 11 2012, n=2 10 9 8 7 6 5

Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90

12 11 2013, n=0 10 9 8 7 6 5 Frequency 4 3 2 1 0 0 10 20 30 40 50 60 70 80 90

Total length (mm)

Figure 3-87. Length-frequency distribution for southern pygmy perch in Tookayerta Creek (us Winery Road), Tookayerta Catchment (Reach 9) between 2009 and 2013 (graphs below the dotted line denote the current reporting period).

200

State of fish communities across the EMLR, 2010 to 2013

Overall performance report

The catchment was in MODERATE condition over the period of critical water shortage (as assessed at the end of the 2009 reporting period), with strong populations of three threatened species occurring at two mid pool-riffle sites (Fleurieu Swamps (reach 3 & 4) was performing poorly) and the terminal wetland (reach 8) dry (Figure 3-88). Over the present reporting period, ecological assets performing well in 2009 declined whereas there was improvement in those performing poorly in 2009. Positives for the catchment included the continued performance of ecological assets in reach 5 and the partial recovery of the terminal wetland (although Yarra pygmy perch remain absent). Overall, the catchment was again classified as being in MODERATE condition the end of the present reporting period (Table 3-30).

9 Reach types

8 Headwaters Upper 7 Mid 6 Gorge Lowland 5 Wetlands

3 2

of 9) (out score Condition 1

0 2009 2010 2011 2012 2013

Year

Figure 3-88. Trend in condition score across reach types of the Tookayerta Catchment between 2009 and 2013. Scores for each reach type reflect the median score for all ecological assets present in that reach type (reach types that were not sampled are not presented).

201

State of fish communities across the EMLR, 2010 to 2013

Table 3-30. 2013 report card for the Tookayerta Catchment – a comparison of the performance against fish indicators (blacked out indicators are not relevant to that ecological asset). For each fish indicator, a tick ( ) represents a positive result (e.g. for present, a 2 & 3 for recruitment and survivorship indicators and a score > 4 for diverse fish community), and for all other results a cross ( ) shown. For alien species, ticks indicate the desirable result was observed (i.e. <30% of total site numbers) and crosses indicate a negative result (i.e. >30 of total site numbers). Condition scores for each ecological asset (out of 9) reflect the sum for each indicator (out of 7) plus an alien species score (out of 2). The median of scores for all ecological assets are used to estimate the overall catchment score. For ecological assets and overall catchment score are defined as good (>6, xxx), moderate (3 to 6, xxx) and poor (<3, xxx). See section 2.6 for full explanations ASSESSMENT for 2013 INDICATOR

Relevant site

Condition Alien species Reach score ECOLOGICAL ASSET Presence Recruitment Survivorship

Reach 3 & 4 – Upper catchment & Swampy Creek spring fed Fleurieu Swamps Southern pygmy perch 0 0 0 0 Brawley Swamp 0 0.0 Mountain galaxias 0 0 0 0 Reach 5 – Spring fed pool/riffle sequence (Nangkita Creek) River blackfish 1 2 2 5 us Willowburn Rd Southern pygmy perch 1 3 2 6 2 7.0 Mountain galaxias 1 1 2 4 Reach 6 – Perennial (spring influence) high flow pool-riffle sequence River blackfish 1 0 0 1 Compass Cabins Southern pygmy perch 0 0 0 0 2 3.0 Mountain galaxias 1 1 0 2 Reach 7 – Lowland pool and swamp sequence (potentially under spring influence) River blackfish 0 3 1 4 Deep Creek crossing 2 Southern pygmy perch 1 0 0 1 River blackfish 0 0 0 0 3.0 us Winery Rd (Railway) Southern pygmy perch 0 0 0 0 2 Mountain galaxias 1 1 0 2 Reach 8 – Black swamp and terminal wetland under Lake Alexandrina influence Yarra pygmy perch 0 0 0 0 Black Swamp 2 3.5 Diverse fish community 3 3

Median 3.0

202

State of fish communities across the EMLR, 2010 to 2013

Section 4. DISCUSSION

The EMLR is distinguished by being a region comprising of altered temporary streams capable of maintaining a diverse fish community (Whiterod et al. in review). The long history of water abstraction and altered stream flow has not been without impact, and has contributed to declines in the distribution and abundance of many native freshwater fish (Hammer 2004; Hammer et al. 2009). Yet, 33 freshwater fish species occur in the region, which is greater than nearby regions (Whiterod et al. in review). The impacts of water abstraction were exacerbated by the millennium drought and critical water shortages were experienced across the region between 2007 and 2010 (van Dijk et al. 2013). Regular condition assessment (Hammer 2007c; Hammer 2009) and the review of long-term fish data (Whiterod et al. in review) documented the decline and loss of fish-related ecological assets during the period of critical water shortage, despite wide ranging management actions being undertaken in an attempt to avoid expiration (Hammer et al. 2013). Over 2010 and 2011, high and unseasonal rainfall ended the millennium drought, lead to increased EMLR stream flow and restored water levels in the Lower Lakes and terminal wetlands. It was hoped that those improved conditions would aid the recovery of stressed native fish populations across the region.

4.1 Catchment and reach trends

The long-term review of Whiterod et al. (in review) highlighted a mixed recovery of the native fish community across the region after the end of the millennium drought, with recovery varying between species and functional groups and between reaches. The status reporting presented in Section 3 provides complimentary assessment by detailing trends in the status of all identified fish-related ecological assets between the last reporting period (2009) and now (2013), which are summarised for catchment and reaches in Table 4-1. This comparison revealed the majority of catchments (six of ten) are now performing better than at the height of the period of critical water shortage, which is unsurprising, except to say that a greater degree of recovery may have reasonably been expected. Alarmingly, the Finniss and Inman catchments as well as the Tookayerta catchment were deemed to have all declined in condition despite the expectation of improvements. These patterns may reflect limited source populations to facilitate recovery given the extent of decline experienced during the millennium drought, most obviously realised by the expiration of populations and species (e.g. Yarra pygmy perch from terminal wetland of Finniss Catchment) from the region. In support of this observation, the assessed catchments were considered to be in either poor or moderate condition,

203

State of fish communities across the EMLR, 2010 to 2013 with no catchments deemed to be in good condition, at the end of the present reporting period. Thus, overall the EMLR was assessed as being in moderate condition at the end of the present reporting period. It is likely that further recovery will be required to increase site and population resilience to cope with future periods of drought.

Table 4-1. 2013 overall status of reaches and catchments of the EMLR – a comparison of the reach and catchment level performance against fish indicators between 2009 and 2013. Condition scores (out of 9) are defined as good (>6, xxx), moderate (3 to 6, xxx) and poor (<3, xxx). Reaches are headwaters (HW), upper pool-riffle (UC), mid pool-riffle (MC), gorge (GO), lowland (LO) and terminal wetlands (TW) with reaches not sampled highlighted (with n/s). See section 2.6 for full explanations. Condition Reach Overall No Catchment HW UC MC GO LO TW 2013 2009 1 Angas n/s 8.5 4.5 n/s 5.0 1.5 4.8 4.0 2 Bremer n/s 1.0 n/s n/s 3.0 3.0 3.0 1.0 3 Currency n/s 3.0 7.0 n/s 3.5 3.5 3.5 3.5 4 Finniss n/s 8.5 3.8 n/s 1.0 3.0 4.0 4.3 5 Inman n/s n/s 3.5 n/s n/s n/s 3.5 6.0 6 Marne n/s 7.5 0.0 0.0 2.0 n/s 1.0 0.0 7 Reedy n/s n/s 3.5 4.5 2.0 n/s 3.5 2.5 8 Salt, Premimma & Rocky Gully n/s n/s n/s n/s n/s 1.0 1.0 2.5 9 Saunders n/s n/s n/s n/s 2.0 n/s 2.0 0.0 10 Tookayerta n/s n/s 3.0 n/s 3.0 3.5 3.0 4.0

2013 n/s 7.5 3.5 2.3 2.5 3.0 3.3 2009 n/s 3.0 4.3 1.6 3.8 0.5 3.0

Whiterod et al. (in review) emphasised that spatial patterns across the EMLR were best described at the reach scale. As such, we have provided a summary of status reporting by reach (Table 4-1). In 2009, all reach types were considered to be in poor or moderate condition, but only upper pool-riffle and gorge reaches as well as the terminal wetlands showed improvement over the present reporting period. Upper pool-riffle and gorge reaches, which suffered extensive drying of the period of critical water shortage benefited greatly from improved stream flow to the point they were considered to be in good condition as of 2013. This improvement largely reflected the ability of mountain galaxias to persist in refuge pools that remained during the critical water shortage period and then readily recolonise and recruit, taking advantage of greater connectivity and pool condition.

The terminal wetlands were impacted the greatest due to the broader impacts of critical water

204

State of fish communities across the EMLR, 2010 to 2013 shortage with many drying by 2009 (e.g. Marne, Finniss, Currency, Bremer, Angas). Not surprisingly, improved water availability and inundation of these terminal wetlands led to the return of diverse fish communities (namely diadromous species and freshwater generalists) and contributed a marked increase in condition. However, freshwater specialists (e.g. Yarra pygmy perch, southern pygmy perch) have not responded favourably, despite reintroductions (Bice et al. 2013) and appear to have been permanently lost during the period of critical water shortage

Over the last reporting period, the performance of the mid-catchment reach was mixed, with some retaining key refuges and populations for future recovery (e.g. Angas River, Currency Creek, Reedy Creek), but others observing critical declines in restricted populations (e.g. southern pygmy perch in the Finniss River). This reach type performed worse over the present reporting period, but was still considered to be in only moderate condition. During the period of critical water shortage, the lowland reaches were impacted by reduced water availability, but did not recover during the present reporting period despite improved flows and re-inundation of downstream terminal wetlands. The performance of these reach types is of considerable concern and must be a focus of conservation and management over the following years.

4.2 Fish monitoring recommendations

To best detect change and performance of fish related EWR indicators under declining, stable or improving scenarios, long-term investigations are required and the continuation of the current spread of sites recommended (Hammer 2007c). Whiterod et al. (in review) highlighted the value of long-term datasets (2001−2013) to explore spatial patterns and temporal trends across periods of hydrologic change across and within the EMLR. Expansion of the EMLR fish monitoring program, and a committed to annual monitoring since 2007, now ensures that temporally replicated data is available for 50−60 ongoing sites that allow region-wide assessment of the condition and performance of different stream catchments and reach types across the region. The focus on annual autumn sampling remains appropriate to detect survivorship and, importantly, recruitment of native fish populations. It is critical that the EMLR fish monitoring program continue to detect future changes in flow regimes and ecosystem impacts across the region, associated with climate change (Morrongiello et al. 2011), ongoing water abstraction, or indeed in response to management actions through EWRs associated with the EMLR WAP (SAMDBNRM Board 2013). As was highlighted during the period of critical water shortage, fine scale temporal monitoring for ecological assets under threat will remain necessary during periods of reduced flow to allow

205

State of fish communities across the EMLR, 2010 to 2013 appropriate response to critical thresholds (see Hammer et al. 2013). Additionally, Whiterod et al. (in review) highlighted the deficiency of sampling associated with the headwaters of the EMLR and we recommend that a targeted inventory is conducted in this reach type (cf Hammer 2004).

In summary, it is recommended that the following complementary actions be undertaken:

 EMLR fish monitoring program – continuation of annual autumn monitoring;  Fine-scale sampling (as required) – specific investigation of ecological assets under threat;  Targeted headwater inventory – specific sampling in this reach type.

4.3 Reporting process & links with EWRs

The previously developed reporting process for fish-related ecological assets in the EMLR (Hammer 2007c; Hammer 2009) was refined during the present project. The aim was to define rules to guide a more objective assessment of condition. While this approach is robust, it may benefit from further refinement in the future. Ultimately, condition assessments would be linked more closely to the flow regime that prevailed (e.g. flow metrics) over the reporting period; however, despite advances in the understanding of empirical relationships between fish responses and flow metrics (but see Whiterod et al. in prep), this level of sensitivity analysis is some way off.

206

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Adams M, Raadik TA, Burridge CP, Georges A (2014). Global biodiversity assessment and hyper- cryptic species complexes: more than one species of elephant in the room? Systematic Biology 63, 518-533. Arthington AH, Bunn SE, Poff NL, Naiman RJ (2006). The challenge of providing environmental flow rules to sustain river ecosystems. Ecological Applications 16, 1311-1318. Bertozzi T, Adams M, Walker KF (2000). Species boundaries in carp gudgeons (Eleotrididae: Hypseleotris) from the River Murray, South Australia: evidence for multiple species and extensive hybridization. Marine and Freshwater Research 51, 805-815. Bice C, Hammer M, Leigh S, Zampatti B (2010). 'Fish monitoring for the 'Drought Action Plan for South Australian Murray-Darling Basin threatened freshwater fish populations: summary for 2009/10.' SARDI Aquatic Sciences, Adelaide. Bice C, Hammer M, Leigh S, Zampatti B (2011). 'Fish monitoring for the 'Drought Action Plan for South Australian Murray-Darling Basin threatened freshwater fish populations: summary for 2010/11.' SARDI Aquatic Sciences, Adelaide. Bice C, Hammer M, Wilson P, Zampatti B (2009). 'Fish monitoring for the 'Drought Action Plan for South Australian Murray-Darling Basin threatened freshwater fish populations. SARDI Publication No. F2009/000451-1.' SARDI Aquatic Sciences, Adelaide. Bice C, Whiterod N, Wilson P, Zampatti B, Hammer M (2013). 'The Critical Fish Habitat Project: reintroductions of threatened fish species in the Coorong, Lower Lakes and Murray Mouth region 2011-2013.' SARDI Aquatic Sciences, Adelaide. Bice C, Whiterod N, Zampatti B (2014). 'The Critical Fish Habitat Project: assessment of the success of reintroductions of threatened fish species in the Coorong, Lower Lakes and Murray Mouth region 2011-2014.' SARDI Aquatic Sciences, Adelaide. Bunn SE, Arthington AH (2002). Basic principles and ecological consequences of altered flow regimes for aquatic biodiversity. Environmental Management 30, 492-507. CSIRO (2007). 'Water availability in the Eastern Mount Lofty Ranges.' Report to the Australian Government from the CSIRO Murray-Darling Basin Sustainable Yields Project. CSIRO, Australia. Hammer M (2001). Molecular systematics and conservation biology of the southern pygmy perch Nannoperca australis (Günther, 1861) (Teleostei: Percichthyidae) in south-eastern Australia. B. Sc. (Honours) thesis, Adelaide University. Hammer M (2002). 'Environmental water requirements for freshwater fishes of the Marne River Catchment, South Australia.' Report produced for the River Murray Catchment Water Management Board, Adelaide. Hammer M (2004). 'Eastern Mount Lofty Fish Inventory: distribution and conservation of freshwater fishes of tributaries to the Lower River Murray, South Australia.' Native Fish Australia (SA) Inc & River Murray Catchment Water Management Board, Adelaide. Hammer M (2005). 'Recovery monitoring for the southern pygmy perch in the Mount Lofty Ranges South Australia, 2001-2005 review.' Native Fish Australia (SA) Inc., Adelaide. Hammer M (2006a). 'Report on stage one of the Southern Fleurieu fish inventory. Report to Department of Water Land and Biodiversity Conservation.' Native Fish Australia Inc. and Aquasave, Adelaide.

State of fish communities across the EMLR, 2010 to 2013

Hammer M (2006b). 'Review and 2005 performance of fish indicators for Environmental Water Requirements of the Marne River Catchment, South Australia. Report to SAMDB NRM Board.' Aquasave Consultants, Adelaide. Hammer M (2006c). 'Review of monitoring data for river blackfish in the Eastern Mount Lofty Ranges, South Australia: 2002-2006. Report to the South Australian Murray-Darling Basin Natural Resources Management Board.' Aquasave Consultants, Adelaide. Hammer M (2007a). 'Data summary and 2006 performance of fish indicators for Environmental Water Requirements of the Marne River Catchment, South Australia.' Aquasave Consultants, Adelaide. Hammer M (2007b). 'Distribution, status and urgent conservation measures for Yarra Pygmy Perch in the Murray-Darling Basin. Report to Department for Environment and Heritage, South Australian Government.' Aquasave Consultants, Adelaide. Hammer M (2007c). 'Freshwater fish monitoring for threatened species and environmental water requirements in the Eastern Mount Lofty Ranges. Report to the SA Murray-Darling Basin NRM Board.' Aquasave Consultants, Adelaide. Hammer M (2007d). 'A preliminary population model for Mountain Galaxias in the Eastern Mount Lofty Ranges, South Australia based on 2002-2006 monitoring data.' Aquasave Consultants, Adelaide. Hammer M (2009). 'Freshwater fish monitoring in the Eastern Mount Lofty Ranges: environmental water requirements and tributary condition reporting for 2008 and 2009. Report to the SAMDB NRM Board.' Aquasave Consultants, Adelaide. Hammer M (2010). 'Report on in situ conservation activities at Rodwell Creek for 2009-2010.' Report to Department of Environment and Natural Resources (DENR). Aquasave Consultants, Adelaide. Hammer M, Wedderburn S, van Weenan J (2009). 'Action Plan for South Australian Freshwater Fishes.' Native Fish Australia (SA) Inc., Adelaide. Hammer MP, Adams M, Foster R (2012). Update to the catalogue of South Australian freshwater fishes (Petromyzontida & Actinopterygii). Zootaxa 3593, 59-74. Hammer MP, Bice CM, Hall A, Frears A, Watt A, Whiterod NS, Beheregaray LB, Harris JO, Zampatti B (2013). Freshwater fish conservation in the face of critical water shortages in the southern Murray–Darling Basin, Australia. Marine and Freshwater Research 64, 807-821. Kingsford RT, Walker KF, Lester RE, Young WJ, Fairweather PG, Sammut J, Geddes MC (2011). A Ramsar wetland in crisis - the Coorong, Lower Lakes and Murray Mouth, Australia. Marine and Freshwater Research 62, 255-265. Lintermans M (2013). A review of on-ground recovery actions for threatened freshwater fish in Australia. Marine and Freshwater Research 64, 775-791. Morrongiello JR, Beatty SJ, Bennett JC, Crook DA, Ikedife DN, Kennard MJ, Kerezsy A, Lintermans M, McNeil DG, Pusey BJ (2011). Climate change and its implications for Australia's freshwater fish. Marine and Freshwater Research 62, 1082-1098. Mosley LM, Corkhill E, Heneker TM, Hipsey MR, Skinner D, Aldridge KT (2012). The impact of extreme low flows on the water quality of the Lower Murray River and Lakes (South Australia). Water Resources Management 26, 3923-3946. Poff NE, Allan JD, Bain MB, Karr JR, Prestegaard KL, Richter BD, Sparks RE, Stromberg JC (1997). The natural flow regime: a paradigm for river conservation and restoration. BioScience 47, 769-784.

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Poff NL, Richter BD, Arthington AH, Bunn SE, Naiman RJ, Kendy E, Acreman M, Apse C, Bledsoe BP, Freeman MC (2010). The ecological limits of hydrologic alteration (ELOHA): a new framework for developing regional environmental flow standards. Freshwater Biology 55, 147-170. SAMDBNRM Board (2013). 'Water Allocation Plan for the Eastern Mount Lofty Ranges.' South Australian Murray-Darling Basin Natural Resource Management Board, Murray Bridge, Australia. Smith BB (2006). 'Final report on the 'fish' component of the 2005 River Murray Wetlands Baseline Survey.' SARDI Aquatic Sciences, Adelaide. van Dijk AIJM, Beck HE, Crosbie RS, Jeu RAM, Liu YY, Podger GM, Timbal B, Viney NR (2013). The Millennium Drought in southeast Australia (2001–2009): Natural and human causes and implications for water resources, ecosystems, economy, and society. Water Resources Research 49, 1040-1057. VanLaarhoven J, van der Wielen M (2009). 'Environmental water requirements for the Mount Lofty Ranges prescribed water resources areas.' Department of Water, Land and Biodiversity Conservation & South Australian Murray-Darling Basin Natural Resources Management Board, Adelaide. Walker KF, Sheldon F, Puckridge JT (1995). A perspective on dryland river ecosystems. Regulated Rivers: Research and Management 11, 85-104. Wedderburn S (2014). 'An Assessment of Threatened Fish Populations in Lake Alexandrina and Lake Albert, South Australia.' The University of Adelaide, Adelaide. Wedderburn S, Barnes T (2009). 'Condition monitoring of threatened fish species at Lake Alexandrina and Lake Albert (2008-2009). Report to the Murray-Darling Basin Authority and the South Australian Murray-Darling Basin Natural Resources Management Board.' The University of Adelaide, Adelaide. Wedderburn S, Barnes T (2011). 'Condition Monitoring of Threatened Fish Species at Lake Alexandrina and Lake Albert (2010-2011). Report to the Murray-Darling Basin Authority and the South Australian Department for Water.' The University of Adelaide, Adelaide. Wedderburn S, Barnes T (2012). 'Condition Monitoring of Threatened Fish Species at Lake Alexandrina and Lake Albert (2011-2012). Report to the Murray-Darling Basin Authority and the South Australian Department for Water.' The University of Adelaide, Adelaide. Wedderburn S, Barnes T (2013). 'Condition Monitoring of Threatened Fish Species at Lake Alexandrina and Lake Albert (2012-2013). Report to the Murray-Darling Basin Authority and the South Australian Department for Water.' The University of Adelaide, Adelaide. Wedderburn S, Barnes T (2014). 'Condition Monitoring of Threatened Fish Species at Lake Alexandrina and Lake Albert (2013-2014). Report to the Murray-Darling Basin Authority and the South Australian Department for Water.' The University of Adelaide, Adelaide. Wedderburn S, Hammer M (2003). 'The Lower Lakes Fish Inventory: distribution and conservation of freshwater fishes of the Ramsar Convention wetland at the terminus of the Murray-Darling Basin, South Australia.' Native Fish Australia (SA) Inc., Adelaide. Wedderburn S, Hillyard K (2010). 'Condition monitoring of threatened fish species at Lake Alexandrina and Lake Albert (2009-2010). Report to the Murray-Darling Basin Authority and the South Australian Murray-Darling Basin Natural Resources Management Board.' The University of Adelaide, Adelaide.

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Whiterod N (2014). 'Status of fish communities in the lower Mount Barker Creek.' A report for the Goolwa to Wellington Local Action Planning (GWLAP) Association. Aquasave - Nature Glenelg Trust, Goolwa Beach. Whiterod NS, Hammer MP, Vilizzi L (in prep). Linking the recruitment and survivorship of freshwater stream specialists to flow metrics and microhabitat in a Mediterranean-type region of temporary streams. Whiterod NS, Hammer MP, Vilizzi L (in review). Spatial and temporal variability in fish community structure across a Mediterranean-type region of temporary streams. Submitted to. Ecology of Freshwater Fish.

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