THE BASIN PLAN Water quality technical report for Macquarie Castlereagh surface water resource plan area (SW11)

NSW Department of Planning, Industry and Environment / dpie.nsw.gov.au

Published by NSW Department of Planning, Industry and Environment dpie.nsw.gov.au Title: Water quality technical report for Macquarie Castlereagh surface water resource plan area (SW11)

First published: February 2020

Department reference number: INT17/243328 Acknowledgments

The soils maps in this report contain data sourced from the NSW Office of Environment and Heritage.

© State of New South Wales through Department of Planning, Industry and Environment [2020]. You may copy, distribute, display, download and otherwise freely deal with this publication for any purpose, provided that you attribute the Department of Planning, Industry and Environment as the owner. However, you must obtain permission if you wish to charge others for access to the publication (other than at cost); include the publication in advertising or a product for sale; modify the publication; or republish the publication on a website. You may freely link to the publication on a departmental website. Disclaimer: The information contained in this publication is based on knowledge and understanding at the time of writing (October 2018) and may not be accurate, current or complete. The State of New South Wales (including the NSW Department of Planning, Industry and Environment), the author and the publisher take no responsibility, and will accept no liability, for the accuracy, currency, reliability or correctness of any information included in the document (including material provided by third parties). Readers should make their own inquiries and rely on their own advice when making decisions related to material contained in this publication.

Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Summary Good quality water protects public health, supports economic production and maintains a healthy river ecosystem. Water quality is largely determined by land use, geology, climate, riparian vegetation and stream flow, and reflects the interactions of natural and man-made practices that occur in a drainage area and the riparian zone. Degradation of water quality can put stress on a range of aquatic organisms, impinge on Aboriginal cultural and spiritual uses of water, increase the cost of drinking water treatment, contribute to public health risks and decreases the suitability of water for irrigation and agriculture. Alteration of the Australian landscape since European settlement has resulted in marked changes in catchment conditions. Runoff from cropping areas, erosion of soil and nutrients from stream banks and discharge from saline areas can lead to increased turbidity, salinity, sedimentation, nutrient load and chemical residues which in turn can degrade aquatic ecosystem health. The regulation of rivers through the construction of large storages and weirs can lead to changes to flow regimes, cold water pollution, harmful algal blooms and disruption of longitudinal connectivity of river processes. Water quality condition in the Macquarie Castlereagh Water Resource Planning Area (WRPA) varies from poor to excellent. Water quality issues occurring within the catchment are the result of a combination of factors. These include alteration to natural flow regimes, in particular disruption by Windamere and Burrendong Dams, changes to catchment conditions and land use change. Table 1 summarises the major water quality issues in the Macquarie Castlereagh WRPA. Table 1: Summary of major issues and causes of water quality degradation

Issue Location Potential causes

Harmful algal uplands Stratification and warm water temperatures in Windamere, Burrendong and Ben blooms Chifley Dams, nutrient inputs to dams.

Dissolved oxygen uplands, Reduced flow and increased low flow and cease to flow periods disrupting and pH outside of midlands, dissolved oxygen dynamics and increasing eutrophication. normal ranges lowlands

Increased nutrients uplands, Stream bank and riparian condition, grazing and cropping practices, carp and and turbidity midlands, feral species. In the lowlands, increased sediment and nutrient input associated lowlands with erosion.

Toxicants and midlands, Pesticide use in cropping areas. pesticides lowlands

Disruption to midlands, Reduced freshes and high flows, disruption of longitudinal connectivity by organic carbon lowlands Windamere and Burrendong Dams. cycling

Thermal pollution midlands, Cold water released from Burrendong Dam in summer and Windamere Dam during bulk water transfers.

NSW Department of Planning, Industry and Environment | INT17/243328 | i Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Contents Summary ...... i Contents ...... ii List of tables ...... iv List of figures...... v 1. Introduction ...... 1 1.1. Purpose...... 1 1.2. Context...... 2 1.3. Catchment description ...... 3 1.4. Water quality targets ...... 4 1.4.1. Assessment using Basin Plan water quality targets ...... 5 1.4.2. Water quality targets for water-dependent ecosystems ...... 5 1.4.3. Water quality targets for raw water for treatment for human consumption ...... 6 1.4.4. Water quality targets for irrigation water ...... 6 1.4.5. Water quality targets for recreational water ...... 7 1.4.6. Salinity targets for the purposes of long-term salinity planning and management ...... 7 2. Water quality parameters ...... 8 2.1. Turbidity and suspended sediment ...... 8 2.2. Nutrients ...... 9 2.3. Dissolved oxygen ...... 9 2.4. pH ...... 10 2.5. Water temperature and thermal pollution ...... 10 2.6. Salinity ...... 11 2.7. Harmful algal blooms ...... 12 2.8. Toxicants ...... 13 2.9. Pathogens ...... 13 3. Water access rules and flow management in the Macquarie Castlereagh WRPA ...... 14 4. Methods ...... 16 4.1. Site selection and monitoring ...... 16 4.2. Water quality index (WaQI) ...... 18 4.3. Catchment stressor identification ...... 19 4.3.1. Conceptual mapping ...... 20 4.3.2. Literature review ...... 20 4.3.3. Summary statistics ...... 20 4.3.4. Data analysis ...... 20 4.3.5. Spatial and GIS ...... 20 4.3.6. Local and expert knowledge ...... 20

NSW Department of Planning, Industry and Environment | INT17/243328 | ii Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

4.4. Macquarie Castlereagh WRPA Risk Assessment ...... 20 5. Results ...... 22 5.1. Water quality index (WaQI) ...... 22 5.1.1. Water-dependent ecosystems ...... 22 5.1.2. Water temperature ...... 23 5.1.3. Irrigation ...... 26 5.1.4. Recreation ...... 27 5.2. Literature review ...... 29 5.3. Summary statistics ...... 30 5.3.1. Total annual flow ...... 33 5.4. Local and expert knowledge ...... 33 5.5. Risk assessment...... 34 6. Discussion...... 36 6.1. Elevated levels of salinity ...... 36 6.2. Elevated levels of suspended matter...... 38 6.3. Elevated levels of nutrients ...... 40 6.4. Elevated levels of cyanobacteria...... 41 6.5. Water temperature outside natural ranges ...... 42 6.6. Dissolved oxygen outside natural ranges ...... 43 6.7. Elevated levels of pesticides and other contaminants ...... 43 6.8. pH outside natural ranges ...... 44 6.9. Elevated pathogen counts ...... 44 6.10. Knowledge gaps ...... 45 7. Conclusion ...... 46 References ...... 48 Appendix A. Water quality monitoring site locations ...... 55 Appendix B. Water quality index (WaQI) method...... 57 Appendix C. Literature Review ...... 59 Appendix D. Water quality summary statistics ...... 64 Appendix E. Draftsman plots and Box plots by site ...... 71 Fish River at Hazelgrove ...... 72 Turon River at Bathurst Point...... 74 Macquarie River at Bruinbun ...... 76 Cudgegong River at Rylstone Bridge ...... 78 Cudgegong River at Yamble Bridge ...... 80 Macquarie River downstream Burrendong Dam ...... 82 Bell River at Newrea ...... 84

NSW Department of Planning, Industry and Environment | INT17/243328 | iii Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Little River at Arthurville ...... 86 Macquarie River at Molong Rail Bridge ...... 88 Talbragar River at Elong Elong ...... 90 Castlereagh River at Mendooran ...... 92 Macquarie River at Warren Weir ...... 94 Marthaguy River at Carinda ...... 96 Macquarie River at Bells Bridge ...... 98 Bogan River at Gongolgon ...... 100 Appendix F. Local and expert knowledge meetings ...... 102

List of tables Table 1: Summary of major issues and causes of water quality degradation ...... i Table 2: Water quality processes ...... 3 Table 3: Water quality targets for water dependent ecosystems objective for all aquatic ecosystems ...... 5 Table 4: Salinity targets for irrigation water ...... 6 Table 5: Blue-green algae targets for recreational water...... 7 Table 6: Salinity targets for purposes of long term salinity planning in the Macquarie Castlereagh WRPA ...... 7 Table 7: List of routine water quality monitoring stations in the Macquarie Castlereagh WRPA ...... 16 Table 8: List of continuous electrical conductivity monitoring stations in the Macquarie Castlereagh WRPA ... 17 Table 9: List of continuous water temperature monitoring stations in the Macquarie Cudgegong WRPA...... 17 Table 10: Water quality index scores for the Macquarie Castlereagh WRPA 2010-2015 water quality data .... 22 Table 11: Water quality index scores and 95th percentile results for the Macquarie Castlereagh WRPA 2005- 2015 continuous electrical conductivity data ...... 26 Table 12: Sites with high and medium risk to the health of water dependent ecosystems from turbidity ...... 35 Table 13: Sites with high and medium risk to the health of water dependent ecosystems from total phosphorus ...... 35 Table 14: Sites with high and medium risk to the health of water dependent ecosystems from total nitrogen .. 35 Table 15: Sites with high and medium risk to the health of water dependent ecosystems from pH ...... 36 Table 16: Sites with high and medium risk to the health of water dependent ecosystems from dissolved oxygen ...... 36 Table 17: Location of water quality monitoring stations in the Macquarie Castlereagh WRPA ...... 55 Table 18: Review of published literature ...... 59 Table 19: Water quality summary statistics for the Macquarie Castlereagh WRPA 2007-2015 water quality data ...... 64 Table 20: Bogan River at Gongolgon electrical conductivity for purposes of long term salinity planning in the Macquarie Castlereagh WRPA...... 69

NSW Department of Planning, Industry and Environment | INT17/243328 | iv Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Table 21: Castlereagh River at Gungalman electrical conductivity for purposes of long term salinity planning in the Macquarie Castlereagh WRPA ...... 69 Table 22: Macquarie River at Bells Bridge electrical conductivity for purposes of long term salinity planning in the Macquarie Castlereagh WRPA ...... 70 Table 23: Comparison of annual salt loads in the Macquarie Castlereagh WRPA ...... 70 Table 24: Meetings held to develop the Macquarie Castlereagh water quality status and issue report ...... 102

List of figures Figure 1: Flow diagram illustrating the components of the Macquarie Castlereagh surface water resource plan ...... 2 Figure 2: Water quality zones and monitoring sites for the Macquarie Castlereagh WRPA...... 4 Figure 3: Continuous water temperature monitoring sites in the upper Macquarie Castlereagh WRPA ...... 18 Figure 4: Conceptual diagram of the CSI process ...... 19 Figure 5: Macquarie Castlereagh WRPA water quality index scores ...... 23 Figure 6: Water temperature in the Cudgegong River downstream of Windemere Dam compared to estimated 20th and 80th percentile of natural temperature ...... 24 Figure 7: Minimum daily water temperature in the Cudgegong River against mean daily flow downstream of Windamere Dam from 2000 to 2016 ...... 24 Figure 8: Water temperature in the Macquarie River downstream of Burrendong Dam compared to estimated 20th and 80th percentile of natural temperature ...... 25 Figure 9: Minimum daily water temperature in the Macquarie River downstream of Burrendong Dam from 2010 to 2016 ...... 26 Figure 10: Mean daily electrical conductivity (µS/cm) in the Macquarie River at Baroona from 2005 to 2015 .. 27 Figure 11: Potentially toxic cyanobacteria biovolume in Windamere Dam 2010 to 2014 ...... 28 Figure 12: Potentially toxic cyanobacteria biovolume in Burrendong Dam 2010 to 2015 ...... 28 Figure 13: Water quality data for water quality parameters by site ...... 32 Figure 14: Annual flow (ML/year) at selected gauging stations...... 33 Figure 15: River styles recovery potential in the Macquarie Castlereagh WRPA ...... 39 Figure 16: Soil total nitrogen (0 to 5 cm) for the Macquarie Castlereagh WRPA ...... 40 Figure 17: Soil total phosphorus (0-5 cm) for the Macquarie Castlereagh WRPA...... 41 Figure 18: Soil pH (0 to 5 cm) for the Macquarie Castlereagh WRPA ...... 44 Figure 19: Draftsman plots for Fish River at Hazelgrove ...... 72 Figure 20: Water quality data for Fish River at Hazelgrove ...... 73 Figure 21: Draftsman plots for Turon River at Bathurst Point ...... 74 Figure 22: Water quality data for Turon River at Bathurst Point...... 75 Figure 23: Draftsman plots for Macquarie River at Bruinbun ...... 76 Figure 24: Water quality data for Macquarie River at Bruinbun ...... 77

NSW Department of Planning, Industry and Environment | INT17/243328 | v Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Figure 25 : Draftsman plots for Cudgegong River at Rylstone Bridge ...... 78 Figure 26 : Water quality data for Cudgegong River at Rylstone Bridge ...... 79 Figure 27 : Draftsman plots for Cudgegong River at Yamble Bridge...... 80 Figure 28 : Water quality data for Cudgegong River at Yamble Bridge ...... 81 Figure 29 : Draftsman plots for Macquarie River downstream Burrendong Dam ...... 82 Figure 30 : Water quality data for Macquarie River downstream Burrendong Dam ...... 83 Figure 31 : Draftsman plots for Bell River at Newrea ...... 84 Figure 32 : Water quality data for Bell River at Newrea ...... 85 Figure 33 : Draftsman plots for Little River at Arthurville ...... 86 Figure 34 : Water quality data for Little River at Arthurville...... 87 Figure 35 : Draftsman plots for Macquarie River at Molong Rail Bridge ...... 88 Figure 36 : Water quality data for Macquarie River at Molong Rail Bridge ...... 89 Figure 37 : Draftsman plots for Talbragar River at Elong Elong...... 90 Figure 38 : Water quality data for Talbragar River at Elong Elong ...... 91 Figure 39 : Draftsman plots for Castlereagh River at Mendooran ...... 92 Figure 40 : Water Quality data for the Castlereagh River at Mendooran ...... 93 Figure 41 : Draftsman plots for Macquarie River at Warren Weir ...... 94 Figure 42 : Water quality data for Macquarie River at Warren Weir ...... 95 Figure 43 : Draftsman plots for Marthaguy River at Carinda ...... 96 Figure 44 : Water quality data for Marthaguy River at Carinda ...... 97 Figure 45 : Draftsman plots for Macquarie River at Bells Bridge ...... 98 Figure 46 : Water quality data for Macquarie River at Bells Bridge ...... 99 Figure 47 : Draftsman plots for Bogan River at Gongolgon ...... 100 Figure 48 : Water quality data for Bogan River at Gongolgon ...... 101

NSW Department of Planning, Industry and Environment | INT17/243328 | vi Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

1. Introduction 1.1. Purpose The Murray Darling Basin Plan (2012) is an instrument of the Commonwealth Water Act (2007). It provides the framework for long term integrated management of water resources of the Murray Darling Basin. The Basin Plan requires water quality management plans (WQMP) are developed for all water resource areas in the Basin. Each WQMP will;  Establish water quality objectives and targets for freshwater dependent ecosystems, irrigation water and recreational purposes;  Identify key causes of water quality degradation;  Assess risks arising from water quality degradation, and  Identify measures that contribute to achieving water quality objectives. This report provides an overview of the water quality condition of the Macquarie Castlereagh water resource plan area (WRPA) by comparing data to the Basin Plan water quality targets (Basin Plan 2012, Schedule 11). The Basin Plan water quality targets set out the appropriate water quality required for environmental, social, cultural and economic benefits in the Murray Darling Basin. Monitoring progress towards achieving the targets will identify trends and inform actions that address the causes of water quality decline. These targets have been used to assess existing water quality data, and to identify areas of risk to aquatic ecosystems, recreational and irrigation use. The report also outlines the factors influencing water quality in the region, specifically the likely causes of water quality degradation issues, as required by Chapter 10, Section 10.30 of the Basin Plan.

BASIN PLAN 10.30 Water quality management plan to identify key causes of water quality degradation. The water quality management plan must identify the causes or likely causes, of water quality degradation in the water resource plan area having regard to the key causes of water quality degradation identified in Part 2 of Chapter 9 and set out in Schedule 10.

The information in this report supports the development of the Macquarie Castlereagh WQMP. It provides the background and technical information to develop water, land and vegetation management measures to maintain or improve water quality in the Macquarie Castlereagh WRPA. Figure 1 is a flow diagram illustrating how this report supports other components of the surface water resource planning process.

NSW Department of Planning, Industry and Environment | INT17/243328 | 1 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Water Resource Plan

Resource Description Description of water resource plan area to provide an understanding of the region and its resources

Risk assessment Status and issues paper Identifies risks of not achieving Basin Plan Summarises the current condition of water environmental, social and economic outcomes resources and issues to consider when and proposes strategies for mitigation developing the Water Resource Plan

Land and Long Term Vegetation Watering Plan Management Salinity Technical Water Quality Technical Report Report Primary Develop, Issues Technical information and analysis Technical information and analysis mechanism implement and Assessment to develop water and land to develop water and land outlining evaluate best Report management measures that management measures that watering practice land protect or improve salinity. protect or improve water quality requirements and vegetation for key management environmental practices to assets. increase Guides the productivity use of and Water Sharing Plan environmental sustainability Water Quality Management Plan Describes water rights, compliance with water over a of riverine Provides a framework to protect, improve and sustainable diversion limits, water quality 20 year period landscapes restore water quality and salinity that is fit for management, environmental watering, and purpose risks to water resources meeting critical human needs

Incident Response Guide Describes how water resources will be managed during an extreme event

Monitoring Evaluation and Reporting Plan Monitoring the effectiveness of measures for the purpose of adaptive management and reports progress against requirements of Schedule 12 of the Basin Plan

Figure 1: Flow diagram illustrating the components of the Macquarie Castlereagh surface water resource plan

1.2. Context Water quality can be defined in terms of the physical, chemical and biological content of water and in terms of purpose and use. Water quality may be fit for one purpose, but not another. For example, water may be of good quality to irrigate crops, but may not support a healthy population of fish. This report refers to water quality degradation, or to poor water quality as:  Elevated levels of nutrients, turbidity, blue-green algae, salinity, toxicants or pathogens, and  Water temperature, pH and dissolved oxygen outside of certain ranges. Water quality is dynamic. The physical, chemical and biological content of water varies with time and location. Table 2 shows how water quality can be defined in three related, but slightly different ways.

NSW Department of Planning, Industry and Environment | INT17/243328 | 2 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Table 2: Water quality processes

Long term water quality Poor water quality event Ecosystem processes

This describes long-term These refer to occurrences of water Water quality parameters are bound up average trends over a period of quality issues for set periods of time in fundamental ecological functions of months to years. In this report, that are generally not ongoing. rivers and catchments. These are less the water quality parameters easy to define as ‘good’ or ‘bad’, and Examples may include a potentially used are from monthly often involve complex toxic algal bloom or anoxic measurements at a selection of interrelationships. blackwater (low-oxygen) event. locations. While the occurrence of these Examples may include the movement Major trends are reported in five events may be short lived, their of organic carbon from floodplains to year periods. Indicator targets effects can be long-term. rivers to support productivity, or the are listed in Tables 3 to 6. delivery of sediment from upstream to downstream.

1.3. Catchment description The Macquarie Castlereagh WRPA is flanked by the Namoi and Darling catchments to the north and west, the Lachlan catchment to the south and the Sydney/Shoalhaven Basin to the east. Major towns include Orange, Bathurst, Dubbo, Mudgee and Nyngan. The area comprises three major catchments; the Castlereagh, Bogan and Macquarie Rivers. The Castlereagh River is approximately 541 km in length and rises in rugged broken country in the Warrumbungle Range at an elevation of approximately 850 m. The Castlereagh River flows through Timor Dam on its way to joining the Macquarie River downstream of the Macquarie Marshes. The Macquarie River is formed by the joining of the Campbells and Fish Rivers, which drain a high plateau area centred near Oberon with a general elevation of 900 to 1000 m above sea level. The river flows northward through steep gorge country in the Hill End area and is impounded by Burrendong Dam upstream of Wellington. The Cudgegong River rises in the sandstone tableland country east of Rylstone, is impounded by Windamere Dam upstream of Mudgee, and then flows through Mudgee before flowing into Burrendong Dam. Downstream of Burrendong Dam, the Macquarie River continues to flow in a northwest direction through Wellington and Dubbo, and is joined by three major tributaries; the Talbragar, Bell and Little Rivers. At Narromine the Macquarie River takes a dramatic turn to the north and commences a complex system of anabranches and effluent creeks that connect the Macquarie, Darling and Bogan Rivers. The Macquarie Marshes are located toward the end of the catchment and comprise a meandering network of effluent channels and anabranches with shallow swamps, lagoons and floodplains. The Macquarie Marshes were listed as a wetland of international significance under the Ramsar Convention in 1986, and are significant habitat for colonial waterbirds and contain a wide range of vegetation types. The Macquarie River does emerge from the wetlands before joining the Castlereagh River and then flowing into the Barwon River near Brewarrina. The Bogan River rises in the Harvey Ranges between Parkes and Peak Hill and flows northwest through a broad, flat landscape through Nyngan to join the Darling River near Bourke. Major effluent streams of the lower valley include the Albert Priest Canal (artificial), and Gunningbar and Duck Creeks, which deliver regulated flows from the Macquarie River to the lower Bogan River. Land use in the Macquarie Castlereagh WRPA is largely grazing in the upper catchment with increased cultivation with distance down the catchment. A detailed description of climate, land and water usage and water regulation infrastructure can be found in the Macquarie Castlereagh surface water resource description report (DoIW 2018a).

NSW Department of Planning, Industry and Environment | INT17/243328 | 3 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

1.4. Water quality targets The Basin Plan water quality targets set out the appropriate water quality required for environmental, social, cultural and economic benefits in the Murray Darling Basin. Monitoring progress towards achieving the targets will identify trends and inform actions that address the causes of water quality decline. The Basin Plan identifies water quality “target application zones” approximating lowland, upland and montane areas of the major river valleys. Lowland areas have an altitude of less than 200 m, upland areas fall between 200 and 700 m and montane areas have an altitude greater than 700 m. The boundaries of these zones are shown in Figure 2. Two water-dependent ecosystems are described in the Basin Plan; Declared Ramsar wetlands (streams and rivers; lakes and wetlands) and Other water-dependent ecosystems (streams, rivers, lakes and wetlands). The assessment of water quality targets in this report is focused on Other water-dependent ecosystems, as there are no water quality monitoring sites located in the Ramsar listed wetlands in the Macquarie Marshes. A revision of the current water quality monitoring program is to be undertaken to fill identified information gaps. The Basin Plan water-dependent ecosystem targets for turbidity, total phosphorus, total nitrogen, dissolved oxygen and pH were developed following the methods outlined in the ANZECC Guidelines (2000). Water quality data for rivers and streams in ‘reference’ condition from each of the water quality zones were used to develop the target values for each zone (Tiller and Newall 2010). In zones where there were no reference sites, the appropriate default trigger value from the ANZECC Guidelines (2000) for slightly to moderately disturbed systems was used as the Basin Plan water quality target (Tiller and Newall 2010).

Figure 2: Water quality zones and monitoring sites for the Macquarie Castlereagh WRPA

NSW Department of Planning, Industry and Environment | INT17/243328 | 4 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

1.4.1. Assessment using Basin Plan water quality targets The ANZECC Guidelines (2000) are currently under revision (Guideline Document 4: Australian and New Zealand Guidelines for Fresh and Marine Water Quality 2000) as part of the broader revision of the National Water Quality Management Strategy. It is anticipated that there will be no default trigger values in the revised guidelines for Basin States as it is expected that these states have developed regional water quality targets as part of other water planning processes. Basin States may choose to use the water quality targets of the Basin Plan in lieu of the default trigger values of the ANZECC Guidelines (2000) if local water quality guidelines are not available. Trigger values and management targets are conceptually different. A trigger value is a concentration below which there is a low risk of adverse effects, and if exceeded, indicates that some form of action should commence. Management targets are long term objectives used to assess whether an environmental value is being achieved or maintained. An assessment of Basin Plan water quality targets in NSW (Mawhinney and Muschal 2015) identified targets in some zones and zone boundaries as being inappropriate. Perceived poor water quality at a monitoring site may be in response to an inappropriate target, rather than excessive pollutants. In these cases, the Basin Plan targets should be revised in preference for location specific targets which consider local catchment conditions. It is anticipated the revision of the National Water Quality Management Strategy will improve the advice about comparing results from individual monitoring sites against water quality targets, with more emphasis on catchment assessments and flow-dependant trigger values. The Basin Plan allows an alternate target to be specified in the WQMP under certain conditions. It is expected that the recommendation to develop specific targets will also be retained in the revised National Water Quality Management Strategy. There will be further discussion of water quality targets in the Macquarie Castlereagh WQMP. 1.4.2. Water quality targets for water-dependent ecosystems The targets for water dependent ecosystems are to ensure water quality is sufficient to:  Protect and restore ecosystems,  Protect and restore ecosystem functions,  Ensure ecosystems are resilient to climate change, and  Maintain the ecological character of wetlands. Turbidity, total phosphorus and total nitrogen annual medians in the Macquarie Castlereagh WRPA should be below the target values listed in Table 3. For dissolved oxygen and pH the annual median should fall within the stated range. The toxicant targets are taken from the ANZECC water quality guidelines (2000) using the values for the protection of 95% or 99% of species. The 95% protection of species trigger values applies to typical, slightly to moderately disturbed systems. Table 3: Water quality targets for water dependent ecosystems objective for all aquatic ecosystems

Toxicants Dissolved (must not Total Total oxygen exceed Water Quality Ecosystem Turbidity pH Phosphorus Nitrogen (mg/L; or Temperature values in Salinity Zone Type (NTU) (µg/L) (µg/L) saturation 3.4.1 of the (%)) ANZECC guidelines)

Water dependent ecosystems (not including Ramsar sites)

B3 Streams, rivers, 20 35 600 >8mg/L or 7.0–8.0 between the the End of valley (Castlereagh lakes and 90-110% 20th and 80th protection of targets for Macquarie wetlands percentile of 95% of salinity in valleys, Upland natural monthly species Appendix 1 zone) water of Schedule temperature B to the A3 Streams, rivers, 35 50 600 >7.0 mg/L; 6.5–8.0 agreement (Castlereagh lakes and or Macquarie wetlands 80-110%

NSW Department of Planning, Industry and Environment | INT17/243328 | 5 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

valleys, Lowland zone)

Ramsar listed water dependent ecosystems

B3 Streams and 5 20 310 >8mg/L or 7.0–8.0 between the the End of valley (Castlereagh rivers 90-110% 20th and 80th protection of targets for Macquarie percentile of 99% of salinity in valleys, Upland Lakes and 20 10 350 90–110% 6.5–8.0 natural monthly species Appendix 1 zone) wetlands water of Schedule temperature B to the A3 Streams and 20 30 320 >7.0 mg/L; 6.5–8.0 agreement (Castlereagh rivers or Macquarie 80-110% valleys, Lowland zone) Lakes and 20 10 350 90-110% 6.5-8.0 wetlands 1.4.3. Water quality targets for raw water for treatment for human consumption The target is to minimise the risk that raw water taken to be treated for human consumption results in adverse human health effects. The Public Health Act 2010 and the Public Health Regulation (2012) require drinking water suppliers to develop and adhere to a Drinking Water Management System (DWMS). The DWMS addresses the elements of the Framework for Management of Drinking Water Quality (Australian Drinking Water Guidelines (NHMRC and NRMMC, 2011)) and is a requirement of water suppliers operating licence (NSW Ministry of Health 2013). Water providers in the Macquarie Castlereagh WRPA, include:

Bathurst Regional Council Lithgow City Council Bogan Shire Council Mid-Western Regional Council Cabonne Council Narromine Shire Council Cobar Shire Council Oberon Council Coonamble Shire Council Orange City Council Dubbo Regional Council Warren Shire Council Fish River Water Supply Warrumbungle Shire Council Gilgandra Shire Council 1.4.4. Water quality targets for irrigation water The aim of the agriculture and irrigation target is that the quality of surface water, when used in accordance with the best irrigation and crop management practices and principles of ecologically sustainable development, does not result in crop yield loss or soil degradation. The target is for the electrical conductivity 95th percentile of each 10 year period that ends at the end of the water accounting period, not exceed 957µS/cm. The target in Table 4 applies at sites where water is extracted by an irrigation infrastructure operator for the purpose of irrigation. In NSW, irrigation infrastructure operators are defined as a separate third party that holds a water access entitlement and delivers water to shareholders. These include NSW Irrigation Corporations, Private Irrigation Districts and Private Water Trusts. The Narromine Irrigation Board of Management is the only irrigation infrastructure operator in the Macquarie Castlereagh WRPA. The development of the Sodium Adsorption Ratio (SAR) target is outside the scope of this document and will be determined in future reporting when data is available. The time series electrical conductivity data collected by the river gauging station network was used to assess this target rather than monthly manual grab samples. Table 4: Salinity targets for irrigation water

Electrical Sodium Water Quality Ecosystem Type conductivity adsorption Zones (µS/cm) ratio

NSW Department of Planning, Industry and Environment | INT17/243328 | 6 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

All Streams, rivers, lakes 957 undetermined and wetlands

1.4.5. Water quality targets for recreational water The primary aim of these targets is to protect the health of humans from threats posed by the recreational use of water. This includes a level of risk to human health from water quality threats posed by exposure to blue- green algae (cyanobacteria) through ingestion, inhalation or contact during recreational use of water resources. The targets are based on Chapter 6 of the National Health and Medical Research Council Guidelines for Managing Risk in Recreational Water (NHMRC 2008). In addition, it is also a general target that cyanobacterial scums should not be consistently present. The recreational water targets are listed in Table 5. Table 5: Blue-green algae targets for recreational water

Water Quality Ecosystem Guidelines Zone Type

  10 µg/L total microcystins; or  50 000 cells/mL toxic Microcystis aeruginosa; or All Recreational 3 water bodies biovolume equivalent of  4 mm /L for the combined total of all cyanobacteria where a suitable for known toxin producer is dominant in the total biovolume; or primary contact.   10 mm3/L for total biovolume of all cyanobacterial material where known toxins are not present; or  Cyanobacterial scums consistently present

1.4.6. Salinity targets for the purposes of long-term salinity planning and management Electrical conductivity targets have not been described for each water quality zone of the Murray Darling Basin. Instead, the Murray Darling Basin End-of-Valley salinity targets, as described in Schedule B, Appendix 1 of the Commonwealth Water Act (2007), have been incorporated into the water quality targets. The End-of- Valley targets for the Macquarie Castlereagh WRPA are listed in Table 6. As for the irrigation water targets, the time series electrical conductivity data has been used to assess this target rather than monthly samples. Table 6: Salinity targets for purposes of long term salinity planning in the Macquarie Castlereagh WRPA

End- of -Valley Targets (as absolute values)

Salinity (EC µS/cm) Salt Load (t/yr) Water Quality Zones Ecosystem Type

Median Peak (80%ile) Mean (50%ile)

Macquarie River Streams, rivers, 504 744 25 760 lakes and wetlands

Bogan River Streams, rivers, 456* 581* 34 830 lakes and wetlands

Castlereagh River Streams, rivers, 368 8 910 lakes and wetlands

NSW Department of Planning, Industry and Environment | INT17/243328 | 7 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

* The End-of-Valley 50th and 80th percentile salinity targets for the Bogan River listed in Appendix 1 of Schedule B of the Murray Darling Agreement for the Bogan River have been reversed in this report 2. Water quality parameters This report focuses on assessment of water quality parameters listed in the Basin Plan. These parameters represent general water quality condition and are most likely to demonstrate change over time from broad scale implementation of natural resource management. 2.1. Turbidity and suspended sediment Turbidity is a measure of water clarity. As light passes through water it is scattered by suspended material; the higher the scatter of light, the higher the turbidity. For example, after rain, water in rivers may appear brown due to scattering of light from high levels of suspended soils. Turbidity and the amount of total suspended solids are closely related in the Macquarie and Castlereagh catchments. The amount of suspended sediment in water is generally related to the intensity of human activity in the catchment, such as land clearing, accelerated erosion from agricultural land, stream banks or channels and localised issues such as the dispersive nature of the soil and stock access. High turbidity is often associated with increased flow following storm events. Increased turbidity can lead to reduction in light penetration and primary production. It can also lead to blooms of some harmful blue-green algae species as they are able to out compete other algal species for light in highly turbid conditions (Oliver et al. 2010). Increased suspended sediments can also have negative impacts on plants through smothering (Brookes 1986) and on fish, for example, by clogging gills (Bruton 1985). Suspended matter can also provide a mode of transport for pollutants, such as heavy metals, (Chapman et al. 1998), nutrients and pesticides (Mawhinney 1998) and bacteria (Wilkinson et al. 1995). Turbidity should be measured immediately without altering the original sample conditions such as temperature and pH (APHA 1995). Field turbidity is more representative of instream conditions and should be used in preference to laboratory measurement (Buckland et al. 2008).

Volume and manner of water release for storages

Poor soil conservation Carp practices

Overgrazing of catchments, grazing of Elevated levels of Declining stream morphology, gully riverbank and floodplains suspended matter erosion, side wall cut and head migration

Wave wash from Rapid drawdown of boats water

Inappropriate frequency timing and location of cultivation

NSW Department of Planning, Industry and Environment | INT17/243328 | 8 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

2.2. Nutrients Nutrients such as nitrogen and phosphorus are important for sustaining growth and productivity within rivers, but at high concentrations can become an issue in freshwater ecosystems. In many circumstances the inputs of nutrients to rivers has increased due to human activities. This process is known as eutrophication (meaning well-nourished) (Smith et al. 1999). Sources of nutrient contamination include discharge from sewage treatment works, farms and industry, and runoff from agricultural land and urban storm water (Smith et al. 2006). Nutrients can be dissolved, bound within sediments, or adsorbed onto suspended material (i.e. soil or organic matter). Increased nutrient concentration can cause issues including nuisance algal blooms (Anderson et al. 2002), dissolved oxygen depletion (Dodds 2006) or inversely supersaturated and toxic effects to aquatic organisms (e.g. ammonia) (Davis and Koop 2006). This document generally refers to total nitrogen or total phosphorus as a basic measure of all forms of these two elements.

Nutrients from water storages

Soil and organic matter Fertilisers

Elevated levels of nutrients

Atmospheric Animal waste deposition

Sewage and industrial discharge

2.3. Dissolved oxygen Dissolved oxygen in water is essential for supporting fish and aquatic animals. If oxygen levels rise too high or drop too low it places stress on animals and can be fatal (Boulton et al. 2014). Dissolved oxygen may be measured as either the concentration of oxygen in water (mg/L), or as a percentage of the maximum amount of oxygen that may dissolve in water (% saturation). Dissolved oxygen concentrations vary throughout the day and are generally lowest at night when plants and algae are not producing oxygen. Dissolved oxygen levels drop when respiration (microbes and animals breathing oxygen) out paces oxygen replenishment by primary production (photosynthesis from aquatic plants and algal and atmospheric adsorption). This process is called ecosystem metabolism. Factors that influence metabolism include concentration of organic carbon and nutrient bioavailability, water temperature, light penetration, turbidity and hydrology (Caffrey 2004; Young et al. 2008). The Basin Plan targets for dissolved oxygen include a lower and upper range. Maintaining dissolved oxygen levels within this range indicates that ecosystem metabolism is largely in equilibrium. When there is a sudden input of bioavailable organic carbon and nutrients, for example when flood waters inundate an area with high levels of fresh leaf litter and flush this material back into the river, microbial respiration can increase rapidly causing oxygen levels to drop to very low concentrations. These are known as anoxic blackwater events (Whitworth et al. 2012). Alternatively, high nutrient inputs can lead to excessive aquatic plant growth resulting in very high oxygen levels or supersaturation.

NSW Department of Planning, Industry and Environment | INT17/243328 | 9 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Release of low oxygen bottom waters Eutrophication and excessive from dams and weirs plant and algal growth

Dissolved oxygen outside natural ranges

High microbial respiration as a result of Oxygen depletion in standing pools organic matter loading

2.4. pH The pH is a measure of how acidic or basic water is. pH ranges between 0 (very acidic) to 14 (very basic) with 7 being neutral. pH outside of natural ranges can be harmful to plants and animals (Boulton et al. 2014). It influences the solubility and bioavailability of nutrients and carbon and the toxicity of pollutants (Closs et al. 2009). Very high or low pH can affect the taste of water, increase corrosion in pipes and pumps and reduce the effectiveness of drinking water treatment (WHO 2004). The pH in water varies with soil type, geology and surface water and groundwater interactions. Human activities such as agricultural practices that expose acid sulphate soils and increase erosion may lead to decreased pH (Dent and Pons 1995). Eutrophication and excessive algal growth can lead to increases in pH (Boulton et al. 2014). Detrimental effects from pH on aquatic ecosystems are unlikely at the levels found across much of the Murray-Darling Basin (Watson et al. 2009).

Exposure to the air of soils containing Agricultural practices that lead to iron sulfide material soil acidification

pH outside of natural ranges

Eutrophication and excess plant Urban runoff and algal growth

2.5. Water temperature and thermal pollution Water temperature influences many biological and ecosystem processes. Warmer temperatures can increase growth rates and metabolism of microbes, animals, plants and algae (Boulton et al. 2014; Kaushal et al. 2010). Temperature is also linked to spawning, breeding and migration patterns of many aquatic animals (Astles et al.

NSW Department of Planning, Industry and Environment | INT17/243328 | 10 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

2003; Lessard and Hayes 2003). Higher temperatures can result in increased solubility of salts and decreased solubility of oxygen (Boulton et al. 2014). Temperature is highly dynamic and varies at different time scales (e.g. seasonally and day/night). Human activities can have large impacts on temperature. Thermal water pollution can occur when dams stratify creating a cold bottom layer. If water is released from this bottom layer, it can lead to considerably colder water temperature than normal (Preece 2004). Thermal water pollution has had significant negative impacts on fish recruitment and can potentially influence ecosystem productivity and carbon cycling downstream of dams (Lugg and Copeland 2014; Webb et al. 2008). The removal of riparian vegetation can reduce shading, leading to increased water temperatures (Marsh et al. 2005; Rutherford et al. 2004). Other human activities such as discharge from power plants or warmer groundwater can also lead to increased river temperature (Lardicci et al. 1999). Climate change is also affecting river temperatures in the Murray Darling Basin (Pittock and Finlayson 2011).

Water released from below Climate change thermocline of large storages

Thermal pollution

Removal of shading riparian Reduced flow vegetation

2.6. Salinity Salinity is the presence of soluble salts in water. It is generally measured as electrical conductivity (the ability of dissolved salts to transmit an electric current). Increased salinity can have harmful effects on many plants and animals (James et al. 2003), effect drinking water supplies (WHO 2004) and cause damage and loss to cropping and horticulture sectors (Hillel 2000). The suitability of water for irrigation is often measured as a sodium adsorption ratio (SAR), which is a measure of the relative concentration of sodium, calcium and magnesium (Sposito and Mattigod 1977). Increased electrical conductivity in rivers may be derived from the presence of salt in underlying soil released by the weathering of rocks, salt deposited during past marine inundation of an area, or salt particles being carried over the land surface from the ocean. Australia’s arid climate provides insufficient rainfall to dilute the high levels of salt in the landscape. This has been further exacerbated by the increased mobilisation of salts by the use or discharge of saline groundwater to surface water, removal of deep-rooted native vegetation to be replaced with shallow-rooted crops or pastures and discharge of saline water from mining or industrial processes. The initial stage of a flood is characterised by high electrical conductivity, often called a ‘first flush’. These appear as sharp spikes in the data followed by a rapid decline. As rainfall first starts to run off the landscape, it mobilises salts concentrated on the soil surface and washes them into the waterways. As flow increases, salts concentrated in the bottom of pools are also flushed out. Following this peak, electrical conductivity drops rapidly due to the dilution of salts by rainwater. The irrigation industry is more likely to experience difficulties with these high salinity spikes before impacts of any long term accumulation are realised. It is advisable for irrigators to let this first flush pass downstream before commencing to pump.

NSW Department of Planning, Industry and Environment | INT17/243328 | 11 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Replacement of deep-rooted vegetation with shallow-rooted vegetation

Increased deep drainage below Irrigation with groundwater at locations irrigated agricultural land displacing where highly saline upper aquifer water saline groundwater to surface water drains to lower aquifer

Use of water with a high ratio of sodium Saline surface and shallow groundwater Elevated levels of to calcium and magnesium for irrigation drainage from irrigated land salinity

De-watering of Irrigation at high saline groundwater salinity risk locations

Reduction of in-stream flows Saline water discharges limiting dilution

2.7. Harmful algal blooms Most algae are safe and are a natural part of aquatic ecosystems. However, some types of blue-green algae (cyanobacteria) can produce hepatotoxins, neurotoxins and contact irritants. When these species occur in bloom proportions (harmful algal blooms) they pose a serious risk to human, animal and ecosystem health (Chorus and Bartram 1999). In addition to toxin production, algal blooms can produce taste and odour problems in water supplies and blockages in irrigation systems. Harmful algal blooms can occur when there are suitable conditions including high levels of nitrogen and phosphorus, warm water temperatures and sunny days, low turbidity and calm water conditions where water may stratify (Anderson et al. 2002; Hudnell 2008). Blue-green algae blooms are normally associated with lakes and reservoirs, but do occur in rivers when conditions are favourable.

Water with little or no flow

High temperatures Stratification

Harmful algal blooms

Nutrients Sunlight

Seeding from upstream

NSW Department of Planning, Industry and Environment | INT17/243328 | 12 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

2.8. Toxicants Toxicants refer to chemical contaminants that have the potential to be toxic at certain concentrations. These include metals, inorganic and organic toxicants (Warne 2002; Warne et al. 2014). Toxicants can have public health impacts and induce stress and fatalities in plants and animals (Heugens et al. 2001; Newman 2009). Toxicants enter water from a range of human activities including agriculture, industry and mining, and can also enter surface waters naturally through groundwater connectivity. Spray drift, vapour transport and runoff are the main pathways for pesticide transport into river systems (Mawhinney 1998, Raupach et al. 2001). Spray drift and vapour can both contribute low level but almost continuous inputs to the riverine ecosystem during the peak spraying season. The likelihood of pesticide drift is influenced by weather conditions, the method of application, equipment used and crop structure. Runoff tends to provide occasional high concentrations of pesticide contamination. Pesticides in runoff can be dissolved in the water, bound within sediments or adsorbed on to suspended particles.

Carp

Toxicants in sewage Erosion of contaminated land

Increased deep drainage below Elevated levels of Inappropriate disposal of pesticides irrigated agricultural land displacing and toxicants saline groundwater to surface water toxicants

Leaching of toxicants Runoff of pesticides and into groundwater other toxicants

2.9. Pathogens Bacteria and microorganisms occur naturally in rivers. Certain species have the potential to elicit disease symptoms; these are referred to as pathogens. In certain concentrations, pathogens can have negative impacts on public health (Prss 1998; WHO 2004), aquatic animals (Gozlan et al. 2006), stock watering (LeJeune et al. 2001) and inhibit the use of water for irrigation (Steele and Odumeru 2004). Human activities can increase the potential risk from pathogens including discharge of human and animal waste and sewage, and access of stock and animals to rivers and water supplies (Ferguson et al. 1996; Fong and Lipp 2005; Hubbard et al. 2004). Deal and Wood (1998) reported high levels of faecal coliforms were generally reported in spring and summer whilst autumn and winter had lower levels. The sources of the E.Coli in river samples were identified as both animal and human in origin. Current monitoring and knowledge of the presence of pathogen issues in the Macquarie and Castlereagh catchment is limited. It is expected that increased runoff will result in increased faecal coliforms as material such as soil and faecal matter is washed into waterways. Additionally, during periods of low rainfall and low flow, faecal coliforms have appropriate conditions to multiply (Deal 1997). Large water bird breeding events in the Macquarie Marshes result in naturally high levels of faecal coliforms. The pathogens would largely be restricted to the rookery area and immediately downstream.

NSW Department of Planning, Industry and Environment | INT17/243328 | 13 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Major waterbird breeding events

Elevated levels of pathogens

Human and animal Sewage and waste wastewater discharges

3. Water access rules and flow management in the Macquarie Castlereagh WRPA In the unregulated catchment, there are very limited opportunities to manage water quality through flow management. Under the current water sharing plans for the Macquarie Bogan Unregulated and Alluvial Water Source (2016) and the Castlereagh River Unregulated and Alluvial Water Source (2017), pumping is generally not permitted from natural pools when the water level in the pool is lower than its ‘full capacity’. ‘Full capacity’ can be approximated by the pool water level at the point where there is no visible flow into and out of that pool. The Cease to Pump rule ensures that additional pressure is not placed on pools by extracting water when the waterway has stopped flowing. During low flows, as pools contract, water quality can deteriorate, algal blooms occur, dissolved oxygen levels decline and fauna compete for the reducing food supplies. In the regulated system downstream of Windamere and Burrendong Dams there is more scope to utilise flow rules and environmental flows to benefit water quality. In the Water Sharing Plan for the Macquarie and Cudgegong Regulated Rivers Water Source (2016) there are four rules for consideration. Plan extraction limits - Sets a limit on the long term average volume of water that can be extracted. All water above the water sharing plan extraction limit is to be used for the environment. On a long-term average basis, approximately 73% of average annual flows (estimated 1 448 000 ML/year) in the river are protected for the maintenance of basic ecosystem health. Maintaining base flow is important to slow the decline in water quality by preventing pools from stratifying and stagnating. Provide natural flows in the upper reaches of the Cudgegong River – A portion of inflows to Windamere Dam are released to attain, in combination with downstream tributary flows, 150 to 1 500 ML/day at Rocky Waterhole. No releases occur when the capacity of Windamere Dam is less than 110 000 ML, and releases are subject to an annual limit of 10 000 ML. Environmental contingency allowance - Under the Water Sharing Plan, an Environmental Contingency Allowance (ECA) of up to 160 000 ML is available in any water year. An Environmental Flow Reference Group (EFRG), comprising industry, environmental, wetland and Government representatives provides advice on when water should be released for environmental purposes to maximise environmental benefits. The ECA has two sub accounts. Sub account 1 is used to provide more natural flows downstream of Burrendong Dam. Releases are made during the periods 1 June to 30 November and 15 March to 31 May each year to attain, in combination with tributary inflows, a flow of between 500 and 4 000 ML/day at Marebone Weir. Sub account 2 is released when there is a need for special environmental purposes such as:

NSW Department of Planning, Industry and Environment | INT17/243328 | 14 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

 To enhance opportunities for native fish recruitment and dispersal in the Macquarie River and Macquarie Marshes, and  To ensure completion of colonial water bird breeding and to alleviate severe, unnaturally prolonged drought conditions in the Macquarie Marshes. Supplementary flow access rules - There are also restrictions on extractions under supplementary water access licences. Holders of these licences are able to extract water during announced periods when flows exceed those required to meet other obligations and environmental needs, such as when Burrendong Dam is spilling or as a result of high tributary inflows downstream of the dam. These restrictions are in place to:  Preserve a significant proportion of natural tributary flows for river health and the wetlands;  Protect important rises in water levels;  Maintain wetland and floodplain inundation, and  Maintain natural flow variability. The Commonwealth Environmental Water Office (CEWO) currently holds up to 134 516 ML of environmental water in the Macquarie Valley. The NSW Office of Environment and Heritage (OEH) holds approximately 50 000 ML of “discretionary” or “held” environmental water which has been acquired under the Riverbank Program or Wetlands Recovery Program, either through water efficiency works or by purchase of entitlement. Current environmental watering is largely focused on meeting environmental demands at target assets and protecting a proportion of unregulated flows to restore more natural flows to the Macquarie system. This includes the Macquarie Marshes Ramsar site, ecologically important distributary creeks and the lower Macquarie River. Environmental water can augment base flows and freshes to support wetland and riparian vegetation and the survival and reproduction of waterbirds, fish and other vertebrates. Environmental water is to be managed in accordance with the Long Term Watering Plan (LTWP), Basin Watering Strategy and Annual Basin Watering Priorities. It is not the intent of the Water Quality Management Plan to propose the use of environmental water to address specific water quality issues. However, the release of environmental water for its designated purpose, will provide water quality benefits for the Macquarie and Cudgegong Rivers, such as breaking up stratification in pools, diluting salts, mobilising dissolved organic carbon and making conditions less favourable for harmful algal bloom development. Holders of environmental water in their independent decision making, must 'have regard' to dissolved oxygen, salinity and recreational water quality when making decisions about the use of environmental water. There are opportunities to adjust the way water is delivered from Windamere and Burrendong Dams to provide additional water quality and environmental benefits to the aquatic ecosystem. Releasing large volumes water as a block, with very steep rising and falling limbs, has the potential to pose threats to the Cudgegong and Macquarie Rivers through bank slumping and bank erosion. Mimicking a natural flood event by maintaining natural flow variability and natural rates of change in water levels, with more gradual rising and falling limbs, can help reduce bank slumping. Increased water levels can inundate lower benches, flushing carbon into the system providing fuel to stimulate riverine food webs. High flow velocities can also scour silt and biofilms from rocks and logs in the river, resetting biofilm development and improving habitat quality. The trade of water entitlement is another potential rule to manage risks to water quality. Trading entitlement out of an over allocated water source or away from a potentially sensitive area, could have longer term benefits by assisting in mitigating the impact on instream values via reduced levels of extraction. Similarly, the trade of held environmental water into a stressed water source could provide benefits to water quality. Water trade has not been identified in this report as an immediate mitigation measure, as there is no certainty of where or when it may occur.

NSW Department of Planning, Industry and Environment | INT17/243328 | 15 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

4. Methods 4.1. Site selection and monitoring The water quality data used in this report were compiled from 15 routine water quality monitoring stations located within the Macquarie Castlereagh WRPA. The data were collected on a monthly basis for the State Water Quality Assessment and Monitoring Program (SWAMP). This water quality monitoring program is responsible for collecting, analysing and reporting the ambient water quality condition of rivers in New South Wales. The program in its current form commenced in November 2007 replacing numerous regionally based water quality monitoring programs. The data set used in this report covers a five year period from July 2010 to June 2015. A five year time period was chosen as it is consistent with the Basin Plan (Schedule 12) five yearly review against water quality targets. A full station list is given in Table 7 and the location of these sites in relation to the Basin Plan water quality zones is shown in Figure 2. The coordinates for all monitoring sites are listed in Appendix A. Table 7: List of routine water quality monitoring stations in the Macquarie Castlereagh WRPA

Station Basin Plan WQ zone Station Name Number B3 420004 Castlereagh River at Mendooran B3 42110171 Fish River at Hazelgrove B3 42110170 Turon River at Bathurst Point B3 421025 Macquarie River at Bruinbun B3 421038 Cudgegong River at Rylstone Bridge B3 421019 Cudgegong River at Yamble Bridge B3 421077 Macquarie River downstream Burrendong Dam B3 421018 Bell River at Newrea B3 421176 Little River at Arthurville B3 421042 Talbragar River at Elong Elong B3 42110101 Macquarie River at Molong Rail Bridge B3 421004 Macquarie River at Warren Weir A3 421011 Marthaguy Creek at Carinda A3 421012 Macquarie River at Bells Bridge A3 421023 Bogan River at Gongolgon

There are 17 continuous electrical conductivity monitoring sites in the Macquarie Castlereagh WRPA. These are located at existing river gauging stations and take electrical conductivity readings every 15 minutes. The sites are listed in Table 8. Site coordinates are listed in Appendix A. The data from monitoring sites located upstream of Burrendong Dam have not been assessed, due to the lack of irrigation in these catchments. The Bogan River at Gongolgon, Castlereagh River at Gungalman and Macquarie River at Bells Bridge are the End- of-Valley salinity target sites for each catchment. All continuous electrical conductivity data is stored in the HYDSTRA database.

NSW Department of Planning, Industry and Environment | INT17/243328 | 16 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Table 8: List of continuous electrical conductivity monitoring stations in the Macquarie Castlereagh WRPA

Station Station Name Number 421004 Macquarie River at Warren Weir 421011 Marthaguy Creek at Carinda 421012 Macquarie River at Bells Bridge 421018 Bell River at Newrea 421019 Cudgegong River at Yamble Bridge 421023 Bogan River at Gongolgon 421026 Turon River at Sofala 421039 Macquarie River at Neurie Plain 421040 Macquarie River downstream Burrendong Dam 421048 Little River at Obley 421079 Cudgegong River downstream Windamere dam 421090 Macquarie River downstream Marebone weir 421107 Marra Creek at Billybingbone 421127 Macquarie River at Baroona 421191 Macquarie River at Yarracoona 420020 Castlereagh River at Gungalman Bridge 420017 Castlereagh River at Hidden Valley

Blue-green algae monitoring in the Macquarie Castlereagh WRPA focuses on Burrendong and Windamere Dams. Due to the large surface area of Burrendong Dam, samples are collected at seven locations, covering the main recreational areas of the dam (Stations 1, 3 and 6, State Recreation Area, Sport and Recreation Area, Mookerawa Waters and Cudgegong Park). Two samples are collected in Windamere Dam (Station 1 and Recreation Area). A sample is also collected downstream of both dams to determine if potentially toxic blue-green algae are being released into the Cudgegong or Macquarie Rivers. Water temperature data is collected at all routine water quality monitoring sites, however as it is collected monthly, it does not give an indication of diurnal variation or detect cold water impacts. Continuous water temperature data is collected at 17 sites with permanent sensors installed at gauging stations. There are a further 16 temporary HOBO temperature loggers installed in the Macquarie valley to investigate the effectiveness of the thermal curtain installed in Burrendong Dam. The data from these loggers has not been included in this assessment due to the short length of data record. A full station list is given in Table 9 and the location of these sites is shown in Figure 3. Table 9: List of continuous water temperature monitoring stations in the Macquarie Cudgegong WRPA

Station Station Name Sensor type Number 421004 Macquarie River at Warren Weir Permanent 421011 Marthaguy Creek at Carinda Permanent 421012 Macquarie River at Bells Bridge Permanent 421018 Bell River at Newrea Permanent 421019 Cudgegong River at Yamble Bridge Permanent 421023 Bogan River at Gongolgon Permanent 421026 Turon River at Sofala Permanent

NSW Department of Planning, Industry and Environment | INT17/243328 | 17 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

421039 Macquarie River at Neurie Plain Permanent 421040 Macquarie River downstream Burrendong Dam Permanent 421048 Little River at Obley Permanent 421079 Cudgegong River downstream Windamere dam Permanent 421090 Macquarie River downstream Marebone weir Permanent 421107 Marra Creek at Billybingbone Permanent 421127 Macquarie River at Baroona Permanent 421191 Macquarie River at Yarracoona Permanent 420020 Castlereagh River at Gungalman Bridge Permanent 420017 Castlereagh River at Hidden Valley Permanent

MACQUARIE CASTLEREAGH WATER RESOURCE PLAN AREA - WATER TEMPERATURE MONITORNG SITES

Macquarie River at Baroona GF DUBBO "

Cudgegong River at Yamble Bridge GF

WELLINGTON " Macquarie River MUDGEE D/S Burrendong Dam Little Bell River " Cudgegong River at at Newrea GF Obley River D/S GF Windamere Dam GF LAKE BURRENDONG GF

LAKE WINDAMERE

Turon River Macquarie at Sofala River at GF Yarracoona n i s a GF B g n li r a ORANGE D y " a rr u M

BATHURST "

Data Sources: GF Water temperature monitoring sites NSW Industry I Lands & Water I Water. Office of Environment and Heritage. " Towns Murray Darling Basin Authority. Geoscience Australia. Rivers ± 0 20 40 60 80 Macquarie Castlereagh boundary Map produced by NSW Industry I Lands & Water 28 September 2018 Highways kilometres Figure 3: Continuous water temperature monitoring sites in the upper Macquarie Castlereagh WRPA

4.2. Water quality index (WaQI) A water quality index (WaQI) is an important tool to communicate and report water quality condition. It conveys information that is complex and on different scales (e.g. 75% saturation dissolved oxygen and 0.05 mg/L total phosphorus) to a common score and rating. A literature review was conducted in 2015 to understand the different approaches and techniques for calculating and using water quality indexes globally. A method based on a modified Canadian Council of Ministers of the Environment (CCME) water quality index (Lumb et al. 2006) was then defined, that incorporated both frequency and exceedance of water quality targets. The method scales five years of data

NSW Department of Planning, Industry and Environment | INT17/243328 | 18 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

into a single number between 1 and 100 which corresponds to four categories: Poor, Fair, Good and Excellent. It is applied to both individual parameters and parameters combined to provide an overall score (Appendix B). For New South Wales WQMP, the WaQI is calculated for each water quality parameter individually and as an overall integrated index. It includes total nitrogen, total phosphorus, turbidity, dissolved oxygen and pH. There is no weighting of individual parameters. It is based on the exceedance of the water quality targets as prescribed in Schedule 11 of The Basin Plan. Where data is available, temperature, salinity and blue green algae have also been scored as individual parameters. The outcome provides a number between 1 and 100, and is categorised according to the following water quality rating.

4.3. Catchment stressor identification The Catchment Stressor Identification process (CSI) (Figure 4) helps describe the status, issues and potential causes of water quality degradation. The process uses an eco-epidemiological approach (Cormier 2006), and is broadly related to the approach developed by Cormier et al. (2003) for water quality planning in North America for the United States Environmental Protection Agency (USEPA). It identifies issues and causes based on the idea of abductive inference; that is; considering possible causes of water quality degradation, weighing evidence and putting forward factors likely contributing to water quality degradation. Once the water quality degradation issues are defined, evidence is gathered and weighed before conclusions on probable causes synthesised. The CSI process is intended to be iterative and involves conceptual mapping, data evaluation, literature reviews, GIS mapping and input of local and expert knowledge. The process consists of a standard set of procedures and outputs. The final output expresses what water quality degradation is present and the likely cause, using narrative, figures and maps.

Figure 4: Conceptual diagram of the CSI process

NSW Department of Planning, Industry and Environment | INT17/243328 | 19 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

4.3.1. Conceptual mapping Conceptual models are a useful step in mapping out possible causes of water quality degradation. They help define the scope of possible causes of water quality degradation and show interlinkages between both causes of degradation and between water quality parameters. A standard conceptual diagram for overall water quality and each parameter has been created based primarily on Schedule 10 of the Basin Plan. These standard models will then be revised for each parameter in each WRP area during the CSI process. 4.3.2. Literature review A review of both published and grey literature has been undertaken for the Macquarie Castlereagh WRPA. Published literature was reviewed using a standardised approach through the Web of Science database. Grey literature was reviewed in an informal manner through web searches and Google Scholar and included water quality trend reports that have been completed for turbidity and salinity. 4.3.3. Summary statistics The water quality data used to generate summary statistics and the following analysis was primarily from the State Water Quality Assessment and Monitoring Program (SWAMP). Summary statistics of available data for each parameter in a WRP area have been defined. These include basic statistics such as range (minimum, maximum), central tendency (mean, median) and variability (standard deviation, interquartile range, coefficient of variation). These statistics help define basic patterns of water quality degradation. 4.3.4. Data analysis Analysing water quality data is a crucial step in diagnosing issues and their causes. Basic analysis involved examining relationships between parameters, temperature and season, location and hydrology. Data analysis was used to help understand the nature of ecological problems, their interdependencies, seasonal variances, relationship to flow regimes and spatial relationships. 4.3.5. Spatial and GIS Existing spatial information relevant to the causes of water quality degradation for each parameter has been compiled into ArcGIS geodatabases. Initial maps will be produced with relevant spatial information and land use are determined through the CSI process for each WRP area boundary. The spatial information may be refined during the CSI process. 4.3.6. Local and expert knowledge For each WRP area, meetings were held with the technical working group comprised of representatives from partner agencies and other invited experts. These meetings facilitated input of local knowledge and expert opinion to WQMP. In general, these meetings occurred on a one-on-one or organisational basis. This approach was chosen to allow more freedom for people to speak and explore ideas. Information from these meetings was used to refine the scope of water quality degradation, conceptual diagrams, GIS mapping, and to guide further exploration. They also helped define conclusions reached for the causes of water quality degradation and most relevant and fit-for-purpose information to include in this report and the Macquarie Castlereagh WQMP. 4.4. Macquarie Castlereagh WRPA Risk Assessment Risk assessments are the first steps in the development of a water resource plan for each surface water and groundwater planning area in the Murray Darling Basin. Risk assessments and associated water resource plans must be prepared having regard to current and future risks to the condition and continued availability of water resources in a water resource plan area, and outline strategies to address those risks. The risk assessment approach compiles the best available information to highlight the range of potential risks that may be present. Where a risk is highlighted as medium or high, it does not necessarily imply that existing rules in the water sharing plan require change or are inadequate, but rather, that further detailed investigation

NSW Department of Planning, Industry and Environment | INT17/243328 | 20 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

may be required. The risk assessment also highlights where existing plan rules may already be mitigating the risk. The risk to the health of water dependent ecosystems was assessed by identifying the risk, quantifying the impact based on instream values (consequence) and determining the probability of that consequence occurring (likelihood). The consequence of poor water quality was determined using the HEVAE (High Ecological Value Aquatic Ecosystems) instream value. For each monitoring station a reach was defined as 25 km upstream and downstream of the site. This was chosen as a conservative estimate of the spatial representativeness of water quality data and movement of instream biota within the river channel. The consequence decision support tree was then used to define the final consequence score using the HEVAE instream values within each reach area. For detailed description of the risk assessment process and outputs, refer to the Risk Assessment for the Macquarie Castlereagh Water Resource Plan Area (SW11) (2018b). The calculation method for the likelihood scores varied between water quality attributes. The likelihood scores for total nitrogen, total phosphorus, dissolved oxygen, pH and turbidity were the frequency that the Basin Plan water quality target was exceeded, based on monthly sampling data for the five year period, 2010 to 2015. Continuous electrical conductivity data, rather than discrete monthly data, was used to assess risks from poor salinity. The data were assessed against the respective Macquarie, Bogan and Castlereagh End-of-Valley salinity targets. The likelihood of water being unsuitable for irrigation was calculated using the frequency that the 95th percentile of the daily mean electrical conductivity exceeded the irrigation salinity target for the 10 year period from 2005 to 2015. Water temperature risk was based on the presence of a large storage classified as having a severe, moderate or low cold water pollution status, according to Preece (2004). The objective for recreational water quality is to achieve a low risk to human health from water quality threats posed by exposure through ingestion, inhalation or contact during recreational use. Blue-green algae were chosen as the indicator for risk to recreational water quality because of the potential for some species to impact on human health. The risk of water being unsuitable for recreational use considered the frequency of high concentrations of potentially toxic algal blooms (likelihood), compared to the degree of recreational usage of the water body where the sample was taken (consequence). New South Wales currently manages the risk of human exposure to blue-green algal blooms through a coordinated regional approach with the Regional Algal Coordination Committees (RACC). State-wide and regional contingency plans and guidelines have been developed to provide methodologies on the management of algal blooms (NSW Office of Water 2014). The objective of the guidelines is to provide a risk assessment framework to assist with the effective management response to freshwater, estuarine and marine algal blooms. They aim to minimise the impact of algal blooms, by providing adequate warning to the public ensuring their health and safety in recreational situations and for stock and domestic use. Under the current management of algal blooms, the level of human exposure to a bloom can be reduced by management practices such as issuing algal alerts. Alert levels have been developed and are used to determine the actions that need to be undertaken with respect to an algal incident. These alerts have been adopted from the National Health and Medical Research Council algal bloom response guidelines (NHMRC 2008). The risk to a site with a high recreational usage may be reduced by the management strategy of placing algal warning signs at the site and informing users of the risks and dangers. Therefore, where these warning arrangements are in place, a low consequence value was used. Pathogens, pesticides, heavy metals and other toxic contaminants are not monitored regularly, so were not included in the risk assessment.

NSW Department of Planning, Industry and Environment | INT17/243328 | 21 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

5. Results 5.1. Water quality index (WaQI) 5.1.1. Water-dependent ecosystems The WaQI scores for each parameter and the overall score for each site was calculated for the 2010 to 2015 water quality data set. A total of five sites were rated as poor; Macquarie River at Warren Weir and Bells Bridge, Marthaguy Creek at Carinda and Talbragar River at Elong Elong. Cudgegong River at Rylstone, Little River at Arthurville, Turon River at Bathurst Point and Fish River at Hazelgrove all rated as good, with all other sites rated as fair. The results from the WaQI are shown in Table 10 and summarised in Figure 5. Table 10: Water quality index scores for the Macquarie Castlereagh WRPA 2010-2015 water quality data

Site Name Rating WaQI Total N Total P Turbidity pH DO Castlereagh River at Mendooran Fair 65 80 31 71 97 35 Macquarie River at Warren Weir Poor 51 62 38 29 84 62 Marthaguy Creek at Carinda Poor 31 15 7 24 80 55 Macquarie River at Bells Bridge Poor 48 24 22 43 82 61 Bell River at Newrea Fair 74 75 64 65 93 60 Cudgegong River at Yamble Bridge Fair 73 77 54 85 94 52 Bogan River at Gongolgon Poor 55 37 37 65 88 63 Macquarie River at Bruinbun Fair 73 73 60 77 58 77 Cudgegong River at Rylstone Bridge Good 82 58 75 100 91 70 Talbragar River at Elong Elong Poor 31 37 7 22 85 46 Macquarie River D/S Burrendong Dam Fair 76 46 75 100 81 60 Little River at Arthurville Good 82 76 87 86 63 57 Macquarie River at Molong Rail Bridge Fair 68 56 55 76 89 56 Turon River at Bathurst Point Good 91 97 94 91 70 64 Fish River at Hazelgrove Good 88 81 87 99 84 89

NSW Department of Planning, Industry and Environment | INT17/243328 | 22 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Figure 5: Macquarie Castlereagh WRPA water quality index scores 5.1.2. Water temperature There are no long term, water temperature monitoring sites upstream of Windamere Dam. In Figure 6, data from the Turon River at Sofala has been used as a surrogate site to indicate water temperatures in the upper catchment. The Sofala site has a similar altitude and catchment area to upstream of Windamere Dam, however the steep topography of the Turon catchment yields larger flows. The monthly 20th and 80th percentiles were calculated using the mean hourly water temperature data. The monthly median temperature downstream of Windamere Dam was also calculated using the hourly water temperature data. Figure 6 compares the monthly median temperature at the downstream Windamere Dam site to the percentiles of the reference sites. The thermal pollution WaQI score, using the difference between the reference site and downstream data for Windamere Dam was 70, which is a fair rating. The water temperature data in Figure 7 is the daily minimum water temperature at three sites; Turon River at Sofala, Cudgegong River downstream of Windamere Dam and Cudgegong River at Yamble Bridge, compared against the mean daily flow in the Cudgegong River downstream of Windamere Dam. The downstream of Windamere Dam (421079) site is located 4.4 kms below the wall, while Yamble Bridge (421019) is 90 kms downstream of the dam.

NSW Department of Planning, Industry and Environment | INT17/243328 | 23 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

30 Reference 20%ile 28 Reference 80%ile Downstream Windamere median 26

24

22

20

18

16

14

12 Water temperature (°C) 10

8

6

4

2 May-05 Oct-06 Feb-08 Jul-09 Nov-10 Apr-12 Aug-13 Dec-14 May-16 Date Figure 6: Water temperature in the Cudgegong River downstream of Windemere Dam compared to estimated 20th and 80th percentile of natural temperature

8000 Mean Daily flow D/S Windamere (R) Turon R at Sofala (L) 30 Cudgegong R D/S Windamere (L) Cudgegong R at Yamble Bridge (L) 7000

25 6000

5000 20

4000

15 3000 Mean daily flow (ML/day)

10 2000 Minimum daily water temperature (°C)

1000 5

0 Apr-2001 Jan-2004 Oct-2006 Jul-2009 Apr-2012 Dec-2014 Date Figure 7: Minimum daily water temperature in the Cudgegong River against mean daily flow downstream of Windamere Dam from 2000 to 2016

NSW Department of Planning, Industry and Environment | INT17/243328 | 24 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

There are two long term water temperature monitoring sites upstream of Burrendong Dam; Turon River at Sofala and Macquarie River at Bruinbun. There is also a short data set for the Macquarie River at Longpoint. The data from all three sites has been incorporated into the combined “reference site” data for upstream of Burrendong Dam. Figure 8 compares the monthly median temperature at the downstream Burrendong Dam site to the percentiles of the reference sites. The thermal pollution WaQI score for Burrendong Dam has been calculated before and after the installation of the thermal curtain in 2014 to reduce cold water pollution in the Macquarie River downstream of the dam. Pre- curtain the score was 45, which is Poor. Post-curtain, the score improved to 61. The water temperature data in Figure 9 is the daily minimum water temperature at five sites on the Macquarie River both upstream and downstream of Burrendong Dam. The Macquarie River downstream of Burrendong Dam (421040) gauging station is 7.5 km below the wall. It is a further 110 km to the next site at Dubbo (421001) and 163 km to Baroona (421127). The Macquarie downstream of Marebone Weir (421090) is approximately 400 km downstream of Burrendong Dam. The Bogan and Castlereagh catchments have not been assessed as there are no large storages posing cold water pollution impacts in these catchments.

30 Reference 20%ile Reference 80%ile Downstream Burrendong median

25

20

15 Water tempertaure (°C)

10

5

Aug-2010 Sep-2011 Oct-2012 Nov-2013 Dec-2014 Jan-2016 Feb-2011 Apr-2012 May-2013 Jun-2014 Jul-2015 Aug-2016

Date Figure 8: Water temperature in the Macquarie River downstream of Burrendong Dam compared to estimated 20th and 80th percentile of natural temperature

NSW Department of Planning, Industry and Environment | INT17/243328 | 25 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

35 Macquarie at Bruinbun Macquarie DS Burrendong Dam Macquarie at Dubbo 30 Macquarie at Baroona Macquarie at Marebone

25

20

15

10 Minimum daily water temperature (°C)

5

0 Aug-10 Feb-11 Sep-11 Apr-12 Oct-12 May-13 Nov-13 Jun-14 Dec-14 Jul-15 Jan-16 Aug-16

Date Figure 9: Minimum daily water temperature in the Macquarie River downstream of Burrendong Dam from 2010 to 2016 5.1.3. Irrigation The agriculture and irrigation salinity target is for the 95th percentile of the daily mean electrical conductivity not to exceed 957 µS/cm over a 10 year period. This target applies at sites where water is extracted by an irrigation infrastructure operator for the purpose of irrigation. The Narromine Irrigation Board of Management is the only irrigation infrastructure operator in the Macquarie Castlereagh WRPA. Water is pumped from the Macquarie River at Narromine, approximately 24 km downstream of the Macquarie River at Baroona gauging station. The 95th percentile of the 2005 to 2015 electrical conductivity data set and results of the WaQI are shown in Table 11. Table 11: Water quality index scores and 95th percentile results for the Macquarie Castlereagh WRPA 2005-2015 continuous electrical conductivity data

Station Name 95th percentile WaQI score Rating Macquarie River at Baroona 709 100 Excellent The mean daily electrical conductivity in the Macquarie River at Baroona fluctuates throughout the year, with results rarely exceeding the agriculture and irrigation salinity target. The highest electrical conductivity results are recorded in winter and the lower readings in summer (Figure 10). As the target is exceeded in winter, when there is less water utilised for irrigation, the risk of any impacts on soil and crop health is minimised.

NSW Department of Planning, Industry and Environment | INT17/243328 | 26 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

1200

1000

800

600

400 Mean daily electrical conductivity (µS/cm) conductivity electrical daily Mean

200

0 May-05 Oct-06 Feb-08 Jul-09 Nov-10 Apr-12 Aug-13 Dec-14

Figure 10: Mean daily electrical conductivity (µS/cm) in the Macquarie River at Baroona from 2005 to 2015 5.1.4. Recreation The algal biovolume data from Windamere and Burrendong Dams is displayed in Figures 11 and 12 respectively. The red line indicates the red alert level for recreational use based on the National Health and Medical Research Council guidelines. The extreme values in both Figures have not been displayed graphically to maintain focus on the core data. The WaQI score for harmful algal blooms in Windamere Dam is 50, which is a poor rating, and in Burrendong Dam a score of 87, which is a good rating.

NSW Department of Planning, Industry and Environment | INT17/243328 | 27 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

100 485 mm3/L

80 /L) 3

60

40 Potentially toxic cyanobacteria biovolume (mm biovolume cyanobacteria toxic Potentially 20

0 Jan-10 Aug-10 Feb-11 Sep-11 Apr-12 Oct-12 May-13 Nov-13 Jun-14

Figure 11: Potentially toxic cyanobacteria biovolume in Windamere Dam 2010 to 2014

50 819 mm3/L

40 /L) 3

30

20 Potentially toxic cyanobacteria biovolume (mm biovolume cyanobacteria toxic Potentially 10

0 Jan-10 Aug-10 Feb-11 Sep-11 Apr-12 Oct-12 May-13 Nov-13 Jun-14 Dec-14 Jul-15

Figure 12: Potentially toxic cyanobacteria biovolume in Burrendong Dam 2010 to 2015

NSW Department of Planning, Industry and Environment | INT17/243328 | 28 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

5.2. Literature review A literature search was undertaken to gather information from the published literature relevant to water quality in the Macquarie Castlereagh WRPA. Following is a summary of relevant information with more detailed information listed in Appendix C. Parts of the Macquarie and Castlereagh valleys are severely impaired. Approximately 42% of river length in the Castlereagh catchment and 29% of the Macquarie catchment has been substantially modified from natural condition (Norris et al. 2001). There are reaches in the upper catchment around Bathurst and large sections of the Talbragar River with less than 20% native woody riparian vegetation. Inversely, there are long reaches with greater than 80% cover in the Turon River catchment and the lower Macquarie, Castlereagh and Bogon Rivers (DoIW 2018b). Riparian vegetation is important as a carbon source, its shading reduces solar radiation, limiting in-channel autotrophic production (Kelleway et al. 2010) and as a source of large woody debris to protect against erosion and restore river health (Erskine et al. 2012). Austin et al. (2010) estimated that climate change my reduce water yield in the Castlereagh by up to 24% by 2030 and 54% by 2070 and the Macquarie and Bogan by up to 22% by 2030 and 51% by 2070. The reduced water yield will also lead to decreased salt yield. Balcombe et al. (2011) identifies climate change as a current and future threat to the Basin fish fauna. Continued over regulation of water resources will place as much if not more stress on remnant fish species. Climate change is likely to lead to fewer refuge pools during dry periods and decreased available drought refugia. Water temperature, flows, habitat and food resource (prey size and availability) all impair fish recruitment. Flow magnitude and water temperature appear to have the largest effect in determining larval fish composition (Rolls et al. 2013). It is suggested that a lack of prey and food resources may be one reason why there is not a strong response to managed flow events (Rolls et al. 2013). In addition, where river channels have already been impacted by regulated flows, complex surfaces such as benches may have already been lost, so restoring more natural flows at these levels of channel, may have little immediate impact on carbon and nutrient processing (Woodward et al. 2015). Low level benches will need to be ‘rebuilt’ before environmental flows can increase connectivity. Astles (2003) manipulated the temperature of water from Burrendong Dam. Silver perch grown in warmer temperatures (18 to 24°C) grew longer and heavier than those in cooler water (12 to 14°C). Both Silver Perch and Murray Cod showed behavioural preferences for warmer water. In 2013, water temperature ranges downstream of Burrendong Dam were only briefly met for Golden Perch episodically near the end of the spawning season and not at all for Murray Cod and Silver Perch (Gray 2016). Rayner et al. (2009; 2015) studied fish recruitment responses to flows in the Macquarie Marshes. Temperatures were 4 to 12°C below spawning threshold for native fish, which promoted the spawning of alien fish. It was recommended that the release of flows consider water temperature in order to promote native fish recruitment. Investigations into sediment sources by Wethered et al. (2015) found that whilst topsoils contribute up to 39% of sediment in headwaters, beyond the headwaters, the greater percentage is from sub soils. Subsoils enter the river system via gully and bank erosion, topsoils are transported by sheet and rill erosion. Top soil makes a greater contribution when cultivation and grazing is present versus forest and woodland. Kobayashi et al. (2011b) measured longitudinal patterns in water quality at multiple sites in the Macquarie River downstream of Marebone Weir during a low flow year. Two distinct ecological zones were identified:  Upstream zone with high dissolved oxygen, turbidity, diatoms and gross primary productivity/planktonic respiration (GPP/PR), and  Downstream zone with a high level of nutrients, dissolved organic nitrogen, cyanobacteria, bacteria, protozoans and cladocerans. Numerous studies into the response of the Macquarie Marshes to environmental flows have been undertaken. Dissolved oxygen can be very low (3 mg/L) in-channel and on floodout areas, but supersaturated in the lagoons where primary production is high. Zooplankton numbers were very high in the lagoons. Nutrient concentrations (including dissolved inorganic phosphorus, dissolved inorganic nitrogen, dissolved organic nitrogen, dissolved organic phosphorus, total nitrogen and total phosphorus) were high (Kobayashi et al. 2015). During a release, total nitrogen concentrations increases rapidly after inundation, followed by total

NSW Department of Planning, Industry and Environment | INT17/243328 | 29 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

phosphorus and dissolved organic carbon. Bacteria and phytoplankton increased with dissolved organic carbon and nutrients rapidly. Increases in total nitrogen and total phosphorus following inundation, led to levels above targets. All factors were higher at sites with a vegetation canopy rather than open, highlighting the importance of riparian vegetation (Kobayashi et al. 2009). Kangaroo faeces was found to be a source of around 6% of total nitrogen, 3% of total phosphorus and 8% of dissolved organic carbon during flooding in Macquarie Marshes (Kobayashi et al 2011a). A study examining sediment cores and fossil records found an increase in sedimentation rate and turbidity between 1940 and 1970 (Yu et al. 2015). It was suggested that livestock grazing and building channels and levees was responsible. Algal species have shifted from those preferring a pH less than 7 to those favouring greater than 8. The increased pH was identified as being due to increased erosion with base cations and decrease in acid generating native vegetation. Herron et al. (2003) suggests small scale strategic tree plantings on their own will not be enough to impact on salt loads at the End-of-Valley monitoring site. Widespread tree plantings may reduce salt loads but will also lead to reductions in water flows in the short term. Electrical conductivity in the Macquarie Marshes was found to be low. Aquatic plant germination and species richness decreases significantly with increasing salinity (<300 to 1000 mg/L). Similar for zooplankton hatching, the Macquarie Marshes had significant declines above <300 mg/L. Community stricture changed above 1000 mg/L (Brock et al. 2005). In an assessment of wetlands and rivers in the Macquarie, Lachlan and Murrumbidgee valleys the driver for and gross primary productivity and gross primary productivity/planktonic respiration in channel habitats was a function of dissolved organic carbon. While in non-channel habitats, the driver was a function of total nitrogen and/or total phosphorus (Kobayashi et al. 2009). Nutrient bioassays in Chifley Dam showed that cyanobacteria was phosphorus limited 33% of the time, nitrogen and phosphorus limited 25% of the time and not nutrient limited 42% of the time (Kobayashi and Church 2003). It was also found that the nitrogen:phosphorus ratio did not predict when nutrients were limiting and that zooplankton grazing was generally not high enough to supress algae. Olley and Caitcheon (2000) suggest that the best strategy to limit excess algal growth in lowland rivers is to manage flow so that the river remains turbid and stratification of pools is prevented. The detection of agricultural chemical residues, particularly the insecticide endosulfan in routine water samples was an issue in the Macquarie Valley in the 1990s (Muschal 2001). The concentrations and frequency of detections were lower in the Macquarie valley than the more northern NSW cotton growing areas. The delivery of pesticides to the aquatic environment appeared largely dependent on rainfall and flooding. When pesticide monitoring ceased, the movement of chemical residues into the river system was reducing with the adoption of industry best management guidelines and improved agronomic practices (Muschal 2001). 5.3. Summary statistics Summary statistics for the key water quality parameters at each monitoring site in the Macquarie Castlereagh WRPA have been displayed as tables (Appendix D) and represented using box plots (Appendix E). The box plots in Figure 13 show the annual 25th, 50th and 75th percentile values, with error bars indicating the 10th and 90th percentile values for each site. The data set extends from 2007 to 2015 and displays monitoring site variability within the Macquarie Castlereagh WRPA. There are numerous plots within Figure 13, A) total nitrogen, B) total phosphorus, C) turbidity, D) total suspended solids, E) dissolved oxygen, F) pH, G) electrical conductivity measured during monthly sampling. There is a general trend of increasing nutrient concentrations down the catchment with the highest results in Marthaguy Creek at Carinda. There are also very high concentrations in Talbragar River at Elong Elong. The concentrations of nutrients detected are not limiting to algal growth. As harmful algal blooms were not regularly detected in the Macquarie River, this indicates that other factors are restricting algal growth. Turbidity also increased with distance down the catchment, reflecting the impact of the cumulative effects of land use, soil disturbance and human activity on water quality. Dissolved oxygen levels fluctuate between sites in response to local drivers. In the upper catchment, dissolved oxygen levels are stable and suitable to support aquatic life. The Cudgegong River at Yamble Bridge and Bell River at Newrea both have oxygen levels below the Basin Plan lower limit. In contrast, Little River at Arthurville

NSW Department of Planning, Industry and Environment | INT17/243328 | 30 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

exceeded the upper limit. This suggests oxygen production by aquatic macrophyte and algal growth in Little River is outpacing respiration. The largest range in dissolved oxygen results are in the lower catchment. At these sites high turbidity reduces light penetration, reducing aquatic plant growth and higher water temperature reduces the solubility of oxygen in the water column, resulting in low dissolved oxygen. Inversely, the high nutrient levels can result in increased photosynthesis and subsequent supersaturated oxygen levels. Compared to other parameters, pH is relatively consistent throughout the Macquarie Castlereagh WRPA. The pH is slightly elevated (basic), but not to the extent where it would impact on the health of aquatic ecosystems or agricultural enterprises. Little River has the highest median electrical conductivity followed by the Bell River. There is limited opportunity for irrigation from Little River, making the risk of impacts to agriculture production and soil structure, low. The bulk of the water stored in Burrendong Dam is sourced from flood water, which has a low electrical conductivity. The release of this water, maintains a low electrical conductivity in the lower Macquarie River for most of the year. As the electrical conductivity is not increasing with distance down the catchment, this suggests there is limited connectivity between surface water and saline shallow groundwater, which agrees with connectivity studies (Brownbill et al. 2011). The annual salt load at all three End-of-Valley sites exceeded the salt load target during the higher flow years of 2010/2011. Annual median electrical conductivity and salt loads are summarised in Tables 22 and 23 in Appendix D. Draftsman plots for each site have been developed to assess the relationships between parameters. These figures are shown in Appendix E. Sites generally showed a positive correlation between total nitrogen, total phosphorus and turbidity, indicating similar transport mechanisms for the three parameters. This suggests that nutrients are transported in the river system, bound to particulate matter. The highest total nitrogen and total phosphorus concentrations tend to coincide with increased flow. This indicates that the majority of the nutrients are derived from diffuse sources rather than point sources. In addition, there are some high readings during low flow, highlighting there can be a mixture of nutrient sources, such as livestock or release of nutrients from bed sediments. In contrast to nutrients and turbidity, electrical conductivity is negatively correlated to flow and decreases as salts are diluted by increased flow. Generally, as the dissolved oxygen levels increased, so too did the pH. This indicates increased metabolism at these sites is raising the dissolved oxygen and also pushing up the pH.

NSW Department of Planning, Industry and Environment | INT17/243328 | 31 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

3.0 A) 0.5 0.65 2.5 B) 0.4 2.0 0.3 1.5 0.2 TP(mg/L)

TN(mg/L) 1.0 0.5 0.1 0.0 0.0 BellR BellR FishR FishR Little R Little R Little Turon R Turon R Turon Bruinbun Rylstone Bruinbun Rylstone Talbragar Talbragar Yamble Br Yamble Br Yamble Gongolgon Gongolgon Molong Rail Molong Rail Molong Castlereagh BellsBridge Castlereagh BellsBridge Warren Weir Warren Weir Warren Marthaguy Ck Marthaguy Ck Marthaguy DSBurrendong DSBurrendong

225 200 C) 291 605 200 D) 175 150 150 125 100 100 75 TSS (mg/L) TSS 50 50 Turbidity(NTU) 25 0 0 BellR BellR FishR FishR Little R Little R Little Turon R Turon R Turon Bruinbun Rylstone Bruinbun Rylstone Talbragar Talbragar Yamble Br Yamble Br Yamble Gongolgon Gongolgon Molong Rail Molong Rail Molong Castlereagh BellsBridge Castlereagh BellsBridge Warren Weir Warren Weir Warren Marthaguy Ck Marthaguy Ck Marthaguy DSBurrendong DSBurrendong

160 9.0 E) 140 F) 8.5 120 8.0 100 pH 7.5 80 DO(%sat) 60 7.0 40 6.5 BellR BellR FishR FishR Little R Little R Little Turon R Turon R Turon Bruinbun Rylstone Bruinbun Rylstone Talbragar Talbragar Yamble Br Yamble Br Yamble Gongolgon Gongolgon Molong Rail Molong Rail Molong Castlereagh BellsBridge Castlereagh BellsBridge Warren Weir Warren Weir Warren Marthaguy Ck Marthaguy Ck Marthaguy DSBurrendong DSBurrendong

2000 G) 1750 1500 1250 1000 750

EC(µS/cm) 500 250 0 BellR FishR Little R Little Turon R Turon Bruinbun Rylstone Talbragar Yamble Br Yamble Gongolgon Molong Rail Molong Castlereagh BellsBridge Warren Weir Warren Marthaguy Ck Marthaguy DSBurrendong

Figure 13: Water quality data for water quality parameters by site

NSW Department of Planning, Industry and Environment | INT17/243328 | 32 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

5.3.1. Total annual flow Many water quality attributes are strongly correlated to river flow conditions. Flow during the 2010 to 2015 data period was characterised by high flows from 2010 to 2011, and lower flow from 2012 to 2015. Heavy rainfall in 2010 saw the capacity of Burrendong Dam increase from 12% (181 000 ML) up to 119% (1 412 057 ML). There were no significant inflows from 2013 to 2015. Figure 14 illustrates the total annual flow at selected gauging stations from the upland, midland and lowland areas. The use of total annual flow gives a general indication of river flow conditions. No attempt has been made to assess individual results against flow at the time of sampling, or the timing of sampling in relation to high or low flow evets. The general trend at most sites were higher nutrient and turbidity results during the wetter years and lower during dryer years.

1400000

Castlereagh at Hidden Valley 1200000 Bogan River at Neurie Plain Macquarie at Bruinbun Cudgegong at Yamble Bridge Macquarie at Warren Weir Macquarie at Bells Bridge 1000000

800000

600000 Total Annual flow (ML) flow Annual Total

400000

200000

0 2010/2011 2011/2012 2012/2013 2013/2014 2014/2015

Figure 14: Annual flow (ML/year) at selected gauging stations 5.4. Local and expert knowledge Meetings were held with relevant stakeholders and technical experts to gather information and identify water quality issues relevant for the development of the Macquarie Castlereagh WRPA water quality technical report. A list of the meetings held is in Appendix G. Following is a summary of the key water quality issues identified. Cold water pollution from Burrendong Dam – When at full capacity, cold water pollution extends approximately 400 km downstream from Burrendong Dam with little influence from tributaries. Under normal operation, impacts from Windamere Dam are restricted to the immediate vicinity downstream of the dam. As Windamere Dam is located upstream of Burrendong Dam, high volume transfers may occur when there is insufficient supply in Burrendong Dam to meet the requirements of water users in the lower Macquarie Valley. Higher discharges and deeper intakes may be used at these times to transfer a large volume of water, leading to more severe and extensive cold water pollution in the Cudgegong River. Turbidity - Turbidity increases with distance downstream due to increasing intensity of human activity, changing soil types and carp hot spots. The release of the carp virus is still under investigation. There needs to be a water quality allowance to seed the virus and to flush the system of dead fish. There are issues with

NSW Department of Planning, Industry and Environment | INT17/243328 | 33 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

erosion and sediment transport in the Macquarie Marshes. There is increased turbidity in the upper catchment from grazing and livestock access to waterways. River salinity – Salinity was identified as an emerging issue for OEH and the Long Term Watering Plan. Irrigators have hired a consultant to report on the risks of salinity related to environmental watering. River salinity is largely isolated to unregulated tributaries, principally Little River, with elevated levels from Bell River. The electrical conductivity in these tributaries is high, but it is diluted upon entering the Macquarie River. Surface water and groundwater connectivity is not well understood. Anoxic blackwater - Anoxic blackwater was not identified as a major issue during overbank flooding in the Macquarie or Castlereagh catchments. Toxicants – Herbicide and insecticide residues from historical and current agricultural practices, change of land use from grazing to cropping, aerial spraying and spray drift were identified as issues. Chemical residues can also enter the river when irrigation infrastructure fails. Due to the lack of current data, the risk is largely unknown. There is a general concern regarding toxicants associated with the irrigation of cotton. Blue-green algae - Blue-green algae are only an issue for recreational use in Burrendong and Windamere Dams. Algal blooms are rarely detected elsewhere in the Macquarie River, possibly due to high flow from irrigation releases over summer and high turbidity in the lower catchment. Algal blooms are sometimes detected in the Bogan River at Gongolgon during low flows. Pathogens – There are numerous large centres located in the Macquarie Castlereagh WRPA contributing urban runoff to the river system. There is an unknown risk from the high prevalence of septic systems across the catchment. Rubbish – Gross pollutants are a concern at Dubbo. The issue is being addressed through an education program. As approximately 75% of the river corridor is managed privately, engaging with landholders was identified as a priority. Other issues raised included major barriers to fish passage, supporting refugia, protecting flow events, releasing water to mimic natural flow events, discretionary or more effective use of supplementary/environmental water, ammonia production in the Marshes, concerns over gauging stations being taken off-line without consultation with water users and water managers and addressing water quality data gaps. The issue of whether the volume of environmental water currently available is enough to be effective was also raised. There have been numerous projects undertaken to help address water quality in the Macquarie Castlereagh WRPA. These include, but not limited to:  RiverSMART (Non-Government Organisation) is focusing on water quality and riparian work around Warren;  FISH friendly irrigators program;  Habitat mapping and identifying riparian pressures to produce spatial layers for the Macquarie, and  Small habitat action grants, working on improving river geomorphology. 5.5. Risk assessment The impact of the quality of the water in Macquarie and Castlereagh waterways to the health of water dependent ecosystems was assessed by identifying the risk. This was achieved by quantifying the impact based on instream values (consequence) and determining the probability of that consequence occurring (likelihood). Tables 12 to 16 list the sites with medium and high risk scores in the Macquarie Castlereagh Risk Assessment for each parameter. Burrendong and Windamere Dams and Chifley Reservoir were all rated as having a high likelihood of algal blooms. When algal blooms occur, the level of human exposure can be reduced by implementing management practices. The risk at a site with a high recreational usage can be reduced by the management

NSW Department of Planning, Industry and Environment | INT17/243328 | 34 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

strategies of issuing algal alerts, placing algal warning signs at the site and informing users of the risks and dangers. The consequence values reflect these arrangements and were calculated as being low for all sites in the Macquarie Castlereagh WRPA. The risk rating from blue green algae to recreational water use at Burrendong and Windamere Dams and Chifley Reservoir was medium and all other sites low. The risk to the health of water dependent ecosystems in the Macquarie River at Bells Bridge from salinity was high, while the risk at Bogan River at Gongolgan and Castlereagh River at Gungalman was medium. The suitability of water for irrigation at the Macquarie River at Baroona was low risk. The risk to the health of water dependent ecosystems from the release of cold water from Windamere Dam was low, and high for Burrendong Dam.

Table 12: Sites with high and medium risk to the health of water dependent ecosystems from turbidity

Station Name Consequence Likelihood Level of Risk Talbragar River at Elong Elong Low High Medium Macquarie River at Warren Weir Very high High High Marthaguy Creek at Carinda Very high High High Macquarie River at Bells Bridge Very high Medium High Bogan River at Gongolgan Medium Medium Medium

Table 13: Sites with high and medium risk to the health of water dependent ecosystems from total phosphorus

Station Name Consequence Likelihood Level of Risk Macquarie River at Bruinbun Medium Medium Medium Cudgegong River at Yamble Bridge High High High Macquarie River at Molong Rail Bridge Very high Medium High Talbragar River at Elong Elong Low High Medium Macquarie River at Warren Weir Very high High High Marthaguy Creek at Carinda Very high High High Macquarie River at Bells Bridge Very high High High Bogan River at Gongolgan Medium High Medium Castlereagh River at Mendooran Low High Medium

Table 14: Sites with high and medium risk to the health of water dependent ecosystems from total nitrogen

Station Name Consequence Likelihood Level of Risk Cudgegong River at Rylstone Medium Medium Medium Macquarie River D/S Burrendong Dam Low High Medium Macquarie River at Molong Rail Bridge Very high Medium High Talbragar River at Elong Elong Low High Medium Macquarie River at Warren Weir Very high Medium High Marthaguy Creek at Carinda Very high Medium High Macquarie River at Bells Bridge Very high High High Bogan River at Gongolgan Medium High Medium

NSW Department of Planning, Industry and Environment | INT17/243328 | 35 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Table 15: Sites with high and medium risk to the health of water dependent ecosystems from pH

Station Name Consequence Likelihood Level of Risk Macquarie River at Bruinbun Medium Medium Medium Little River at Arthurville High Medium Medium Macquarie River at Molong Rail Bridge Very high Low Medium Macquarie River at Warren Weir Very high Low Medium Marthaguy River at Carinda Very high Low Medium Macquarie River at Bells Bridge Very high Low Medium Table 16: Sites with high and medium risk to the health of water dependent ecosystems from dissolved oxygen

Station Name Consequence Likelihood Level of Risk Cudgegong River at Rylstone Medium Medium Medium Cudgegong River at Yamble Bridge High High High Bell River at Newrea Medium High Medium Little River at Arthurville High Medium Medium Macquarie River at Molong Rail Bridge Very high High High Talbragar River at Elong Elong Low High Medium Macquarie River at Warren Weir Very high High High Marthaguy Creek at Carinda Very high Medium High Macquarie River at Bells Bridge Very high Low Medium Castlereagh River at Mendooran Low High Medium 6. Discussion Water quality attributes in the Macquarie Castlereagh WRPA are strongly correlated to flow at most sites. High flow from rainfall and runoff can result in higher turbidity, nutrients and possibly pesticides and pathogens, but lower electrical conductivity. The Basin Plan water quality targets were developed using data collected from 1991 through to 2009 to try and incorporate a spread of climatic and flow conditions (Tiller and Newall 2010). It was noted that although the time period covered a range of conditions, the data used was primarily collected at base or low flow, and generally missed high flow and flood events. It should be noted that as the Basin Plan targets refer to low flow conditions, targets for flow dependent attributes are likely to be exceeded in wetter years. There was a general trend of higher nutrient and turbidity results in the wetter years of 2010 and 2011, with many very high results collected in these years. There is a general trend toward increasing turbidity, total nitrogen and total phosphorus concentrations with distance down the catchment as cumulative impacts increase. The four sites rated as poor are all located at the bottom of the WRPA. A poor rating may be as a consequence of an inappropriate target, rather than an indication of the quality of the water at a particular site. This issue will be addressed further in the WQMP. 6.1. Elevated levels of salinity Electrical conductivity in the upland region is mostly low and negatively related to discharge with the highest electrical conductivities occurring during low and cease to flow periods. Progressing down the catchment, electrical conductivity levels are low for the majority of the midlands area, though there are localised areas in some tributaries with naturally occurring higher salinities such as the Little and Talbragar Rivers. The highest salinities in these tributaries occur during low and cease to flow periods when there is a higher contribution to base flow from groundwater, or salts are concentrated in pools by evaporation.

NSW Department of Planning, Industry and Environment | INT17/243328 | 36 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

The median data from the unregulated catchments shows an increase in electrical conductivity following the commencement of heavy rainfall across the catchment in July/August 2010. McGeoch et al. (2017) hypothesised that an episodic decline in salinity in NSW rivers during the 2000’s may have been due to extended drought conditions. Long periods of low rainfall can cause a drop in shallow groundwater levels, resulting in a disconnection between saline groundwater and fresher surface water, causing the observed lower salinity levels in streams. The return of wetter conditions in 2010 would have recharged shallow water tables, increasing the contribution of groundwater to low flows, raising the electrical conductivity. Generally the electrical conductivity was increasing until 2014 and then declining again. This trend is masked by data gaps at the Talbragar and Castlereagh River monitoring sites. Future monitoring will show whether recent salinity observations in unregulated catchments persist at current levels or continue to decrease across all sites as shallow saline groundwater aquifers decline. The highest mean daily electrical conductivity results were in the Little River at Obley. Irrigation is limited in the Little River catchment due to low flows, so the risk of crop damage and increased soil salinity is low. The high electrical conductivity in Little River may also be influencing the low turbidity and total suspended solids results, with salts causing suspended material to settle out of the water column. There is an increase in electrical conductivity in the Cudgegong River at Yamble Bridge. In the steeper areas around the locality of Goolma, there is high to extreme electrical conductivity at some sites. Large salinity spikes of up to 18 000 µS/cm can occur in events which last from days to weeks in local streams (DoIW 2018c). The electrical conductivity in the Macquarie River downstream of Burrendong Dam shows a different relationship between electrical conductivity and flow to the other monitoring sites. Prior to the flooding, the median electrical conductivity downstream of Burrendong Dam was stable between 300 and 350 µS/cm. Floodwaters are characterised by high electrical conductivity in the first flush and then much lower readings. The volume of floodwater reduced the median electrical conductivity to less than 250 µS/cm. As this water was released, and more saline tributary base flows entered the dam, the electrical conductivity increased again. The Narromine Irrigation Board of Management is the only irrigation infrastructure operator in the Macquarie Castlereagh WRPA. Water is pumped from the Macquarie River at Narromine and diverted to the irrigation area. The 95th percentile of the daily mean electrical conductivity in the Macquarie River at Baroona did not exceed the 957 µS/cm target for irrigation. The mean daily electrical conductivity in the Macquarie River at Baroona fluctuated throughout the year only exceeding the agriculture and irrigation target for a few days in September 2007 and July and August 2011. As the higher results were in the cooler months when there is less water utilised for irrigation, the risk of impacts on soil and crop health is minimised. The electrical conductivity of surface water in the lowlands area is generally considered excellent for irrigation purposes, but can be higher in low flow periods. The risk to the health of water dependent ecosystems in the Macquarie River at Bells Bridge (End-of-Valley site) from salinity was high. Brock et al. (2005) showed that aquatic plant germination and species richness decreased when salinities increase above 300 mg/L. Similarly for zooplankton hatching, the Macquarie Marshes had significant declines above 300 mg/L. The electrical conductivity at the End-of-Valley site is regularly above these levels. Maintaining low flow in unregulated catchment s and ensuring that freshes are available to the environment helps to break up stratification, provide dilution flows and prevent saline water from sitting on the bottom of pools. This will maintain the health of the river and the continued use of the water for productive purposes. River salinity is not a major issue in the lower Macquarie valley. Water released from Burrendong Dam has a low electrical conductivity and dilutes saline inflows from tributaries downstream, ensuring water is suitable for irrigation and the protection of water dependent ecosystems. A salinity assessment needs to consider land salinity, salt load and stream electrical conductivity in an integrated framework to determine the hazard of a landscape. The Macquarie Castlereagh valley salinity technical report (DoIW 2018c) uses the Hydrogeological Landscapes (HGL) framework to undertake an assessment, as well as determine the likely cause and identify solutions. In addition, salinity modelling was used to assess catchment behaviour, define problem areas and quantify impacts. The use of discrete and continuous long term salinity data in these modelling frameworks increased both the accuracy and utility of the salinity models. The salinity assessment in the Macquarie Castlereagh valley salinity technical report will

NSW Department of Planning, Industry and Environment | INT17/243328 | 37 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

inform and give support to the WQMP and identify water, land and vegetation measures to increase productivity and environmental sustainability. 6.2. Elevated levels of suspended matter The draftsman plots show there is generally a linear relationship between turbidity and total suspended solids in the Macquarie Castlereagh WRPA, except for the upper catchment where the relationship is masked by the total suspended solids lower detection limit of 5 mg/L. Turbidity and suspended sediments are closely related to discharge, with a general trend of increasing turbidity with distance down the catchment. High turbidity and suspended sediments are issues throughout most of the lowlands area. High levels of turbidity are likely influenced by a number of factors including the wide spread conversion of land for cropping and irrigation, bank and riparian condition, and presence of invasive carp. Rapidly ascending and descending limbs of the hydrograph during irrigation releases may also be responsible for channel erosion downstream of Burrendong Dam. Three sites had a high risk for turbidity, namely the Macquarie River at Warren Weir and Bells Bridge and Marthaguy Creek at Carinda. The Warren Weir site is located at the bottom of the upland zone, where it receives the cumulative impacts from upstream. The Basin Plan turbidity target was not exceeded at this site every year, indicating that the target is appropriate. Marthaguy Creek is ephemeral, mostly receiving flows via regulation through the Macquarie Marshes. The fertile alluvial soils in the lower Macquarie valley have a high clay content which increases their susceptibility to resuspension within the water column. The very fine clay particles in these lowland rivers can remain suspended in the water column during low and zero flow, resulting in high turbidity. Turbidity issues in the Macquarie Marshes are also influenced by grazing practices and presence of invasive feral pigs. Stock trampling causes removal of groundcover, pugging, destabilising soils and erosion of stream banks which can all lead to increases in turbidity (Holmes et al. 2009). Carp can contribute to increased turbidity by stirring up sediments when feeding, uprooting aquatic vegetation, and increasing bank destabilisation (Koehn 2004). Carp are common throughout most of the WRPA and the Macquarie Marshes have been identified as a carp breeding hot-spot for the Murray-Darling Basin (Gilligan et al. 2009). The Talbragar River at Elong Elong had high turbidity results but was not identified as a risk due to the low consequence score. Turbidity in the Talbragar River is exacerbated by areas with high erosion risk, and reaches where bank and riparian condition are poor. River Styles® recovery potential (Figure 15) is synonymous with geomorphic condition. Recovery potential represents geomorphic stability and can indicate the capacity of a stream to return to good condition or to a realistic rehabilitated condition (Brierley and Fryirs 2005). Streams rated as having conservation or rapid recovery potential are likely to be the most stable and in a good condition, whereas streams with low recovery potential may never recover to a natural condition or may continue to decline quickly without intervention (Cook and Schneider 2006). The highest priority for intervention action is the strategic recovery potential reaches. These are reaches of river that may be sensitive to disturbance, triggering impacts that can have off-site effects. Particular emphasis should be placed on reaches or point-impacts (nick-points), where disturbances may threaten the integrity of remnant or refuge reaches. Figure 15 identifies strategic recovery potential reaches throughout the Macquarie Castlereagh catchment. Proactive management strategies in these areas are the most effective means of river conservation, leading to improvements in water quality.

NSW Department of Planning, Industry and Environment | INT17/243328 | 38 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Figure 15: River styles recovery potential in the Macquarie Castlereagh WRPA

There is a long reach of low recovery potential on the Macquarie River downstream of Burrendong Dam. A threat to the recovery potential of this reach is the lack of sediment delivered from the upper catchment. Burrendong Dam acts as a large trap, restricting the movement of sediment down the catchment. As well as providing more suitable conditions within the dam for the production of harmful algal blooms, the reduced sediment load restricts the development of low level benches and bars in the Macquarie River downstream, reducing the river complexity and the recovery potential. There are large portions of the Castlereagh, Talbragar, Bell, Little and upper Macquarie catchments with low recovery potential indicating likely sources of suspended sediment from stream bank erosion. In the unregulated catchments, land and vegetation management are the key drivers for sediment entering waterways. The principal factor generating high sediment loads (and associated nutrients) is the loss of vegetation in the catchment and/or the riparian zone, leading to increased hillslope, gully and bank erosion and suspended sediment loads in the river. The main sources of sediment are gully erosion in degraded areas and hillslope erosion where cover is seasonally low through grazing or tillage of cropped lands (National Land and Water Resources Audit 2001). The implementation of flow rules in these catchments will have little impact on reducing sediment inputs. In the regulated system, reducing the extent of bank erosion and slumping is possible through a more natural, gradual rising and falling limbs of water releases from Burrendong Dam and during bulk water transfers from Windamere Dam.

NSW Department of Planning, Industry and Environment | INT17/243328 | 39 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

6.3. Elevated levels of nutrients The highest nitrogen and phosphorus concentrations in the Macquarie Castlereagh WRPA are in the lowlands area downstream of Dubbo and in the Talbragar River. Nitrogen and phosphorus concentrations generally followed similar trends, indicating similar transport processes are driving both parameters. Nutrient concentrations are generally driven by runoff and erosion during rainfall events with higher concentrations at high flow. In addition, some of the higher nutrient concentrations at some sites occur during low or cease to flow periods. This suggests the sources of nutrients can be mixed. The lower results were in the Turon and Fish Rivers in the upper catchment. Most of the uplands area has moderate soil nutrient concentrations, though there are areas around Bathurst and Orange with higher total nitrogen and total phosphorus (Figures 16 and 17), which may be contributing to the high nutrient concentrations found in the Macquarie River at Bruinbun. Soil erosivity can be exacerbated by the historical conversion of forested land to grazing, particularly clearing in the riparian zone. Access of livestock to the river may be a source of nutrients and turbidity. Septic tanks have also been suggested as possible sources of nutrients. Concentrations of total nitrogen and total phosphorus in the Talbragar River at Elong Elong are above the respective Basin Plan targets, resulting in one of the lowest WaQI scores of 31. Similar to turbidity, as the Talbragar River has a low consequence score, the risk to aquatic ecosystems was medium. The nutrient concentrations at this site are likely to exceed the Basin Plan targets most years. It must be determined if more appropriate targets need to be developed, or accept that the river is degraded, and the low WaQI score is an accurate reflection of the quality of the water.

MACQUARIE CASTLEREAGH WATER RESOURCE PLAN AREA - SOIL TOTAL NITROGEN

QUAMBONE COONAMBLE " "

BINNAWAY GILGANDRA " "

DUBBO "

WELLINGTON MUDGEE " "

n i s a B ORANGE g n " li r BATHURST a D " y a rr u M

Data Sources: NSW Industry I Lands & Water I Water. " Towns Soil Total Nitrogen 0-5cm Office of Environment and Heritage. Murray Darling Basin Authority. Value Rivers Geoscience Australia. High : 0.776694 ± Macquarie Castlereagh boundary 0 20 40 60 80 Low : 0.030852 Map produced by NSW Industry I Lands & Water 22 August 2018 kilometres Figure 16: Soil total nitrogen (0 to 5 cm) for the Macquarie Castlereagh WRPA

NSW Department of Planning, Industry and Environment | INT17/243328 | 40 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

MACQUARIE CASTLEREAGH WATER RESOURCE PLAN AREA - SOIL TOTAL PHOSPHORUS

QUAMBONE COONAMBLE " "

BINNAWAY GILGANDRA " "

DUBBO "

WELLINGTON MUDGEE " "

n i s a B ORANGE g n " li r BATHURST a D " y a rr u M

Data Sources: NSW Industry I Lands & Water I Water. " Towns Soil Total Phosphorus 0-5cm Office of Environment and Heritage. Murray Darling Basin Authority. Value Rivers Geoscience Australia. High : 0.270717 ± Macquarie Castlereagh boundary 0 20 40 60 80 Low : 0.0111924 Map produced by NSW Industry I Lands & Water 22 August 2018 kilometres Figure 17: Soil total phosphorus (0-5 cm) for the Macquarie Castlereagh WRPA

The Macquarie River at Molong Rail Bridge, Warren Weir and Bells Bridge and Marthaguy River at Carinda had total nitrogen and total phosphorus concentrations at high risk of impacting the health of water dependent ecosystems. These four sites had a very high consequence score. The very fine clay particles in these lowland rivers remain suspended in the water column during low and zero flow, resulting in high turbidity and associated nutrients under all flow conditions. The Marthaguy Creek and Macquarie River at Bells Bridge sites are located downstream of the Macquarie Marshes. In wetter years, floodwater flows through the Marshes, making its way eventually to the Barwon River. The highly fertile alluvial clay soil on the floodplain, combined with the high productivity of the wetland, provides a rich source of nutrients. The Warren Weir monitoring site is located at the bottom of the upland zone, where it is receiving the cumulative impacts from upstream. Nutrient concentrations for most of the midland zone remain within targets. The landuse in the region is dominated by grazing with some cropping of the more fertile soils. The fertile soils associated with cropping and irrigation in the lowland area is a potential source of excess nutrients. Pre watering releases following periods of low flow over winter, may be re-suspending nutrients bound up in sediments on the river bed, and bank erosion on the rising limb of the hydrograph. As for sediment, land management is the key driver for nutrients entering waterways in unregulated rivers. The implementation of flow rules upstream of Windamere and Burrendong Dams will have little impact on nutrient management. In the regulated system, reducing the extent of eutrophication caused by bank slumping is possible through a more natural, gradual rising and falling limbs on water releases. 6.4. Elevated levels of cyanobacteria Harmful algal blooms are a regular occurrence in Windamere Dam, with the numbers of potentially toxic blue- green algae reaching the red alert level for recreational use most summers. Nutrient rich inflows from the upper catchment combined with warm, still water during summer provide ideal conditions for algal growth. Red alerts were not as frequent in Burrendong Dam, but was still rated as having a medium risk to recreational water users. Phosphorus and nitrogen concentrations are generally not limiting to algal growth in the Macquarie Castlereagh WRPA. Harmful algal blooms are common in the major storages, however they are rare in the

NSW Department of Planning, Industry and Environment | INT17/243328 | 41 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Macquarie River, indicating that other factors such as flow, turbidity and light availability are the limiting factors. The release of large volumes of water for irrigation over summer means the turbulent, high velocity water is not suitable for algal growth. Nutrient management in the catchment area of Windamere and Burrendong Dams and Chifley Reservoir is essential to reduce the risk of algal blooms within the dams. When algal blooms do occur, the level of human exposure can be reduced by implementing the established algal management framework. The risk at a site with a high recreational usage can be reduced via the management strategies of erecting algal warning signs and informing users of the health risks, dangers and symptoms of ingesting or coming into contact with blue- green algae. Risks to town water supplies can also be reduced through water treatment processes. 6.5. Water temperature outside natural ranges Cold water pollution is hindering ecological responses in the Macquarie River. Burrendong and Windamere Dams were ranked by Preece (2004) as having severe and minor cold water impacts respectively. Windamere Dam has a multi-level intake tower installed to release water from a selected depth. DSNR (2003) indicated that intakes are typically positioned within the thermocline. However, the use of multiple intakes may result in a proportion of hypolimnetic water being released. Under normal operating conditions, discharges are typically small. The small discharge and shallow withdrawal depth limit the size and scale of the thermal impact below this dam. As Windamere Dam is upstream of Burrendong Dam, high volume transfers may occur when there is insufficient supply in Burrendong Dam to meet the requirements of water users in the lower Macquarie valley. Higher discharges and deeper intakes may be used at these times to transfer a large volume of water, leading to more severe and extensive CWP in the Cudgegong River. There were no bulk water transfers between 2010 and 2015. During most summers, the water temperature downstream of Windamere Dam is within the 20th and 80th percentiles of the upstream reference site. Though, in some years an impact can be observed. The water temperature at the downstream site is 3 to 5°C colder than the upstream reference site during the summer months. It is possible that the offtakes were set at a lower depth during summer to avoid releasing potentially toxic blue-green algae into the Cudgegong River, impacting on water users. The water temperature returns to a more natural level by the Yamble Bridge monitoring site, which is located approximately 90 km downstream. Burrendong Dam thermally stratifies from spring to autumn. Available data for a full/near full storage in January shows differences between surface and bottom water temperatures of approximately 12°C (25°C and 13°C respectively) (Bowling et al. 1994, 1995; Sherman 2000). As summer releases are typically drawn from the hypolimnion, marked alterations to the natural thermal regime of the Macquarie River occur. Thermal suppression below Burrendong Dam is around 13°C (Gray 2016). Burrendong Dam has been the subject of numerous studies to determine the size and persistence of thermal disturbance below the dam (Harris 1997: Acaba et al. 2000: Burton and Raisin 2001). As a result, a thermal curtain was installed, becoming operational on 7 May 2014. The top of the curtain is designed to hang approximately 3 to 10 m below the water surface to channel warmer water from the surface into the offtake tower and down through the outlet. There is distinct thermal depression at the downstream gauging station during large releases over the summer months from 2010 to 2013, with a difference of over 10°C between the upstream and downstream sites. The impact is not as marked in the 2014 to 2016 releases with the difference less than 5°C. This may be as a result of the installation of the thermal curtain in May 2014, in conjunction with storage capacity being back down to below 30%, reducing the depth of water at the outlet. When Burrendong Dam is at or near full capacity, the extent of cold water impacts appear to extend beyond the Baroona gauging station which is 163 kms downstream of Burrendong Dam. Water temperature has returned to a more normal regime by Marebone Weir which is located approximately 400 km downstream. As there are no long term monitoring sites between Baroona and Marebone Weir, an accurate measurement of the extent of cold water pollution cannot be made. When Burrendong Dam is at a lower capacity, and with the installation of the thermal curtain, the extent of cold water pollution may only be as far as Baroona. Further water temperature monitoring when Burrendong Dam returns to full capacity is vital to test the true value of the thermal curtain.

NSW Department of Planning, Industry and Environment | INT17/243328 | 42 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

The issue of cold water pollution cannot be mitigated through the use of flow rules in the WRP, environmental flows or adjustments to release patterns. Ongoing investigations will determine if the thermal curtain can effectively mitigate thermal pollution in the Macquarie River. 6.6. Dissolved oxygen outside natural ranges The dissolved oxygen levels at most sites was within the Basin Plan target range for the majority of the monitoring period, however there was a high degree of variability within and between sites through time. During low and cease to flow periods, dissolved oxygen levels can become unpredictable and fluctuate from very high to very low. These variations are primarily driven by the response of instream biota in these rivers. High organic carbon, nutrients and water temperatures result in increased microbial respiration. Inversely, high turbidity and suspended sediment during these times reduces light availability, reducing primary production by aquatic plants. A comparison of dissolved oxygen data shows that the lower results were during the low flow years of 2007 to 2010 indicating respiration is outpacing oxygen replenishment. Dissolved oxygen results increased across the WRPA after the flooding in 2010 to 2011 in response to nutrient inputs and turbulence from increased flow velocity. Some sites (Little River at Arthurville, Turon River at Bathurst Point, Macquarie River at Bells Bridge and Bogan River at Gongolgon) became supersaturated, with oxygen levels up to 190% saturation. This indicates the ecosystem metabolism was out of balance, likely due to high nutrient availability, sediment settling out of the water column, increased light penetration and increased photosynthesis from aquatic plant growth at the sites. In addition to these factors, the solubility of oxygen decreases as water temperature increases, resulting in reduced dissolved oxygen levels. Marthaguy Creek at Carinda and Bogan River at Gongolgon are both located at the bottom of the catchment where a combination of low flow and warm water temperature can result in dissolved oxygen levels below the lower target. The Basin Plan dissolved oxygen target ranges were designed specifically to be applied to monthly data, and provide an indication of any issues. Monitoring of dissolved oxygen is currently conducted monthly, however it does not capture the full diurnal variation. To fully capture dissolved oxygen dynamics, continuous monitoring during a range of hydrologic and seasonal conditions is required. As for water temperature, there are no data available on the influence both within and downstream of the numerous weir structures on dissolved oxygen levels the lower Macquarie valley. There is no continuous dissolved oxygen data collected immediately downstream of Burrendong or Windamere Dams. Due to the depth of Burrendong Dam, it is anticipated that the water drawn from below the hypolimnion would have low dissolved oxygen levels. The routine monthly data from the monitoring site downstream of Burrendong Dam shows that the median dissolved oxygen levels are mostly within the Basin Plan upper and lower limits. Due to the close proximity of the monitoring site to the dam wall, the dissolved oxygen results suggest turbulence from the process of releasing the water, re-oxygenates it as it passes through the dam infrastructure and enters the river. The routine monthly data does not identify any critical low dissolved oxygen events, which would be detected by continuous data. Maintaining low and base flows through cease and commence to pump rules and protection of small freshes in unregulated catchments assist to flush or turn over stratified pools. This breaks down the stratification and prevents water on the bottom of pools becoming anoxic and unsuitable for aquatic fauna. In addition, low flows help prevent excessive algal and aquatic macrophyte growth which can result in supersaturated oxygen conditions. Hypoxic blackwater events resulting from the inundation of floodplains during major flooding events or low flow hypoxia during periods of extreme drought have not been identified as an issue in the Macquarie, Castlereagh or Bogan Rivers. 6.7. Elevated levels of pesticides and other contaminants Pesticide residues have been a pollutant in the lower Macquarie valley with concern amongst water managers, industry groups and the community as a whole about the effects of exposure to agricultural chemicals on

NSW Department of Planning, Industry and Environment | INT17/243328 | 43 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

humans and the environment. Pesticide contamination was found to be reducing up until the mid-2000s when monitoring ceased (Muschal 2001). Development and implementation of the cotton industry’s best management practice guidelines and the introduction of genetically modified Bt resistant cotton each contributed to a trend of declining levels of insecticide and herbicide residues in waterways. There are no current monitoring data to determine if the presence of pesticide residues remains an issue in this area. There is a long history of gold mining in the upper Macquarie catchment, initially focused on the Hill End and Sofala areas. Mine water, tailings and tailings dump leachate from any current mining activities is controlled through environmental protection licences under the Protection of the Environmental Operations Act 1997 (POEO Act). There are no current monitoring data on the presence of toxicants such as heavy metals in the Macquarie Castlereagh WRPA. 6.8. pH outside natural ranges Median pH at all sites is generally within the Basin Plan upper and lower limits. No sites were identified as having a pH at high risk of impacting the health of water dependent ecosystems. Figure 18 shows the pH at the soil surface (0-5 cm) increases down the catchment. This trend is not reflected in the water quality monitoring data, indicating additional factors such as the characteristics of soils deeper in the profile, geology and groundwater interactions are also driving pH in the rivers. The pH tends to be more alkaline than acidic.

MACQUARIE CASTLEREAGH WATER RESOURCE PLAN AREA - SOIL pH

QUAMBONE COONAMBLE " "

BINNAWAY GILGANDRA " "

DUBBO "

WELLINGTON MUDGEE " "

n i s a B ORANGE g n " li r BATHURST a D " y a rr u M

Data Sources: NSW Industry I Lands & Water I Water. " Towns Soil pH 0-5cm Office of Environment and Heritage. Murray Darling Basin Authority. Value Rivers Geoscience Australia. High : 7.91633 ± Macquarie Castlereagh boundary 0 20 40 60 80 Low : 3.65925 Map produced by NSW Industry I Lands & Water 22 August 2018 kilometres Figure 18: Soil pH (0 to 5 cm) for the Macquarie Castlereagh WRPA 6.9. Elevated pathogen counts There are no current data on the extent of pathogens in the Macquarie Castlereagh WRPA. It is expected that with ongoing inputs of human and animal waste, and access of stock and animals to rivers and streams, that pathogens would be present in waterways. Higher counts would be expected following rainfall and runoff flushing contaminants from both rural and urban areas into the rivers. Similarly, high counts may be common during low flows where faecal coliforms have appropriate conditions to multiply and in areas with point source pollution.

NSW Department of Planning, Industry and Environment | INT17/243328 | 44 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Large water bird breeding events in the Macquarie Marshes result in naturally high levels of faecal coliforms. The pathogens from these events would largely be restricted to the rookery areas and immediately downstream. There is an unknown risk from the high prevalence of septic systems across the catchment. As for some other pollutants, pathogens cannot be managed through water planning. 6.10. Knowledge gaps Dissolved oxygen Dissolved oxygen data in the Macquarie Castlereagh WRPA is collected monthly, which does not cover the full diurnal variation in the water column. Efforts are made to collect samples at approximately the same time each month to allow comparison at a site through time. However, this can result in some sites having a low median, because the data is routinely collected earlier in the morning, or inversely, high readings because the samples are collected later in the afternoon. The Basin Plan dissolved oxygen targets were developed to accommodate monthly data. However continuous real time data would provide a complete picture of dissolved oxygen variability and could be used as an early warning for catastrophic events such as anoxic blackwater in refuge pools. Water temperature Water temperature in the Macquarie River is monitored continuously at numerous locations both upstream and downstream of Burrendong Dam. There are currently no permanent stations located between the downstream of Burrendong Dam and Baroona sites, a distance of approximately 163 km. Additional sites are required to more accurately monitor the extent of cold water pollution during releases, assess the effectiveness of the thermal curtain and to indicate if the inflows from the two main tributaries below the dam (Little and Bell Rivers) assist in raising water temperature. There is not a permanent water temperature monitoring site located on the Cudgegong River upstream of Windamere Dam. The addition of a site would remove the need to use data from an adjacent catchment to develop reference data, providing a more accurate assessment of cold water impacts. Clearing of vegetation in the riparian zone and poor geomorphic condition can lead to increased sunlight reaching the water surface, resulting in increased water temperatures. The extent and scale of this form of increased thermal pollution is unknown. Event based monitoring The current water quality monitoring program targets low and base flow conditions with limited, high flow event based monitoring. High velocity water is generally required to transport large concentrations and loads of suspended sediment and associated nutrients, pesticides and pathogens. Suspended solids and nutrients tend to increase during high river flow, when particulate matter is washed from the catchment, bank erosion contributes material and/or bed sediments are resuspended in the water column. The high velocity water in the upper catchment is capable of carrying greater quantities of sediment and nutrients. As the stream bed flattens out across the floodplain, these nutrient rich suspended particles fall out of suspension and are deposited on the floodplain and into river sediments. For streams upstream of Burrendong and Windamere Dams, this material is deposited in the dams, settling out of the water column and providing a source of nutrients to sustain algal blooms. The deposition of sediment in the dam results in less material for instream bar and bench formation downstream. Hazard mapping Spatial modelling to develop hazard mapping, utilising the range of data sets available such as, riparian vegetation cover and geomorphic condition, and overlaying soil erosion risk areas, soil nitrogen and soil phosphorus could identify key areas most likely to contribute to poor water quality and guide the implementation of management decisions. In addition, the mapping and identification of high priority refuge pools would assist in the monitoring and delivery of water to maintain water quality suitable for water depended ecosystems during extended dry periods.

NSW Department of Planning, Industry and Environment | INT17/243328 | 45 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Additional water quality monitoring sites The current New South Wales surface water quality monitoring program has been in operation since 2007. It was established and designed to meet the objectives and data requirements at the time. A revision of the state wide water quality monitoring program is required to better meet the requirements of the Basin Plan and to fill identified information gaps. There is a lack of data to inform the impact that regulatory weirs in the Lower Macquarie valley have on the water temperature and dissolved oxygen profiles both within and downstream of the weir. There is currently only one site located at the bottom of the Bogan River catchment. Additional site(s) are required in the upper catchment. Monitoring in the Talbragar River at Elong Elong and Castlereagh River at Mendooran ceased in 2012. The monitoring of these two catchments needs to be reactivated. Agricultural chemical, toxicants and pathogen data There are no current data on the concentration of agricultural chemical residues in the creeks and rivers of the Macquarie Castlereagh WRPA. As large quantities of insecticides and herbicides are used in the catchment, and the main transport mechanisms for their movement in the environment still exist, it is assumed that there is a risk that chemical residues are present in waterways. Without monitoring data, we cannot determine which chemicals are present, when, or the concentration. Similarly, it is assumed there are pathogens present in the waterways and toxicants in some areas, but the data is not available to confirm this. Development of local water quality targets The Basin Plan water quality targets were not found to be inappropriate for the sites assessed, however there is a need to develop salinity targets for all of the Macquarie Castlereagh WRPA. Time frames do not allow for the development of local water quality targets before the completion of the WQMP. Ramsar wetlands Principle threats to the values of the Ramsar sites in the Macquarie Marshes include changes in hydrologic regime through irrigated agriculture and the construction of water diversion structures, impacts of introduced plants on wetland plant communities, grazing and changed fire regimes. Spencer et al. (2010) recommended revegetation of riparian areas and restriction of stock access to waterways as strategies to improve water quality in wetland areas. As there are no routine water quality monitoring sites in the Ramsar listed wetlands, no assessment of water quality targets has been made in this report and cannot be undertaken in future reports unless monitoring sites are added. Ramsar wetlands will be included in the revision of the water quality monitoring program. 7. Conclusion The quality of the water in a river or stream is a reflection of underlying climate and geology and the multiple activities occurring in a catchment area. There are numerous factors contributing to the observed results, many of which are outside the influence of flow management and therefore cannot be addressed through water planning alone. In unregulated catchments, greater emphasis must be focused on preventing pollutants such as sediment and nutrients from entering waterways through land, soil and vegetation management. As sediment is a major transport mechanism for many pollutants, practices such as maintaining groundcover, vegetated buffer strips and good agronomic practices in conjunction with the management of riparian vegetation to reduce stream bank erosion provide simple and effective means to improve water quality. Land and vegetation management will not only address water quality issues in the rivers but also harmful algal blooms in Windamere, Burrendong and Ben Chifley Dams. In the regulated system, the issues of dissolved oxygen, contribution of sediment and nutrients through bank slumping, dissolved organic carbon and to a lesser degree, cold water pollution can be addressed through the implementation of flow rules. There are opportunities for government agencies, including NSW Local Land Services (LLS), Office of Environment and Heritage (OEH), DPI Fisheries and DPI Agriculture to work closely with DoI Water in

NSW Department of Planning, Industry and Environment | INT17/243328 | 46 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

managing external constraints through complementary measures. Collaboration between natural resource management groups to examine alignment of priorities has been a continued focus of NSW Government (NRC 2010). Alignment of natural resource management continues to be identified as a priority for LLS (Local Land Services 2016) and for the management of environmental water and water quality in New South Wales (OEH 2014). Alignment of priorities for river management will assist in strengthening the outcomes of mitigation measures. The information and data analysis from this report will support the development of the Macquarie Castlereagh Water Quality Management Plan (WQMP). Based on the water quality data and information available, water quality objectives for the Macquarie Castlereagh WRPA will be formulated where there are flow ‘levers’ available to water managers. The WQMP will consider the impacts of wider natural resource and land management on water quality within the Macquarie Castlereagh water resource plan area. It will provide a framework to protect and maintain water quality that is ‘fit for purpose’ for a range of outcomes. These uses and activities may include irrigation of crops, maintaining a healthy environment, recreational fishing or cultural and spiritual links to Country for Aboriginal communities.

NSW Department of Planning, Industry and Environment | INT17/243328 | 47 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

References Abbasi, T., and S. A. Abbasi. 2012. Water quality indices. Elsevier. Acaba Z, Jones H, Preece R, Ross D and Daly H. 2000. The effects of large reservoirs on water temperature in three NSW rivers based on the analysis of historical data. Centre for Natural Resources, NSW Department of Land and Water Conservation, Parramatta. Achterberg, E. P. 2014. Grand challenges in marine biogeochemistry. Frontiers in Marine Science 1: 7. Anderson, D. M., P. M. Glibert, and J. M. Burkholder. 2002. Harmful algal blooms and eutrophication: nutrient sources, composition, and consequences. Estuaries 25: 704-726. ANZECC and ARMCANZ. 2000. Australian guidelines for water quality monitoring and reporting. Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand. ISBN 09578245 1 3. APHA. 1995. Methods for the examination of water and waste water. American Public Health Association, Washington, DC. Astles, K. L., R. K. Winstanley, J. H. Harris, and P. C. Gehrke. 2003. Regulated Rivers and Fisheries Restoration Project – Experimental study of the effects of cold water pollution on native fish. SW Fisheries Final Report Series No.44. NSW Fisheries Research Institute. Austin, J., L. Zhang, R. N. Jones, P. Durack, W. Dawes, and P. Hairsine. 2010. Climate change impact on water and salt balances: an assessment of the impact of climate change on catchment salt and water balances in the Murray-Darling Basin, Australia. Climatic change 100: 607-631. Bauer, J. E., W.-J. Cai, P. A. Raymond, T. S. Bianchi, C. S. Hopkinson, and P. A. Regnier. 2013. The changing carbon cycle of the coastal ocean. Nature 504: 61-70. Boulton, A., M. Brock, B. Robson, D. Ryder, J. Chambers, and J. Davis. 2014. Australian freshwater ecology: processes and management. John Wiley & Sons. Bowling L, Martin V, Hindmarsh B and Al-Talib Z. 1994. State of the Storages 1992-1993. Report TS94.070. Technical Services Division, NSW Department of Water Resources, Parramatta. Bowling L, Martin V, Al-Talib Z and Price M. 1995. State of the Storages 1993-1994. Technical Services Division, NSW Department of Water Resources, Parramatta. Boys, C., N. Miles, and T. Rayner. 2009. Scoping options for the ecological assessment of cold water pollution mitigation downstream of Keepit Dam, Namoi River, Murray-Darling Basin Commission. Murray-Darling Basin Commission. Brierley, G and Fryirs K 2005. Geomorphology and river management: application of the river styles framework. Blackwell Publications, Oxford, UK. Brock, M. A., D. L. Nielsen, and K. Crossle. 2005. Changes in biotic communities developing from freshwater wetland sediments under experimental salinity and water regimes. Freshwater Biology 50: 1376-1390. Brookes, A. 1986. Response of aquatic vegetation to sedimentation downstream from river channelisation works in England and Wales. Biological Conservation 38: 351-367. Brown, R. M., N. I. McClelland, R. A. Deininger, and R. G. Tozer. 1970. A water quality index - do we dare? Water Sew Works 117: 339-343. Brownbill, R.J., Lamontagne, S., Williams R.M., Cook, P.G., Simmons C.T. and Merrik, N. 2011. Interconnection of surface and groundwater systems - River losses from losing - disconnected streams. Technical final report , June 2011, NSW Office of Water , Sydney. NOW 11_187.1. Bruton, M. 1985. The effects of suspensoids on fish. Hydrobiologia 125: 221-241. Buckland, S., Abid, A., Scott, B., Lovell, B., Fuller, D. 2008. Final Report – Improving Victoria’s surface water monitoring project – turbidity assessment methods. Prepared for West Gippsland Catchment Management Authority. Burton C and Raisin G. 2001. Assessment of water temperature regime of the Macquarie River, Central West, New South Wales. In: Thermal Pollution of the Murray-Darling Basin Waterways. Phillips (ed.).

NSW Department of Planning, Industry and Environment | INT17/243328 | 48 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Workshop held at Lake Hume 18-19 June 2001, Inland Rivers Network and World Wide Fund for Nature, Sydney, 45-54. Caffrey, J. M. 2004. Factors controlling net ecosystem metabolism in US estuaries. Estuaries 27: 90-101. Caitcheon, G.C., Beavis, S.G., Crapper, P., Deitrich, C.R., Green, T.R., Hancock, G., Jakeman, A.J., Olley, J.M., Olley, J.M., Wallbrink, P.J. and Zhang, L. 1999. Sediment and phosphorus sources in the Namoi River Basin. Compiled and edited by Caitcheon GC. CSIRO Land and Water and Australian National University. Chapman, P. M., F. Wang, C. Janssen, G. Persoone, and H. E. Allen. 1998. Ecotoxicology of metals in aquatic sediments: binding and release, bioavailability, risk assessment, and remediation. Canadian Journal of Fisheries and Aquatic Sciences 55: 2221-2243. Chorus, I., and J. Bartram. 1999. Toxic cyanobacteria in water: a guide to their public health consequences, monitoring and management. Closs, G. B., B. Downes, and A. Boulton. 2009. Freshwater ecology: a scientific introduction. Cook, N. and Schneider, G. 2006. River Styles® in the Hunter Catchment. Science and Information Division, New South Wales Department of Natural Resources, Sydney, NSW. Cormier, S. M. 2006. Ecoepidemiology: a means to safeguard ecosystem services that suport human welfare., p. 57-72. In G. Arapis, N. Goncharova and P. Baveye [eds.], Ecotoxicology, Ecological Risk Assesment and Multiple Stressors: NATO security through science series. Springer. Cormier, S. M., S. B. Norton, and G. W. Suter. 2003. The US Environmental Protection Agency's Stressor Identification Guidance: A process for determining the probable causes of biological impairments. Human and Ecological Risk Assessment: An International Journal 9: 1431-1443. Cude, C. G. 2001. Oregon water quality index a tool for evaluating water quality management effectiveness. Journal of American Water Resources Association 37: 125-137. Davis, J. R., and K. Koop. 2006. Eutrophication in Australian rivers, reservoirs and estuaries - a southern hemisphere perspective on the science and its implications. Hydrobiologia 559: 23-76. Deal, R 1997. Bacteriological quality of the state’s river systems for 1995/1996. CNR97.008. Centre for Natural Resources. Department of Land and Water Conservation, Parramatta. Deal, R and Wood, J. 1998. Bacteriological quality of the state’s river systems for 1996/1997. CNR97.095. Centre for Natural Resources. Department of Land and Water Conservation, Parramatta. ISSN 1329- 6434. Dent, D. and L. Pons. 1995. A world perspective on acid sulphate soils. Geoderma 67: 263-276. Department of Environment, Climate Change and Water. 2010. Macquarie Marshes adaptive environmental managemen plan. NSW Department of Environment, Climate Change and Water, Sydney. ISBN 978 1 74232 604 7. Department of Sustainable Natural Resources. 2003. Windamere Dam operating protocol workshop summary of outcomes. Includes supporting information from presentations. Workshop held 2 May 2003. NSW Department of Sustainable Resources, Sydney. Dinius, S. 1987. Design of an index of water quality. Water Resources Bulletin 23: 823-843. Dodds, W. K. 2006. Nutrients and the “dead zone”: the link between nutrient ratios and dissolved oxygen in the northern Gulf of Mexico. Frontiers in Ecology and the Environment 4: 211-217. DoIW. 2018a. Macquarie Castlereagh water resource plan surface water resource description. Department of Industry, Water. Parramatta. DoIW. 2018b. Risk assessment for the Macquarie Castlereagh water resource plan area (SW11). Department of Industry, Water. Parramatta. DoIW. 2018c. Macquarie salinity technical report. NSW Department of Industry, Water. Parramatta. Environment Protection Authority. 1997. Proposed interim environmental objectives for NSW waters. NSW Environment Protection Autority, Sydney. Erskine, W. D., M. J. Saynor, A. Chalmers, and S. J. Riley. 2012. Water, wind, wood, and trees: Interactions, spatial variations, temporal dynamics, and their potential role in river rehabilitation. Geographical Research 50: 60-74.

NSW Department of Planning, Industry and Environment | INT17/243328 | 49 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Evans, W. R., M. Gilfedder, and J. Austin. 2004. Application of the Biophysical Capacity to Change (BC2C) model to the Little River (NSW). CSIRO Land and Water. Ferguson, C. M., B. G. Coote, N. J. Ashbolt, and I. M. Stevenson. 1996. Relationships between indicators, pathogens and water quality in an estuarine system. Water Research 30: 2045-2054. Fong, T.T. and E. K. Lipp. 2005. Enteric viruses of humans and animals in aquatic environments: health risks, detection, and potential water quality assessment tools. Microbiology and molecular biology reviews 69: 357-371. Gilligan, D., Hartwell, D. and McGregor, C. 2009. Identification of 'hot-spots' of carp reproduction in the Murray-Darling Basin. American Fisheries Society Conference, 30 August - 3 September 2009, Nashville, USA. Gozlan, R. E., E. J. Peeler, M. Longshaw, S. St-Hilaire, and S. W. Feist. 2006. Effect of microbial pathogens on the diversity of aquatic populations, notably in Europe. Microbes and Infection 8: 1358-1364. Gray, J. M., T. F. A. Bishop, and X. Yang. 2015. Pragmatic models for the prediction and digital mapping of soil properties in eastern Australia. Soil Research 53: 24-42. Gray R. 2016. Effectiveness of cold water pollution mitigation at Burrendong Dam using an innovative thermal curtain. Thesis submitted for Master of Science by Research. University of Technology, Sydney. Harris JH. 1997. Environmental rehabilitation and carp control. In: Controlling carp: exploring the options for Australia. Roberts J and Tilzey R. (eds) Proceedings of a workshop 22-24 October 1996, Albury, CSIRO Land and Water, Griffith, 21-36. Heugens, E. H., A. J. Hendriks, T. Dekker, N. M. v. Straalen, and W. Admiraal. 2001. A review of the effects of multiple stressors on aquatic organisms and analysis of uncertainty factors for use in risk assessment. Critical reviews in toxicology 31: 247-284. Herron, N., R. Davis, W. Dawes, and R. Evans. 2003. Modelling the impacts of strategic tree plantings on salt loads and flows in the Macquarie River Catchment, NSW, Australia. Journal of environmental management 68: 37-50. Herron, N., R. Davis, and R. Jones. 2002. The effects of large-scale afforestation and climate change on water allocation in the Macquarie River catchment, NSW, Australia. Journal of Environmental Management 65: 369-381. Hillel, D. 2000. Salinity management for sustainable irrigation: integrating science, environment, and economics. World Bank Publications. Holmes, S., S. Speirs, P. Berney, and H. Rose. 2009. Guidelines for grazing in the Gwydir Wetlands and Macqaurie Marshes. NSW Department of Primary Industries. Hubbard, R., G. Newton, and G. Hill. 2004. Water quality and the grazing animal. Journal of animal science 82: E255-E263. Hudnell, H. K. 2008. Cyanobacterial harmful algal blooms: state of the science and research needs. Springer Science & Business Media. Hurley, T., R. Sadiq, and A. Mazumder. 2012. Adaptation and evaluation of the Canadian Council of Ministers of the Environment Water Quality Index (CCME WQI) for use as an effective tool to characterize drinking source water quality. Water research 46: 3544-3552. James, K. R., B. Cant, and T. Ryan. 2003. Responses of freshwater biota to rising salinity levels and implications for saline water management: a review. Australian Journal of Botany 51: 703-713. Jenkins, K., R. Kingsford, and D. Ryder. 2009. Developing indicators for floodplain wetlands: managing water in agricultural landscapes. Chiang Mai Journal of Science 36: 224-235. Kaushal, S. S. Likens, G.E., Jaworski, N.A., Pace, M.L., Sides, A.M., Seekell, D., Belt, K.T., Secor, D.H. and Wingate R.L. 2010. Rising stream and river temperatures in the United States. Frontiers in Ecology and the Environment 8: 461-466. Kelleway, J. Mazumder, D., Wilson, G.G., Saintilan, N., Knowles, L., Iles, J. and Kobayashi ,T. 2010. Trophic structure of benthic resources and consumers varies across a regulated floodplain wetland. Marine and Freshwater Research 61: 430-440.

NSW Department of Planning, Industry and Environment | INT17/243328 | 50 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Khan, S., S. Mushtaq, and A. Ahmad. 2008. On-farm options for managing stream salinity in irrigation areas: an example from the Murray Darling Basin, Australia. Kingsford, R. T. 2000. Ecological impacts of dams, water diversions and river management on floodplain wetlands in Australia. Austral Ecology 25: 109-127. Kobayashi, T. and A. G. Church. 2003. Role of nutrients and zooplankton grazing on phytoplankton growth in a temperate reservoir in New South Wales, Australia. Marine and freshwater research 54: 609-618. Kobayashi, T., J. Iles, and L. Knowles. 2011a. Are the faecal pellets of kangaroos (Macropus spp.) a source of nutrients and carbon in an inland floodplain wetland during flooding? A preliminary experimental inundation study in the Macquarie Marshes, New South Wales. Australian Zoologist 35: 458-462. Kobayashi, T., T. J. Ralph, D. S. Ryder, and S. J. Hunter. 2013. Gross primary productivity of phytoplankton and planktonic respiration in inland floodplain wetlands of southeast Australia: habitat-dependent patterns and regulating processes. Ecological research 28: 833-843. Kobayashi, T., T. J. Ralph, D. S. Ryder, S. J. Hunter, R. J. Shiel, and H. Segers. 2015. Spatial dissimilarities in plankton structure and function during flood pulses in a semi-arid floodplain wetland system. Hydrobiologia 747: 19-31. Kobayashi, T., D. S. Ryder, G. Gordon, I. Shannon, T. Ingleton, M. Carpenter, and S. J. Jacobs. 2009. Short- term response of nutrients, carbon and planktonic microbial communities to floodplain wetland inundation. Aquatic Ecology 43: 843-858. Kobayashi, T., D. S. Ryder, T. J. Ralph and others 2011b. Longitudinal spatial variation in ecological conditions in an in‐channel floodplain river system during flow pulses. River research and applications 27: 461-472. Koehn, J. D. 2004. Carp (Cyprinus carpio) as a powerful invader in Australian waterways. Freshwater Biology 57: 882-894. Lardicci, C., F. Rossi, and F. Maltagliati. 1999. Detection of thermal pollution: variability of benthic communities at two different spatial scales in an area influenced by a coastal power station. Marine Pollution Bulletin 38: 296-303. LeJeune, J., T. Besser, N. Merrill, D. Rice, and D. Hancock. 2001. Livestock drinking water microbiology and the factors influencing the quality of drinking water offered to cattle. Journal of Dairy Science 84: 1856- 1862. Lessard, J. L., and D. B. Hayes. 2003. Effects of elevated water temperature on fish and macroinvertebrate communities below small dams. River research and applications 19: 721-732. Local Land Services. 2016. State Strategic Plan 2016 - 2026. Local Land Services, NSW. Lugg, A. and C. Copeland. 2014. Review of cold water pollution in the Murray–Darling Basin and the impacts on fish communities. Ecological Management & Restoration 15: 71-79. Lumb, A., D. Halliwell, and T. Sharma. 2006. Application of CCME Water Quality Index to monitor water quality: A case study of the Mackenzie River Basin, Canada. Environmental Monitoring and Assessment 113: 411-429. Lumb, A., T. Sharma, and J.-F. Bibeault. 2011. A review of genesis and evolution of water quality index (WQI) and some future directions. Water Quality, Exposure and Health 3: 11-24. McGeoch, S., Mawhinney, W. and Muschal, M. 2017. Evaluation of water quality data and historical trends in New South Wales rivers, Australia: 1970-2013. New South Wales Department of Primary Industries, Water, Sydney. ISBN978-1-74256-945-1. Marsh, N., J. C. Rutherford, and S. E. Bunn. 2005. The Role of Riparian Vegetation in Controlling Stream Temperature in a Southeast Queensland Stream. CRC for Catchment Hydrology, Monash University. Mawhinney, W. 1998. Liverpool Plains water quality project. Land use, pesticide use and their impact on water quality on the Liverpool Plains. Department of Land and Water Conservation. ISSN 1329-8984. Mawhinney, W. and Muschal, M. 2015. Assessment of Murray Darling Basin Plan water quality targets in New South Wales; 2007 to 2012. New South Wales Department of Primary Industries, Water, Sydney. ISBN 978-1-74256-792-1. Murray-Darling Basin Authority. 2012. Basin Plan: Chapter 9 – Water quality and salinity management plan.

NSW Department of Planning, Industry and Environment | INT17/243328 | 51 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Muschal, M. 2001. Central and North West regions water quality program: 1999-2000 report on Pesticides monitoring. NSW Department of Land and Water Conservation, Parramatta. ISSN 1327-1032. National Health and Medical Research Council, 2008. Guidelines for managing risks in recreational water. Canberra. ISBN 1864962720. National Land and Water Resources Audit. 2001. Australian Agricultural Assessment, 2001. National Land and Water Resources Audit, Canberra. Newman, M. C. 2009. Fundamentals of ecotoxicology. CRC press. NRC. 2010. Progress towards healthy resilient landscapes: Implementing the Standards and Targets and Catchment Action Plans – 2010 Progress report. NSW Natural Resource Commission, Sydney. Viewed 9 February 2017. http://www.nrc.nsw.gov.au/publications. NHMRC and NRMMC. 2011. Australian Drinking Water Guidelines. National Water Quality Management Strategy. National Health and Medical Research Council and Natural Resource Management Ministerial Council, Commonwealth of Australia, Canberra. ISBN Online 1864965118. NSW Government. 2016. Water sharing plan for the Macquarie and Cudgegong regulated rivers water source 2016. NSW Ministry of Health 2013. NSW Guidelines for Drinking Water Management Systems. Health Protection NSW, NSW Ministry of Health, North Sydney, NSW. Norris, R., Liston, P., Davies, N., Coysh, J., Dyer, F., Linke, S., Prosser, I. and Young, B. 2001. Snapshot of the Murray-Darling Basin river condition. Murray-Darling Basin Commission, Canberra, Australia. Nowak, B. 1992. Histological changes in gills induced by residues of endosulfan. Aquatic toxicology 23: 65-83. OEH. 2014. Cooperative management of environmental water to improve river and wetland health in NSW. NSW and Office of Environment and Heritage, Goulburn St, Sydney. Olley, J., and G. Caitcheon. 2000. Major element chemistry of sediments from the Darling–Barwon River and its tributaries: implications for sediment and phosphorus sources. Hydrological Processes 14: 1159- 1175. Oliver, R., S. Mitrovic, and C. Rees. 2010. Influence of salinity on light conditions and phytoplankton growth in a turbid river. River Research and Applications 26: 894-903. Pittock, J., and C. M. Finlayson. 2011. Australia's Murray–Darling Basin: freshwater ecosystem conservation options in an era of climate change. Marine and Freshwater Research 62: 232-243. Preece, R. 2004. Cold water pollution below dams in New South Wales: a desktop assessment. Protection of the Environment Operations Act 1997 (POEO Act) Prss, A. 1998. Review of epidemiological studies on health effects from exposure to recreational water. International journal of epidemiology 27: 1-9. Public Health Act 2010. New South Wales Government, Sydney. Public Health Regulation 2012. New South Wales Government, Sydney. Ralph, T. J., P. P. Hesse, and T. Kobayashi. 2015. Wandering wetlands: spatial patterns of historical channel and floodplain change in the Ramsar-listed Macquarie Marshes, Australia. Marine and Freshwater Research. Rayner, T. S., K. M. Jenkins, and R. T. Kingsford. 2009. Small environmental flows, drought and the role of refugia for freshwater fish in the Macquarie Marshes, arid Australia. Ecohydrology 2: 440-453. Rayner, T. S., R. T. Kingsford, I. M. Suthers, and D. O. Cruz. 2015. Regulated recruitment: native and alien fish responses to widespread floodplain inundation in the Macquarie Marshes, arid Australia. Ecohydrology 8: 148-159. Raupach M.R., Briggs P.R., Ford P.W., Leys J.F., Muschal M., Cooper B., and Edge V. E. 2001. Endosulfan transport:I. Integrative assessment of airborne and waterborne pathways. Journal of Environmental Quality. 30:714-728. Rolls, R. J. Growns, I.O., Khan, T.A., Wilson, G.G., Ellison, T.L., Prior, A. and Waring, C.C. 2013. Fish recruitment in rivers with modified discharge depends on the interacting effects of flow and thermal regimes. Freshwater Biology 58: 1804-1819.

NSW Department of Planning, Industry and Environment | INT17/243328 | 52 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Roulet, N., and T. R. Moore. 2006. Environmental chemistry: browning the waters. Nature 444: 283-284. Rutherford, J. C., N. A. Marsh, P. M. Davies, and S. E. Bunn. 2004. Effects of patchy shade on stream water temperature: how quickly do small streams heat and cool? Marine and Freshwater Research 55: 737- 748. Sadoddin, A., R. A. Letcher, A. J. Jakeman, and L. T. Newham. 2005. A Bayesian decision network approach for assessing the ecological impacts of salinity management. Mathematics and Computers in Simulation 69: 162-176. Sherman B. 2000. Scoping options for mitigating Cold Water Discharges from Dams, CSIRO Land and Water, Canberra, Consultancy Report 00/21. Smith, V. H., S. B. Joye, and R. W. Howarth. 2006. Eutrophication of freshwater and marine ecosystems. Limnology and Oceanography: 351-355. Smith, V. H., G. D. Tilman, and J. C. Nekola. 1999. Eutrophication: impacts of excess nutrient inputs no freshwater, marine and terrestrial ecosystems. Environmental Pollution 100: 179-196. Spencer JA, Heagney EC and Porter JL. 2010. Final report on the Gwydir waterbird and fish habitat study. NSW Wetland Recovery Program. NSW Department of Environment and Climate Change, Sydney. Sposito, G., and S. V. Mattigod. 1977. On the chemical foundation of the sodium adsorption ratio. Soil Science Society of America Journal 41: 323-329. Srebotnjak, T., G. Carr, A. de Sherbinin, and C. Rickwood. 2012. A global Water Quality Index and hot-deck imputation of missing data. Ecological Indicators 17: 108-119. Steele, M., and J. Odumeru. 2004. Irrigation water as source of foodborne pathogens on fruit and vegetables. Journal of Food Protection 67: 2839-2849. Terrado, M., D. Barcel, R. Tauler, E. Borrell, and S. de Campos. 2010. Surface-water-quality indices for the analysis of data generated by automated sampling networks. TrAC Trends in Analytical Chemistry 29: 40-52. Tiller, D. and Newall, P. 2010. Water quality summaries and proposed water quality targets for the protection of aquatic ecosystems for the Murray-Darling Basin. Prepared by Karoo Consulting PTY LTD for the Murray-Darling Basin Authority. Van Oost, K. Quine, T.A, Govers, G., De Gryze, S., Six, J., Ritchie, J.C., McCarty, G.W. and Heckra, G. 2007. The impact of agricultural soil erosion on the global carbon cycle. Science 318: 626-629. Vaze, J., A. Davidson, J. Teng, and G. Podger. 2011. Impact of climate change on water availability in the Macquarie‐Castlereagh River Basin in Australia. Hydrological Processes 25: 2597-2612. Water Act 2007. (Commonwealth). Schedule B – Appendix 1. Watson, G., Bullock, E., Sharpe, C. and Baldwin, D. 2009. Water quality tolerances of aquatic biota of the Murray-Darling Basin. Report to the Murray-Darling Basin Authority. Murray-Darling Freshwater Research Centre, Wodonga. Warne, M. S. J. 2002. Derivation of the Australian and New Zealand water quality guidelines for toxicants. Australasian Journal of Ecotoxicology 7: 123-136. Warne, M. S. J., Batley, G.E., Braga, O., Chapman, J.C., Fox, D.R., Hickey, C.W., Stauber, J.L. and Van Dam, R. 2014. Revisions to the derivation of the Australian and New Zealand guidelines for toxicants in fresh and marine waters. Environmental Science and Pollution Research 21: 51-60. Webb, B. W., D. M. Hannah, R. D. Moore, L. E. Brown, and F. Nobilis. 2008. Recent advances in stream and river temperature research. Hydrological Processes 22: 902-918. Wethered, A. S., T. J. Ralph, H. G. Smith, K. A. Fryirs, and H. Heijnis. 2015. Quantifying fluvial (dis) connectivity in an agricultural catchment using a geomorphic approach and sediment source tracing. Journal of Soils and Sediments 15: 2052-2066. Whitworth, K. L., D. S. Baldwin, and J. L. Kerr. 2012. Drought, floods and water quality: drivers of a severe hypoxic blackwater event in a major river system (the southern Murray–Darling Basin, Australia). Journal of Hydrology 450: 190-198. WHO. 2004. Guidelines for drinking-water quality: recommendations. World Health Organization.

NSW Department of Planning, Industry and Environment | INT17/243328 | 53 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Wilkinson, J., A. Jenkins, M. Wyer, and D. Kay. 1995. Modelling faecal coliform dynamics in streams and rivers. Water Research 29: 847-855. Woodward, K. B., C. S. Fellows, S. M. Mitrovic, and F. Sheldon. 2015. Patterns and bioavailability of soil nutrients and carbon across a gradient of inundation frequencies in a lowland river channel, Murray– Darling Basin, Australia. Agriculture, Ecosystems & Environment 205: 1-8. Young, R. G., C. D. Matthaei, and C. R. Townsend. 2008. Organic matter breakdown and ecosystem metabolism: functional indicators for assessing river ecosystem health. Journal of the North American Benthological Society 27: 605-625. Yu, L., A. García, A. R. Chivas, J. Tibby, T. Kobayashi, and D. Haynes. 2015. Ecological change in fragile floodplain wetland ecosystems, natural vs human influence: The Macquarie Marshes of eastern Australia. Aquatic Botany 120: 39-50.

NSW Department of Planning, Industry and Environment | INT17/243328 | 54 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Appendix A. Water quality monitoring site locations Table 17: Location of water quality monitoring stations in the Macquarie Castlereagh WRPA

Station Station Name Latitude Longitude Number Routine water quality 420004 Castlereagh River at Mendooran -31.820830 149.115959 421004 Macquarie River at Warren Weir -31.733526 147.865895 421011 Marthaguy Creek at Carinda -30.457339 147.684128 421012 Macquarie River at Bells Bridge -30.434581 147.569516 421018 Bell River at Newrea -32.678401 148.948165 421019 Cudgegong River at Yamble Bridge -32.407626 149.333756 421023 Bogan River at Gongolgon -30.347131 146.897567 421025 Macquarie River at Bruinbun -33.137121 149.429521 421038 Cudgegong River at Rylstone Bridge -32.792833 149.971587 421042 Talbragar River at Elong Elong -32.091380 149.066808 421077 Macquarie River downstream Burrendong Dam -32.663771 149.106581 421176 Little River at Arthurville -32.571768 148.724808 42110101 Macquarie River at Molong Rail Bridge -32.283394 148.604304 42110170 Turon River at Bathurst Point -33.075721 149.671343 42110171 Fish River at Hazelgrove -33.564549 149.897926 Blue-green algae 42110001 Burrendong Dam Station 1 -32.671214 149.107563 42110003 Burrendong Dam Station 3 -32.817881 149.244507 42110006 Burrendong Dam Station 6 -32.599824 149.196450 42110032 Burrendong Dam at State Recreation Area -32.688436 149.112563 42110033 Burrendong Dam at Sport and Recreation Area -32.707047 149.124230 42110035 Burrendong Dam at Mookerawa Waters -32.770103 149.158952 42110034 Burrendong Dam at Cudgegong Park -32.621769 149.258116 4210040 Macquarie River downstream Burrendong Dam -32.634547 149.079508 42110021 Windamere Dam Station 1 -32.730656 149.768664 42110024 Windamere Dam (Rec area) Station 4 -32.807322 149.828664 421079 Cudgegong River downstream Windamere Dam -32.707045 149.754775 Continuous electrical conductivity 421004 Macquarie River at Warren Weir -31.733526 147.865895 421011 Marthaguy Creek at Carinda -30.457339 147.684128 421012 Macquarie River at Bells Bridge -30.434581 147.569516 421018 Bell River at Newrea -32.678401 148.948165 421019 Cudgegong River at Yamble Bridge -32.407626 149.333756 421023 Bogan River at Gongolgon -30.347131 146.897567

NSW Department of Planning, Industry and Environment | INT17/243328 | 55 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

421026 Turon River at Sofala -33.083713 149.688946 421039 Bogan River at Neurie Plain -31.773446 147.126198 421040 Macquarie River downstream Burrendong Dam -32.634547 149.079508 421048 Little River at Obley -32.706771 148.552850 421079 Cudgegong River downstream Windamere Dam -32.707045 149.754775 421090 Macquarie River downstream Marebone weir -31.384553 147.692852 421107 Marra Creek at Billybingbone -30.373446 147.190072 421127 Macquarie River at Baroona -32.212370 148.376183 421191 Macquarie River at Yarracoona -33.157482 149.490292 420020 Castlereagh River at Gungalman Bridge -30.310107 147.998113 420017 Castlereagh River at Hidden Valley -31.418155 149.314492 Continuous water temperature 421004 Macquarie River at Warren Weir -31.733526 147.865895 421011 Marthaguy Creek at Carinda -30.457339 147.684128 421012 Macquarie River at Bells Bridge -30.434581 147.569516 421018 Bell River at Newrea -32.678401 148.948165 421019 Cudgegong River at Yamble Bridge -32.407626 149.333756 421023 Bogan River at Gongolgon -30.347131 146.897567 421026 Turon River at Sofala -33.083713 149.688946 421039 Bogan River at Neurie Plain -31.773446 147.126198 421040 Macquarie River downstream Burrendong Dam -32.634547 149.079508 421048 Little River at Obley -32.706771 148.552850 421079 Cudgegong River downstream Windamere dam -32.707045 149.754775 421090 Macquarie River downstream Marebone weir -31.384553 147.692852 421107 Marra Creek at Billybingbone -30.373446 147.190072 421127 Macquarie River at Baroona -32.212370 148.376183 421191 Macquarie River at Yarracoona -33.157482 149.490292 420020 Castlereagh River at Gungalman Bridge -30.310107 147.998113 420017 Castlereagh River at Hidden Valley -31.418155 149.314492

NSW Department of Planning, Industry and Environment | INT17/243328 | 56 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Appendix B. Water quality index (WaQI) method A water quality index is a tool to communicate complex and technical water quality data in a simple and consistent way. It is useful for presenting information with different units (e.g. mg/L and %saturation) or characteristics (e.g. turbidity in a montane river versus a lowland river) on a common scale. It can also be used as a reporting tool for evaluation of changes in water quality over the life of a water quality management or water sharing plan. For water quality management plans (WQMP) the WaQI is calculated as an overall integrated index (for five to eight parameters) and for each water quality parameter individually. These calculations are performed independently. The overall WaQI for the WQMP includes total nitrogen, total phosphorus, turbidity, dissolved oxygen and pH. It is based on the exceedance of water quality targets as prescribed in Schedule 11 of The Basin Plan. Blue- green algae, salinity and temperature are calculated as individual parameters. To calculate the index a minimum of 30 samples is required across a five year period with a minimum of four samples in any one year. The outcome provides a number between 1 and 100 that is categorised according to the following:

The index for both the overall score or, for an individual parameter is calculated as: √퐹12 + 퐹22 푊푎푄퐼 = ( ) 1.41421

Where F1 (frequency), the frequency of the number of failed tests per total tests, is: 푁푢푚푏푒푟 표푓 푓푎푖푙푒푑 푡푒푠푡푠 퐹1 = ( ) × 100 푇표푡푎푙 푛푢푚푏푒푟 표푓 푡푒푠푡푠

And where F2 (amplitude), the amplitude is the amount a value exceeded he target, is: 퐹2 = (푛푠푒 ÷ [0.01푛푠푒 + 0.01])

Where nse (the normalised sum of excursions) is: ∑푛 푒푥푐푢푟푠푖표푛 푖 푛푠푒 = ( 푖=1 ) 푛푢푚푏푒푟 표푓 푡푒푠푡푠

And where the excursion is: 퐹푎푖푙푒푑 푡푒푠푡 푣푎푙푢푒 푖 퐸푥푐푢푟푠푖표푛 = ( ) 푇푒푠푡 표푏푗푒푐푡푖푣푒 or 푇푒푠푡 표푏푗푒푐푡푖푣푒 퐸푥푐푢푟푠푖표푛 = ( ) 퐹푎푖푙푒푑 푡푒푠푡 푣푎푙푢푒 푖

NSW Department of Planning, Industry and Environment | INT17/243328 | 57 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

How was the method determined? A literature review of existing water quality index methods, purposes and reviews was conducted in 2015. There is extensive literature (over 500 papers), and a wide range of existing methods (more than 100) of calculating water quality indices. A number of individual index methods as well as key text and review papers (e.g. Abbasi and Abbasi 2012; Achterberg 2014; Bauer et al. 2013; Brown et al. 1970; Cude 2001; Dinius 1987; Hurley et al. 2012; Lumb et al. 2011; Srebotnjak et al. 2012; Terrado et al. 2010; Van Oost et al. 2007) were reviewed to determine an appropriate index for New South Wales that is robust and meets requirements. The Canadian Council of Ministers of the Environment (CCME) water quality index (Roulet and Moore 2006) was chosen as method on which to base the WaQI. The key questions that were considered when making this decision were:  Has it been tested and accepted in peer review literature?  How widely is it used?  Can it be used without requiring calibration to biogeographically distinct regions?  Is it flexible, and can it be used with continuous data or toxicants if required?  Has it been tested against ecological indices (e.g. macroinvertebrates)?  Can it be easily presented and understood for reporting? The method has been modified to remove a subindex that included the number of failed parameters. The subindex was excluded as only five to seven parameters will be used to calculate the NSW WaQI. In comparison, the CCME WQI is designed for up to +30 parameters.

NSW Department of Planning, Industry and Environment | INT17/243328 | 58 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Appendix C. Literature Review A Web of Science search was undertaken that always included ‘NSW’ and then one of the following ‘Macquarie River’, ‘Bogan River’, ‘Bell River’, ‘Cudgengong River’, ‘Talbragar River’, ‘Macquarie Marshes’, ‘Burendong Dam’, ‘Windamere Dam’ or ‘Castlereagh River’. On 24 July 2016 this search returned 299 results searching the default database of DoI web of science license. The output is summarised in Table 18. Table 18: Review of published literature

References Subcatchment Description

Evans et al. Little River Modelling approach to test whether afforestation on farmland can reduce 2004 salinity in Little River catchment near Dubbo. Biophysical Capacity to Change - used groundwater flow systems as a framework to estimate groundwater response to land-use change.

Sadoddin et al. Little River Bayesian network tool for managing dryland salinity. Assess ecological impacts 2005 of different management scenarios – habitat fragmentation is a driver of the magnitude of change for different scenarios.

Kingsford 2000 Gywdir wetlands Water quality has had an effect on River Red Gum survival. and Macquarie Marshes (plus Barmah Millewa and, Moira Marshes and Chowilla Floodplain)

Kobayashi et Macquarie Tested response of nutrients, bacteria, algae and zooplankton after al. 2015 Marshes environmental flows to Macquarie Marshes in February 2008. Turbidity was high in channel and in lagoons. Zooplankton numbers were very high in lagoon. Conductivity remained low. Dissolved Oxygen (DO) was very low ~3 at one site in channel and on flood out, but supersaturated in lagoon where primary production was high. Dissolved inorganic phosphorus (DIP) was very high and exceeded was equal to Dissolved inorganic nitrogen (DIN) at four of five sites. Dissolved organic nitrogen (DON) was very high and Dissolved organic phosphorus (DOP) was very high in lagoon. Total nitrogen (TN) and total phosphorus (TP) were very high.

Yu et al. 2015 Macquarie Study examining sediment cores and fossil records. Finds increase in Marshes sedimentation rate and turbidity between 1940-1970. Suggest livestock grazing and building channels and levees to blame. Algal species have shifted from those preferring <7pH to those favouring >8. Suggest this is due to increased erosion with base cations and decrease in acid generating native vegetation.

Rayner et al. Macquarie Studied fish recruitment responses to winter flows in the Macquarie Marshes. 2015 Marshes Temperatures were 4-12°C below spawning threshold for native fish. This promoted spawning of alien fish. Recommend flows consider temperature in order to promote native fish recruitment.

Astles et al. Experiment, Experiment manipulated the temperature of water out of Burrendong Dam. 2003 Macquarie River Silver perch grown in warmer temperatures (18-24°C) grew longer and heavy than those in cooler (12-14°C). Both Silver Perch and Murray Cod showed behavioural preferences for warmer water.

NSW Department of Planning, Industry and Environment | INT17/243328 | 59 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Preece 2004 Murray-Darling Cold water pollution persists 300-400km downstream of Burrendong dam. Basin

Boys et al. Murray-Darling Review of water temperature and fish breeding in Murray Darling Basin. 2009 Basin

Gray 2016 Burrendong In 2013, water temperature ranges downstream of Burrendong Dam were only Dam briefly met for Golden Perch episodically near the end of the spawning season and not at all for Murray Cod and Silver Perch.

Wethered et al. Coolbaggie Used tracers to find contributions between sub and top soils. Found that whilst 2015 Creek catchment topsoils contribute up to 39% of sediment in headwater, within 25km of (tributary of the headwaters 100% is from subsoil. Subsoils (gully and bank erosion), topsoils Macquarie River (sheet and rill erosion). Partly this is due to reduced flows meaning reduced downstream of lateral connectivity on floodplains (i.e. less water contacting floodplains meaning Dubbo) less sediment from those sources – hillslope sediment gets stuck on floodplain). They focus on fine sediment <63µm as previous studies found it is the worst for turbidity and river health. Top soil makes a greater contribution when cultivation and grazing is present versus forest and woodland. There was visible evidence of channel banks and valley floor gully erosion and little evidence of hillslope erosion. There is a decoupling between hillslopes and channels due to a lack of lateral connectivity, despite erosion still being high. Sediment slugs can cause blackwater effects.

Vaze et al. Murray-Darling Future climate change scenarios mean reduced rainfall and less water in rivers 2011 Basin and dams.

Kobayashi et Macquarie River Measured longitudinal patterns in water quality at multiple sites downstream of al. 2011b downstream of Marebone Weir during November 2006 during low flow year. Electrical Marebone Weir Conductivity (EC), TN, TP, DIP, silica, Dissolved organic carbon (DOC), DON, DOP, DOC/DON and planktonic bacteria all increased longitudinally downstream. TN/TP, DIN/DIP, DOC/DOP, DON/DOP, and Gross Primary Productivity (GPP)/Planktonic Respiration (PR) all decreased downstream. DO, NTU, DIN, GPP, PR and counts of cyanobacteria, algae and zooplankton had localised peaks. Two distinct ecological zones identified: Upstream zone with high DO, turbidity, diatoms and GPP/PR and Downstream zone with high levels of nutrients, DON, cyanobacteria, bacteria and protozoans and cladocerns.

Kobayashi et Macquarie Kangaroo faeces is a source of around 6% of TN, 3% of TP and 8% of DOC al. 2011a Marshes during flooding in Macquarie Marshes.

Kobayashi et Wetlands and GPP and GPP/PR are a function of DOC in channel habitats. GPP, PR and al. 2013 Rivers in GPP/PR in non-channel habitats a function of TN and/or TP. Macquarie, Lachlan and Murrumbidgee

Jenkins et al. Macquarie Compared soils that have been dry for four years versus 14 years. Four years 2009 marshes have greater organic carbon content and when wetted in the lab resulted in much lower DO suggested organic matter is still bioavailable when wetted, less so at 14 years. This also supports increased numbers of taxa.

Rayner et al. Macquarie Fish study. Temperature was warmer before flow event (delivering event brings 2009 Marshes cold water down). DO and EC both reduced following the flow event.

NSW Department of Planning, Industry and Environment | INT17/243328 | 60 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Kobayashi et Macquarie Tested nutrients, DOC, bacteria and phytoplankton responses to flood both in- al. 2009 marshes situ during a release and experimentally. TN concentrations increases rapidly following inundation, followed by TP and DOC. Bacteria and phytoplankton increased with DOC and nutrients rapidly. Increases in TN and TP following inundation led to levels above targets. All factors were higher at sites with canopy rather than open highlighting the importance of riparian vegetation.

Brock et al. Narran Lakes, Tested response to zooplankton hatching and seed germination to different 2005 Gwydir salinities in a range of wetlands. Salinity increases in soils when damp but not wetlands, when flooded. Aquatic plant germination and species richness decreased Macquarie significantly with increasing salinity. These decreases started immediately Marshes, between the lowest treatments of <300 to 1000mg/L. Similar for zooplankton Billybung hatching, Macquarie marshes had significant declines above <300 mg/L, Narran Lagoon, Lake lakes and Gwydir had declines above 1000 mg/L. Community stricture changed Cowal, Great above 1000 mg/L. Increased salinity however had no effects on Lake Cowal, Cumbung Darling anabranch and Great Cumbung Swamp (i.e. up to 5000 mg/L Swamp, Darling treatment). There was no change in community structure. anabranch

Khan et al. Box creek, Article outlining options for on farm control of salinity. 2008 Macquarie River

Herron et al. Macquarie River Suggest planting trees to deal with salinity in the headwaters of the Macquarie 2002 River may reduce inflows to Burrendong Dam

Herron et al. Macquarie River Suggest small scale strategic tree plantings on their own will not be enough to 2003 impacts on salt loads at the end of valley monitoring site. Widespread tree plantings may reduce salt loads but also lead to reductions in water flows in the short term.

Environment Community response to water quality objectives. Protection “Five community discussion meetings were held in early 1998 in Bathurst, Authority 1997 Mudgee, Warren and Dubbo, including a separate meeting in Dubbo with Aboriginal people in the Central West on the proposed environmental objectives. At a further meeting in Nyngan concerns were raised about the discussion paper options relating to Duck and Gunningbar creeks, and town water supplies. Subsequently, over 180 written submissions were received.” Equity between upstream and downstream water users in terms of both quality and quantity was one of the key issues identified. Aboriginal people expressed various concerns about catchment and water management and their effects on cultural and spiritual values, such as a reduction in the quantity and safety of fish, mussels and other traditional foods. They requested opportunities to be actively involved in planning and restoration of rivers. These included potable water supply, agricultural water supply, recreation, production of edible fish and shellfish, aquatic ecosystems, aquatic wildlife, recharging of groundwater, scientific education, aesthetic values, bird-watching, and the simple enjoyment of a healthy river.

Olley and Lowlands Determined sources of sediment and sediment-associated phosphorus in the Caitcheon 2000 Barwon-Darling River. Determined that the sediment in the channel is derived from lowland areas of the catchment and that phosphorus concentrations have not changed significantly in the past 200 years. Suggested that the best strategy to limit excess algal growth is to manage flow so that the river remains turbid and stratification of the pools is prevented.

NSW Department of Planning, Industry and Environment | INT17/243328 | 61 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Kobayashi and Macquarie (Ben Nutrient bioassays showed cyanobacteria was P limited 33%, N/P limited 25% Church 2003 Chifley Dam) and not nutrient limited 42% time. N:P ratio didn’t predict when nutrients were limiting. Zooplankton grazing generally not high enough to supress algae.

Ralph et al. Macquarie Land use, earth works played an important role in geomorphological changes. 2015 Marshes Describes a range of management interventions that have taken place.

Rolls et al. Lowlands and Temperature, flows, habitat and food resource (prey size and availability) all 2013 midlands impair fish recruitment. Flow magnitude and temperature appeared to have the largest effect in determining larval fish composition. Hypothesise that a lack of prey and resources may be one of the reasons why there is not a strong response to managed flow events.

Woodward et Midlands Examined carbon and nutrient inputs from banks under different flow heights. al. 2015 Where river channels have already been impacted by regulated flows, complex surfaces may have been lost, so restoring more natural flows at these levels of channel, may have little immediate impact on nutrient processing. Low level benches will need to be ‘rebuilt’ before environmental flows can increase connectivity.

Austin et al. Macquarie (and Estimates that climate change my reduce water yield in the Castlereagh by up 2010 all of Basin) to 24% by 2030 and 54% by 2070, Macquarie-Bogan by up to 22% by 2030 and 51% by 2070. These numbers are based on the higher resolution model of two scenarios tested. This scenario however is overly optimistic and assumes wide spread change in energy production industry towards less emissions intensive. That is the actual impacts may be much worse. The reduced water yield will lead to decreased salt yield. Paper includes estimates for other valleys.

Nowak 1992 Midlands, Exposure of catfish to endosulfan increased the respiratory stress (increased lowlands diffusion distance).

Kelleway et al. Wetlands Carbon sources supporting consumers are varied and appear related to spatial 2010 distribution of primary producers. Highlights the importance of riparian vegetation as a carbon source, its influence on shading and decreases in in- channel solar radiation limiting in-channel autotrophic production.

Norris et al. Macquarie (and Parts of the Macquarie and Castlereagh valleys were severely impaired. 2001 all of Basin Approximately 42% of the Castlereagh and 29% of the Macquarie has been substantially modified from natural condition.

Muschal 2001 Lowlands The detection of agricultural chemical residues, particularly the insecticide endosulfan in routine water samples was an issue in the Macquarie Valley in the 1990s. The concentrations and frequency of detections were lower in the Macquarie Valley than the more northern cotton growing areas. When pesticide monitoring ceased, the movement of chemical residues into the river system was reducing with the adoption of industry best management guidelines and improved agronomic practices.

NSW Macquarie Macquarie Marshes adaptive environmental management plan intends to inform Department of marshes land and water management, and to guide strategies, projects and tasks for Environment, restoring and maintaining critical ecological functions and habitats in the Climate Marshes. Identified changes to flow regimes include: Change and  Reduction in moderate to high flows in Macquarie River at end of Water system

NSW Department of Planning, Industry and Environment | INT17/243328 | 62 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

 Increase in average period between large flows and reduction in average volume of these events  Reduction in number of small flows likely to cause flooding passing Oxley gauge  Establishment of permanent low flows in previously intermittent streams  Reduction in frequency of floods in the marshes and the area inundated.

Gilligan et al. Murray-Darling Carp do not reproduce uniformly throughout river systems. 18 carp hot-spots 2009 Basin have been identified in the Murray-Darling Basin. In addition, nine other areas have habitat features suggesting that they may act as carp hot-spots when flooded. Seven of these 27 hotspots are much more important than the rest, producing very high numbers of juvenile carp. These include wetlands like the Macquarie Marshes, Namoi wetlands, Gwydir wetlands and Barmah-Millewa Forest. Identifying carp breeding hot-spots is a major step forward in developing an integrated pest management strategy.

NSW Department of Planning, Industry and Environment | INT17/243328 | 63 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Appendix D. Water quality summary statistics Table 19: Water quality summary statistics for the Macquarie Castlereagh WRPA 2007-2015 water quality data

Total Nitrogen (mg/L) Site Name N Mean Std Dev Std Error Min Q10 Q25 Median Q75 Q90 Max

Fish River at Hazelgrove 85 0.47 0.17 0.02 0.20 0.31 0.37 0.41 0.56 0.75 0.97

Turon River at Bathurst Point 86 0.23 0.24 0.03 0.05 0.09 0.12 0.16 0.28 0.37 2.00

Macquarie River at Bruinbun 89 0.60 0.42 0.04 0.08 0.31 0.40 0.55 0.70 0.97 3.70

Cudgegong River at Rylstone Bridge 90 0.67 0.21 0.02 0.39 0.46 0.52 0.65 0.77 0.94 1.50

Cudgegong River at Yamble Bridge 83 0.58 0.26 0.03 0.29 0.35 0.40 0.54 0.66 0.93 2.00

Macquarie River D/S Burrendong Dam 83 0.72 0.22 0.02 0.38 0.49 0.57 0.67 0.85 0.92 1.40

Bell River at Newrea 86 0.52 0.37 0.04 0.19 0.23 0.31 0.41 0.55 0.94 2.20

Little River at Arthurville 73 0.60 0.36 0.04 0.20 0.32 0.40 0.53 0.71 0.89 2.40

Macquarie River at Molong Rail Bridge 66 0.61 0.26 0.03 0.32 0.38 0.42 0.52 0.76 1.00 1.40

Talbragar River at Elong Elong 39 1.02 0.50 0.08 0.24 0.39 0.62 1.10 1.30 1.50 2.70

Castlereagh River at Mendooran 44 0.46 0.32 0.05 0.17 0.18 0.23 0.31 0.62 0.99 1.50

Macquarie River at Warren Weir 63 0.62 0.36 0.05 0.27 0.33 0.41 0.48 0.75 1.00 2.00

Marthaguy Creek at Carinda 34 1.72 0.72 0.12 0.92 1.10 1.20 1.50 1.90 2.70 4.20

Macquarie River at Bells Bridge 49 1.19 0.43 0.06 0.53 0.69 0.91 1.10 1.40 1.80 2.40

Bogan River at Gongolgon 66 0.89 0.28 0.03 0.47 0.62 0.67 0.83 1.00 1.40 1.60

Total Phosphorus (mg/L) Site Name N Mean Std Dev Std Error Min Q10 Q25 Median Q75 Q90 Max

Fish River at Hazelgrove 85 0.028 0.008 0.001 0.013 0.018 0.023 0.027 0.032 0.038 0.055

Turon River at Bathurst Point 86 0.021 0.028 0.003 0.006 0.009 0.012 0.015 0.021 0.028 0.204

Macquarie River at Bruinbun 89 0.049 0.051 0.005 0.010 0.022 0.027 0.038 0.051 0.091 0.473

Cudgegong River at Rylstone Bridge 90 0.032 0.019 0.002 0.013 0.019 0.022 0.026 0.032 0.057 0.111

NSW Department of Planning, Industry and Environment | INT17/243328 | 64 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Cudgegong River at Yamble Bridge 83 0.047 0.024 0.003 0.013 0.023 0.028 0.043 0.058 0.074 0.154

Macquarie River D/S Burrendong Dam 83 0.032 0.027 0.003 0.010 0.016 0.020 0.026 0.031 0.051 0.179

Bell River at Newrea 86 0.049 0.052 0.006 0.012 0.024 0.027 0.035 0.049 0.069 0.328

Little River at Arthurville 73 0.030 0.039 0.005 0.005 0.013 0.016 0.021 0.030 0.044 0.300

Macquarie River at Molong Rail Bridge 66 0.037 0.021 0.003 0.010 0.019 0.024 0.031 0.042 0.064 0.126

Talbragar River at Elong Elong 39 0.231 0.153 0.025 0.062 0.096 0.125 0.190 0.317 0.450 0.754

Castlereagh River at Mendooran 44 0.083 0.064 0.010 0.019 0.029 0.037 0.060 0.089 0.187 0.260

Macquarie River at Warren Weir 63 0.059 0.062 0.008 0.010 0.022 0.027 0.040 0.063 0.098 0.394

Marthaguy Creek at Carinda 34 0.343 0.192 0.033 0.118 0.156 0.176 0.280 0.504 0.660 0.736

Macquarie River at Bells Bridge 49 0.117 0.074 0.011 0.028 0.032 0.080 0.108 0.134 0.226 0.381

Bogan River at Gongolgon 66 0.099 0.064 0.008 0.038 0.047 0.057 0.074 0.107 0.200 0.333

Turbidity (NTU) Site Name N Mean Std Dev Std Error Min Q10 Q25 Median Q75 Q90 Max

Fish River at Hazelgrove 89 4.9 4.0 0.4 1.6 2.2 2.7 3.7 5.6 9.0 31.5

Turon River at Bathurst Point 88 5.1 19.4 2.1 0.4 0.5 0.8 1.4 2.9 9.3 175.0

Macquarie River at Bruinbun 90 20.5 42.4 4.5 1.6 4.8 7.1 12.6 19.5 32.7 389.0

Cudgegong River at Rylstone Bridge 91 3.5 2.2 0.2 1.3 1.7 2.0 2.9 3.9 6.1 13.9

Cudgegong River at Yamble Bridge 83 20.8 29.1 3.2 4.7 8.0 9.6 13.5 18.3 40.0 247.0

Macquarie River D/S Burrendong Dam 85 6.6 4.5 0.5 1.7 2.4 3.5 5.3 9.5 12.3 28.3

Bell River at Newrea 86 19.5 62.7 6.8 2.0 3.0 4.2 6.4 9.2 16.0 434.0

Little River at Arthurville 75 11.2 12.8 1.5 1.0 2.0 3.2 6.7 13.0 28.3 72.9

Macquarie River at Molong Rail Bridge 67 18.2 32.3 3.9 3.7 5.6 6.9 10.4 15.0 23.0 228.0

Talbragar River at Elong Elong 39 89.8 125.0 20.0 5.2 10.0 22.9 34.0 85.0 297.0 509.0

Castlereagh River at Mendooran 44 22.1 35.1 5.3 5.0 5.9 7.0 9.0 14.0 35.0 156.0

Macquarie River at Warren Weir 64 40.1 77.8 9.7 3.4 10.7 12.7 20.2 30.4 81.0 549.0

Marthaguy Creek at Carinda 34 221.6 245.6 42.1 20.3 45.0 79.0 125.0 209.0 650.0 1000.0

Macquarie River at Bells Bridge 48 67.9 53.6 7.7 5.2 8.2 19.3 61.5 104.0 138.0 207.0

NSW Department of Planning, Industry and Environment | INT17/243328 | 65 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Bogan River at Gongolgon 65 69.4 85.3 10.6 5.9 11.0 15.0 33.0 88.0 204.0 450.0

Total Suspended Solids (mg/L) Site Name N Mean Std Dev Std Error Min Q10 Q25 Median Q75 Q90 Max

Fish River at Hazelgrove 85 6.2 2.6 0.3 5.0 5.0 5.0 5.0 6.2 10.0 24.0

Turon River at Bathurst Point 86 9.8 28.9 3.1 5.0 5.0 5.0 5.0 7.0 10.0 270.0

Macquarie River at Bruinbun 89 40.3 178.8 19.0 5.0 6.0 11.0 18.0 26.0 42.0 1700.0

Cudgegong River at Rylstone Bridge 90 6.4 3.8 0.4 5.0 5.0 5.0 5.0 6.0 10.0 32.0

Cudgegong River at Yamble Bridge 83 20.7 24.9 2.7 5.0 8.0 11.0 15.0 25.0 32.0 220.0

Macquarie River D/S Burrendong Dam 83 6.4 2.4 0.3 5.0 5.0 5.0 5.0 7.0 10.0 17.0

Bell River at Newrea 86 23.6 78.0 8.4 5.0 5.0 6.0 8.8 13.0 18.0 650.0

Little River at Arthurville 73 12.6 13.8 1.6 5.0 5.0 5.0 8.0 14.0 21.0 88.0

Macquarie River at Molong Rail Bridge 65 16.5 13.9 1.7 5.0 6.0 9.0 13.0 18.0 31.0 71.0

Talbragar River at Elong Elong 39 73.6 80.6 12.9 5.5 13.0 25.0 54.0 80.0 150.0 370.0

Castlereagh River at Mendooran 44 20.7 23.1 3.5 5.0 5.0 6.0 9.5 24.0 58.0 98.0

Macquarie River at Warren Weir 61 41.7 57.2 7.3 9.5 13.0 15.0 23.0 36.0 83.0 340.0

Marthaguy Creek at Carinda 34 95.9 71.6 12.3 13.0 20.0 40.0 77.5 110.0 190.0 290.0

Macquarie River at Bells Bridge 49 55.0 38.7 5.5 5.0 7.0 17.0 58.0 89.0 110.0 130.0

Bogan River at Gongolgon 66 28.6 20.6 2.5 7.0 10.0 15.0 21.0 35.0 54.0 100.0

Dissolved Oxygen (% saturation) Site Name N Mean Std Dev Std Error Min Q10 Q25 Median Q75 Q90 Max

Fish River at Hazelgrove 65 97.1 7.2 0.9 77.9 86.9 93.3 99.5 102.0 104.8 107.1

Turon River at Bathurst Point 55 107.8 13.4 1.8 86.3 91.0 98.3 108.0 114.9 120.9 147.9

Macquarie River at Bruinbun 64 105.2 13.9 1.7 83.2 92.0 99.3 104.8 109.9 113.8 189.9

Cudgegong River at Rylstone Bridge 63 100.2 18.2 2.3 63.2 83.5 88.7 101.7 108.0 111.8 190.7

Cudgegong River at Yamble Bridge 57 79.9 14.9 2.0 24.5 61.7 71.0 79.9 91.0 98.7 106.0

NSW Department of Planning, Industry and Environment | INT17/243328 | 66 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Macquarie River D/S Burrendong Dam 57 97.3 22.7 3.0 31.0 66.8 85.0 100.5 109.8 116.1 166.5

Bell River at Newrea 59 85.3 11.7 1.5 53.7 69.1 76.2 86.0 93.6 101.2 109.1

Little River at Arthurville 51 107.0 16.1 2.2 66.0 89.7 97.0 108.0 119.7 123.4 135.8

Macquarie River at Molong Rail Bridge 34 84.4 20.5 3.5 17.0 65.0 75.0 85.8 93.5 102.9 149.3

Talbragar River at Elong Elong 20 75.4 16.8 3.8 48.8 53.2 60.9 76.5 88.0 97.5 106.0

Castlereagh River at Mendooran 24 75.2 10.8 2.2 57.0 60.0 67.5 75.8 82.1 89.2 97.0

Macquarie River at Warren Weir 32 85.9 11.4 2.0 62.0 75.0 77.2 85.9 95.0 99.5 107.0

Marthaguy Creek at Carinda 26 89.6 37.0 7.3 12.5 51.7 68.4 90.5 101.5 148.0 178.0

Macquarie River at Bells Bridge 35 98.2 23.9 4.0 61.8 67.0 77.9 96.5 111.5 132.6 158.5

Bogan River at Gongolgon 43 86.3 30.5 4.7 28.0 51.0 66.7 85.5 96.9 120.5 178.9

pH Site Name N Mean Std Dev Std Error Min Q10 Q25 Median Q75 Q90 Max

Fish River at Hazelgrove 85 7.5 0.5 0.1 6.1 7.0 7.2 7.5 7.7 8.0 8.6

Turon River at Bathurst Point 73 7.9 0.4 0.0 6.7 7.3 7.7 7.9 8.2 8.3 9.2

Macquarie River at Bruinbun 85 8.0 0.5 0.1 6.1 7.4 7.8 8.0 8.3 8.4 9.0

Cudgegong River at Rylstone Bridge 88 7.5 0.4 0.0 6.3 6.9 7.3 7.5 7.7 8.0 8.4

Cudgegong River at Yamble Bridge 81 7.6 0.4 0.0 6.7 7.2 7.4 7.6 7.8 8.0 10.0

Macquarie River D/S Burrendong Dam 84 7.5 0.5 0.1 6.2 6.9 7.2 7.5 7.8 8.0 8.8

Bell River at Newrea 86 7.5 0.3 0.0 6.7 7.1 7.3 7.5 7.6 7.8 8.5

Little River at Arthurville 72 8.0 0.6 0.1 6.9 7.5 7.7 8.0 8.3 8.5 10.4

Macquarie River at Molong Rail Bridge 65 7.6 0.3 0.0 7.0 7.3 7.4 7.6 7.8 8.1 8.3

Talbragar River at Elong Elong 38 7.7 0.3 0.1 7.1 7.3 7.5 7.8 7.9 8.2 8.3

Castlereagh River at Mendooran 44 7.6 0.3 0.0 6.9 7.3 7.4 7.6 7.8 7.9 8.0

Macquarie River at Warren Weir 64 7.6 0.3 0.0 7.0 7.2 7.4 7.6 7.8 8.1 8.3

Marthaguy Creek at Carinda 32 7.7 0.7 0.1 6.3 7.0 7.2 7.8 8.0 8.7 9.5

Macquarie River at Bells Bridge 47 7.8 0.5 0.1 6.9 7.3 7.4 7.8 8.0 8.4 9.1

Bogan River at Gongolgon 61 7.6 0.6 0.1 6.4 7.0 7.2 7.6 7.9 8.3 9.6

NSW Department of Planning, Industry and Environment | INT17/243328 | 67 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Electrical Conductivity (µS/cm) Site Name N Mean Std Dev Std Error Min Q10 Q25 Median Q75 Q90 Max

Fish River at Hazelgrove 85 101 16 2 66 83 92 100 108 118 155

Turon River at Bathurst Point 85 458 96 10 208 306 412 463 532 581 659

Macquarie River at Bruinbun 89 345 108 11 148 215 258 334 405 503 608

Cudgegong River at Rylstone Bridge 90 397 154 16 234 280 326 353 414 607 1279

Cudgegong River at Yamble Bridge 83 707 155 17 120 511 662 724 806 871 984

Macquarie River D/S Burrendong Dam 83 323 60 7 173 242 284 326 349 409 449

Bell River at Newrea 86 758 133 14 302 612 715 776 837 891 1020

Little River at Arthurville 73 1127 556 65 157 452 601 1190 1471 1709 2729

Macquarie River at Molong Rail Bridge 65 396 135 17 217 261 321 356 427 569 810

Talbragar River at Elong Elong 39 896 396 63 244 340 501 866 1210 1417 1774

Castlereagh River at Mendooran 44 727 264 40 166 335 586 759 914 1054 1200

Macquarie River at Warren Weir 61 459 177 23 165 302 346 419 482 695 1005

Marthaguy Creek at Carinda 34 416 242 41 94 116 180 418 602 762 889

Macquarie River at Bells Bridge 49 575 145 21 364 410 461 554 661 762 988

Bogan River at Gongolgon 66 398 230 28 131 156 192 320 571 766 974

NSW Department of Planning, Industry and Environment | INT17/243328 | 68 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Table 20: Bogan River at Gongolgon electrical conductivity for purposes of long term salinity planning in the Macquarie Castlereagh WRPA

Year Salinity (EC µS/cm) Salt Load (t/year) Median (50%ile) Peak (80%ile) Total 2001-2002 534 683 5708 2002-2003 659 682 1999 2003-2004 419 567 1075 2004-2005 487 602 277 2005-2006 318 353 1614 2006-2007 366 380 701 2007-2008 238 342 12837 2008-2009 294 492 812 2009-2010 192 208 4590 2010-2011 321 442 79152 2011-2012 352 892 30048 2012-2013 463 573 10439 2013-2014 540 663 3562 2014-2015 321 378 1678 2015-2016 413 438 4278 Mean 10585

Table 21: Castlereagh River at Gungalman electrical conductivity for purposes of long term salinity planning in the Macquarie Castlereagh WRPA

Year Salinity (EC µS/cm) Salt Load (t/year) Median (50%ile) Peak (80%ile) Total 2001-2002 1013 1148 3220 2002-2003 660 818 0 2003-2004 516 949 1744 2004-2005 612 710 157 2005-2006 604 701 4810 2006-2007 0 2007-2008 0 2008-2009 0 2009-2010 501 1099 366 2010-2011 447 817 152324 2011-2012 878 954 1065 2012-2013 689 724 922 2013-2014 744 805 1550 2014-2015 279 320 366 2015-2016 316 468 7563 Mean 11606

NSW Department of Planning, Industry and Environment | INT17/243328 | 69 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Table 22: Macquarie River at Bells Bridge electrical conductivity for purposes of long term salinity planning in the Macquarie Castlereagh WRPA

Year Salinity (EC µS/cm) Salt Load (t/year) Median (50%ile) Peak (80%ile) Total 2000-2001 464 617 63403 2001-2002 654 720 11645 2002-2003 617 710 2766 2003-2004 616 679 1782 2004-2005 702 791 1016 2005-2006 618 664 1153 2006-2007 501 625 518 2007-2008 591 698 299 2008-2009 525 604 620 2009-2010 452 486 596 2010-2011 461 525 103469 2011-2012 591 783 15903 2012-2013 0 2013-2014 614 655 1225 2014-2015 608 739 779 2015-2016 592 688 936 Mean 12882

Table 23: Comparison of annual salt loads in the Macquarie Castlereagh WRPA

Castlereagh River at Macquarie River at Bells Year Bogan River at Gungalman Gongolgon Bridge

2001-2002 3220 5708 11645 2002-2003 0 1999 2766 2003-2004 1744 1075 1782 2004-2005 157 277 1016 2005-2006 4810 1614 1153 2006-2007 0 701 518 2007-2008 0 12837 299 2008-2009 0 812 620 2009-2010 366 4590 596 2010-2011 152324 79152 103469 2011-2012 1065 30048 15903 2012-2013 922 10439 0 2013-2014 1550 3562 1225 2014-2015 366 1678 779 2015-2016 7563 4278 936 Mean 11606 10585 12882

NSW Department of Planning, Industry and Environment | INT17/243328 | 70 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Appendix E. Draftsman plots and Box plots by site The mean daily discharge, total nitrogen, total phosphorus, turbidity and total suspended solids data in the Draftsman plots has been natural log transformed to normalise the distribution of the data. The box plots show the annual 25th, 50th and 75th percentile values, with error bars indicating the 10th and 90th percentile values for each parameter. The data set extends from 2007 to 2015, and displays within site variability. In each figure there are numerous plots with A) total nitrogen, B) total phosphorus, C) turbidity, D) total suspended solids, E) dissolved oxygen, F) pH, G) electrical conductivity measured during monthly sampling and H) continuous electrical conductivity (where available). Red lines indicate the Basin Plan water quality targets (and target ranges) from Schedule 11 of the Basin Plan for the appropriate zone. Total suspended solids have a lower detection limit of 5 mg/L.

NSW Department of Planning, Industry and Environment | INT17/243328 | 71 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Fish River at Hazelgrove There is no flow data available for the Fish River monitoring site. There is a strong positive correlation between total nitrogen, total phosphorus and turbidity. There is a slight positive correlation between dissolved oxygen and pH. There is not a clear linear relationship between turbidity and total suspended solids. Any correlation between the two parameters may be masked by the 5mg/L lower detection limit for total suspended solids. The Fish River monitoring site is located in the upper Macquarie River catchment, where it receives reduced impact from human disturbance. This is reflected in the median concentrations of total nitrogen, total phosphorus and turbidity being lower than the respective Basin Plan water quality targets. Median pH levels are between the upper and lower limits, with some results outside this range. In most years the dissolved oxygen results are between the upper and lower ranges. Dissolved oxygen levels dropped below the lower limit in 2009-2010, possibly in response to dry conditions. Electrical conductivity is low.

Figure 19: Draftsman plots for Fish River at Hazelgrove

NSW Department of Planning, Industry and Environment | INT17/243328 | 72 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

1.0 0.06 B) A) 0.8 0.05 0.04 0.6 0.03 0.4 TP(mg/L) TN(mg/L) 0.02

0.2 0.01

0.0 0.00 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

14 20 C) 12 D) 10 15 8 10 6

4 (mg/L) TSS

Turbidity(NTU) 5 2 0 0 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

120 8.5 E) F) 110 8.0

100 7.5 pH 90 7.0 DO(%sat)

80 6.5

70 6.0 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

160 G) 140

120

100 EC(µS/cm) 80

60 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

Figure 20: Water quality data for Fish River at Hazelgrove

NSW Department of Planning, Industry and Environment | INT17/243328 | 73 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Turon River at Bathurst Point The draftsman plots show a positive correlation between total nitrogen, total phosphorus and turbidity, with all three parameters positively correlated to flow. Electrical conductivity is negatively correlated to flow suggesting contributions from saline groundwater during low flow periods and dilution at high flows. As for Fish River, correlation between turbidity and total suspended solids is masked by the 5mg/L lower detection limit for total suspended solids. The fertility of the soils in the Turon River catchment is generally low. This is reflected in median total nitrogen and total phosphorus results below the target values. The land use in the catchment is principally grazing, and the sandy soils keep turbidity results low. The pool/riffle sequence of the Turon River, combined with aquatic plant growth helps maintain elevated dissolved oxygen, at times in excess of the upper limit. High median pH coincides with years with high dissolved oxygen, suggesting the elevated pH could be driven by primary production. Median electrical conductivity is increasing between 2010 and 2014 and declined again in 2015.

Figure 21: Draftsman plots for Turon River at Bathurst Point

NSW Department of Planning, Industry and Environment | INT17/243328 | 74 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

1.0 0.08 B) A) 0.07 0.8 0.06

0.6 0.05 0.04 0.4 0.03 TP(mg/L) TN(mg/L) 0.02 0.2 0.01 0.0 0.00 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

35 40 C) 30 D) 25 30 20 20 15

10 (mg/L) TSS

Turbidity(NTU) 10 5 0 0 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

140 9.0 E) F) 130 8.5 120 8.0 110 pH 7.5

DO(%sat) 100

90 7.0

80 6.5 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

700 700 G) H) 600 600

500 500

400 400 EC(µS/cm) EC(µS/cm) 300 300

200 200 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

Figure 22: Water quality data for Turon River at Bathurst Point

NSW Department of Planning, Industry and Environment | INT17/243328 | 75 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Macquarie River at Bruinbun There is a strong positive correlation between total nitrogen, total phosphorus and turbidity, but there is not strong correlation between these parameters and flow during low flow conditions. There is a strong correlation between electrical conductivity and flow. Dissolved oxygen is stable with occasional low or high readings. Median total nitrogen and total phosphorus results are close to or in excess of the Basin Plan targets. The Basalt derived soils in the headwaters of the Macquarie River are highly fertile and provide a source of nutrients. Turbidity readings are generally below the target, except for high flow events. Flooding in 2010 resulted in very high total nitrogen, total phosphorus and turbidity results, highlighting the important role flooding plays in sediment and nutrient transport. The pH is generally at or in excess of the upper target limit of 8.0. Dissolved oxygen is mostly between the upper and lower target values. The pool/riffle sequence and high nutrients provide ideal conditions for increased growth of algae and aquatic macrophytes, resulting in occasional high dissolved oxygen readings. There was an increase in the median electrical conductivity between 2011 and 2014 following the flooding in 2010. Recharge may have increased the contribution of groundwater to low flows, raising the electrical conductivity.

Figure 23: Draftsman plots for Macquarie River at Bruinbun

NSW Department of Planning, Industry and Environment | INT17/243328 | 76 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

3.0 0.30 A) B) 2.5 0.25

2.0 0.20

1.5 0.15 TP(mg/L) TN(mg/L) 1.0 0.10

0.5 0.05

0.0 0.00 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

100 100 C) 389 NTU 1700 mg/L D) 80 80

60 60

40 40 TSS (mg/L) TSS

Turbidity(NTU) 20 20

0 0 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

140 9.0 F) E) 130 8.5

120 8.0

110 7.5 pH

DO(%sat) 100 7.0

90 6.5

80 6.0 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

G) 600

400 EC(µS/cm)

200 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

Figure 24: Water quality data for Macquarie River at Bruinbun

NSW Department of Planning, Industry and Environment | INT17/243328 | 77 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Cudgegong River at Rylstone Bridge The correlation between parameters is not as strong at the Rylstone Bridge site as other sites in the Macquarie catchment. There is a correlation between total nitrogen and total phosphorus, indicating that both are transported via similar mechanisms. Total nitrogen shows a correlation to turbidity indicating that nutrients are generally transported attached to soil particles. The median total nitrogen exceeded the Basin Plan target most years, where the total phosphorus median only exceeded the target in 2010/2011, due to high flows. Turbidity results are low and stable through time. Electrical conductivity is stable during the drier years from 2007 to early 2010. Following the flooding in 2010, electrical conductivity increased rapidly from 2011 to 2013 and then dropped back to more normal results in 2014 and 2015. The increase is likely as a result of the wetting up of the catchment in 2010 after the preceding dryer years, resulting in increased base flow contributions from more saline shallow groundwater.

Figure 25: Draftsman plots for Cudgegong River at Rylstone Bridge

NSW Department of Planning, Industry and Environment | INT17/243328 | 78 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

1.4 0.12 A) B) 1.2 0.10

1.0 0.08

0.8 0.06 TP(mg/L) TN(mg/L) 0.6 0.04

0.4 0.02

0.2 0.00 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

25 25 C) D) 20 20

15 15

10 10 TSS (mg/L) TSS

Turbidity(NTU) 5 5

0 0 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

130 8.5 E) 120 F) 8.0 110 100 7.5 pH 90 7.0 DO(%sat) 80 6.5 70 60 6.0 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

800 G) 700

600

500

EC(µS/cm) 400

300

200 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

Figure 26: Water quality data for Cudgegong River at Rylstone Bridge

NSW Department of Planning, Industry and Environment | INT17/243328 | 79 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Cudgegong River at Yamble Bridge The draftsman plots show a positive correlation between total nitrogen, total phosphorus and turbidity, with all three parameters positively correlated to flow. Electrical conductivity is negatively correlated to flow suggesting contributions from saline groundwater during low flow periods and dilution at high flows, possibly during releases from Windamere Dam. Total nitrogen results are mostly below the Basin Plan target with some readings in all years exceeding the target. The total phosphorus results are the inverse, with most results exceeding the target and some readings in all years lower than the target. Median turbidity is less than the target in all years with some higher results in response to increased flow. Dissolved oxygen levels are low, with only one year having an annual median in the target range of 90 to 110%saturation. The reason for the low dissolved oxygen at this site is unknown. The median pH and electrical conductivity is stable through time.

Figure 27: Draftsman plots for Cudgegong River at Yamble Bridge

NSW Department of Planning, Industry and Environment | INT17/243328 | 80 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

1.2 0.12 A) B) 1.0 0.10 0.08 0.8 0.06 0.6 TP(mg/L) TN(mg/L) 0.04

0.4 0.02

0.2 0.00 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

80 60 D) C) 50 60 40

40 30

TSS (mg/L) TSS 20

Turbidity(NTU) 20 10

0 0 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

120 8.4 E) F) 110 8.2 100 8.0 7.8 90 7.6 80 pH 7.4 DO(%sat) 70 7.2 60 7.0 50 6.8 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

1100 1100 G) 1000 H) 1000 900 900 800 800 700 700 600 600 EC(µS/cm) EC(µS/cm) 500 500 400 400 300 300 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

Figure 28: Water quality data for Cudgegong River at Yamble Bridge

NSW Department of Planning, Industry and Environment | INT17/243328 | 81 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Macquarie River downstream Burrendong Dam This monitoring site is located less than 200 metres downstream of the outlet of Burrendong Dam. The quality of the water is directly related to the quality of the water in the dam, and the depth from which the water is being drawn. When stratified, the bottom waters of large storages can become anoxic, resulting in the release of nutrients and metals from the reservoir sediments. There appears to be positive correlations between total nitrogen, total phosphorus and turbidity. Electrical conductivity has a slight negative correlation to flow. The boxplots show high nutrient levels in 2010-2011in response to major flooding in the catchment. Burrendong Dam was spilling during this event, allowing nutrient rich floodwater to be released downstream. This trend is not as evident in the turbidity data. As the floodwater reached the dam, the reduced flow velocity would have caused suspended particles to settle to the bottom, reducing the turbidity of the water flowing over the spillway into the Macquarie River. The dissolved oxygen was lowest in 2011-2012 when Burrendong Dam was at 100% capacity. Due to the depth of water at the dam wall, the water released from lower in the profile would have had low dissolved oxygen. The development of anoxia in the hypolimnion over summer would have resulted in increased concentrations of total nitrogen and total phosphorus in the water released. As the depth of water decreased with time through releases, allowing mixing within the storage, the dissolved oxygen increased and nutrient concentrations decreased. Prior to the flooding, the median electrical conductivity was stable between 300 and 350µS/cm. Floodwaters are characterised by high electrical conductivity in the first flush and then much lower readings. The volume of floodwater reduced the median electrical conductivity in the dam to less than 250µS/cm. As this water was released, and more saline base flows entered the dam, the electrical conductivity increased again.

Figure 29: Draftsman plots for Macquarie River downstream Burrendong Dam

NSW Department of Planning, Industry and Environment | INT17/243328 | 82 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

1.6 0.20 B) A) 0.18 1.4 0.16 1.2 0.14 1.0 0.12 0.10 0.8 0.08 TP(mg/L) TN(mg/L) 0.6 0.06 0.04 0.4 0.02 0.2 0.00 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

25 20 C) D) 20 15

15 10 10 TSS (mg/L) TSS

Turbidity(NTU) 5 5

0 0 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

140 8.5 E) F) 120 8.0

100 7.5 pH 80 7.0 DO(%sat)

60 6.5

40 6.0 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

500 500 G) H) 450 450 400 400 350 350 300 300

EC(µS/cm) 250 EC(µS/cm) 250 200 200 150 150 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

Figure 30: Water quality data for Macquarie River downstream Burrendong Dam

NSW Department of Planning, Industry and Environment | INT17/243328 | 83 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Bell River at Newrea As with most sites in the Macquarie valley, the draftsman plots show a positive correlation between total nitrogen, total phosphorus and turbidity, with all three parameters positively correlated to flow. Electrical conductivity is negatively correlated to flow. The main feature of the box plots is the high levels of nutrients and turbidity during the flooding in 2010-2011. During low flow periods the median levels are at, or below the Basin Plan targets. Dissolved oxygen levels are mostly less than the lower limit. The median electrical conductivity is stable most years, with lower readings in 2010-2011.

Figure 31: Draftsman plots for Bell River at Newrea

NSW Department of Planning, Industry and Environment | INT17/243328 | 84 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

2.5 0.35 B) A) 0.30 2.0 0.25 1.5 0.20

1.0 0.15 TP(mg/L) TN(mg/L) 0.10 0.5 0.05 0.0 0.00 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

100 100 C) 434 NTU 650 mg/L D) 80 80

60 60

40 40 TSS (mg/L) TSS

Turbidity(NTU) 20 20

0 0 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

120 8.4 F) E) 8.2 110 8.0 100 7.8 90 7.6 pH 7.4

DO(%sat) 80 7.2 70 7.0 60 6.8 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

1000 1200 G) 900 H) 1000 800 700 800

600 600

EC(µS/cm) 500 EC(µS/cm) 400 400 300 200 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

Figure 32: Water quality data for Bell River at Newrea

NSW Department of Planning, Industry and Environment | INT17/243328 | 85 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Little River at Arthurville There is a strong positive correlation between total nitrogen, total phosphorus and turbidity, but not as strong a correlation between these parameters and flow. There is a strong negative correlation between electrical conductivity and flow. There is also a negative correlation between electrical conductivity and turbidity. The high salinity in Little River may be causing the suspended sediment to settle out, reducing turbidity. The geology of the Little River catchment contains naturally high levels of salt which is transported into surface water. This is reflected in the increased electrical conductivity following groundwater recharge during the flooding in 2010. Median nutrient and turbidity is generally less than targets levels. Dissolved oxygen varies across the data set with low readings in 2008-2009 and high readings in 2012-2013. The pool/riffle sequence and high nutrients provide ideal conditions for increased growth of algae and aquatic macrophytes, resulting in high dissolved oxygen readings. In conjunction with high salinity, sites in the Little River catchment can be highly sodic, leading to increased pH.

Figure 33: Draftsman plots for Little River at Arthurville

NSW Department of Planning, Industry and Environment | INT17/243328 | 86 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

2.5 0.35 B) A) 0.30 2.0 0.25 1.5 0.20

1.0 0.15 TP(mg/L) TN(mg/L) 0.10 0.5 0.05 0.0 0.00 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

80 100 C) 70 D) 80 60

50 60 40 30 40 TSS (mg/L) TSS

Turbidity(NTU) 20 20 10 0 0 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

140 11.0 E) F) 130 10.5 120 10.0 110 9.5 100 9.0

90 pH 8.5

DO(%sat) 80 8.0 70 7.5 60 7.0 50 6.5 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

3000 G) 2500

2000

1500

EC(µS/cm) 1000

500

0 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

Figure 34: Water quality data for Little River at Arthurville

NSW Department of Planning, Industry and Environment | INT17/243328 | 87 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Macquarie River at Molong Rail Bridge Routine water quality samples were not collected at this site in 2012 to 2013. There is a positive correlation between total nitrogen, total phosphorus and turbidity, and a correlation between these parameters and flow. There is a strong negative correlation between electrical conductivity and flow. The median total nitrogen, total phosphorus and turbidity meet the respective Basin Plan targets in the low flow years, but exceed the targets in wet/high flow years. The dissolved oxygen is consistently low throughout the data set, with most results lower than the 90%saturation target. Electrical conductivity is low during the dry years from 2007 to 2010, suggesting little connectivity between groundwater and surface water. The flushing of salts from tributaries downstream of Burrendong Dam (e.g. Little River) resulted in increased electrical conductivity in 2010 to 2011. The salt load in the Macquarie River would then have been diluted by releases from Burrendong Dam in 2011 to 2012. The increasing electrical conductivity at the downstream Burrendong Dam site in 2013 to 2015 is reflected at the Molong Rail Bridge site.

Figure 35: Draftsman plots for Macquarie River at Molong Rail Bridge

NSW Department of Planning, Industry and Environment | INT17/243328 | 88 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

1.6 0.14 A) B) 1.4 0.12 1.2 0.10 1.0 0.08 0.8 0.06 TP(mg/L) TN(mg/L) 0.6 0.04 0.4 0.02 0.2 0.00 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

80 80 C) 228 NTU D)

60 60

40 40 TSS (mg/L) TSS

Turbidity(NTU) 20 20

0 0 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

140 8.5 E) F) 120 8.0

100 7.5 pH 80 DO(%sat) 7.0 60

40 6.5 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

1000 G) 800

600

400 EC(µS/cm) 200

0 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

Figure 36: Water quality data for Macquarie River at Molong Rail Bridge

NSW Department of Planning, Industry and Environment | INT17/243328 | 89 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Talbragar River at Elong Elong Monitoring at this site ceased in 2012, reducing the length of the data set and making the draftsman plots less conclusive. A correlation between total nitrogen, total phosphorus and turbidity is still evident. Most samples collected from the Talbragar River exceeded the total nitrogen, total phosphorus and turbidity Basin Plan targets. Despite the high nutrient concentrations, which can promote the growth of aquatic plants, the median dissolved oxygen levels were less than the lower limit in all years that there was data available. High turbidity could be restricting aquatic plant growth. The median pH remained between the upper and lower limits. Electrical conductivity increased in response to heavy rainfall in 2010. This may be in response to highly saline runoff, or recharge reconnecting groundwater and surface water.

Figure 37: Draftsman plots for Talbragar River at Elong Elong

NSW Department of Planning, Industry and Environment | INT17/243328 | 90 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

3.0 0.8 A) B) 0.7 2.5 0.6 2.0 0.5 1.5 0.4 0.3 TP(mg/L) TN(mg/L) 1.0 0.2 0.5 0.1 0.0 0.0 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

600 400 C) 500 D) 300 400

300 200

200 (mg/L) TSS

Turbidity(NTU) 100 100

0 0 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

120 8.5 E) F) 110 100 8.0 90 80 7.5 pH 70 DO(%sat) 60 7.0 50 40 6.5 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

2000 G) 1750 1500 1250 1000 750 EC(µS/cm) 500 250 0 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

Figure 38: Water quality data for Talbragar River at Elong Elong

NSW Department of Planning, Industry and Environment | INT17/243328 | 91 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Castlereagh River at Mendooran Monitoring at this site ceased in 2012, reducing the length of the data set and making the draftsman plots less conclusive. In addition, there is no flow data available at this site. There is still a general trend of correlations between total nitrogen, total phosphorus and turbidity. There is also a positive correlation between electrical conductivity and pH. The higher electrical conductivity may be in response to increased alkaline salts, raising the pH. Total nitrogen concentrations and turbidity are generally less than the target values, while total phosphorus concentrations are in excess of the target. Dissolved oxygen levels are low with most results less than the lower limit. The median pH is within the upper and lower limits.

Figure 39: Draftsman plots for Castlereagh River at Mendooran

NSW Department of Planning, Industry and Environment | INT17/243328 | 92 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

1.25 0.30 A) B) 1.00 0.25 0.20 0.75 0.15 0.50 TP(mg/L) TN(mg/L) 0.10

0.25 0.05

0.00 0.00 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

160 100 C) 140 D) 80 120

100 60 80 60 40 TSS (mg/L) TSS

Turbidity(NTU) 40 20 20 0 0 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

120 8.5 E) F) 110 100 8.0 90 7.5 80 pH DO(%sat) 70 7.0 60 50 6.5 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

1250 G) 1000

750

500 EC(µS/cm) 250

0 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

Figure 40: Water Quality data for the Castlereagh River at Mendooran

NSW Department of Planning, Industry and Environment | INT17/243328 | 93 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Macquarie River at Warren Weir Routine water quality samples were not collected at this site in 2012 to 2013. From the draftsman plots there is a positive correlation between total nitrogen, total phosphorus and turbidity. The relationship between these parameters and flow is more exponential than linear. There is also a negative correlation between electrical conductivity and flow. In low flow years, the total nitrogen, total phosphorus and turbidity box plots are compressed. As the water quality samples at this site are collected downstream of Warren Weir, there appears to be settling of sediment and associated nutrients in the weir pool at low flows. When flow increases in wetter years, the higher velocity flows are able to resuspend this settled material and carry it over the weir structure. The result is that samples collected during dryer years are more likely to meet the Basin Plan targets than in wet years. Median dissolved oxygen levels are mostly below the lower target. This monitoring site is located close to the boundary of the upland and lowland zones, where it is receiving the cumulative impacts from upstream. The dissolved oxygen target may need to be assessed to determine if it is appropriate for this site. Electrical conductivity is stable through time due to the water received through regulated flows with minimal groundwater/surface water interactions.

Figure 41: Draftsman plots for Macquarie River at Warren Weir

NSW Department of Planning, Industry and Environment | INT17/243328 | 94 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

2.5 0.30 A) B) 2.0 0.25 0.20 1.5 0.15 1.0 TP(mg/L) TN(mg/L) 0.10

0.5 0.05

0.0 0.00 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

200 200 C) 549 NTU D) 340 mg/L

150 150

100 100 TSS (mg/L) TSS

Turbidity(NTU) 50 50

0 0 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

120 8.5 E) F) 110 8.0 100

90 7.5 pH

DO(%sat) 80 7.0 70

60 6.5 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

1000 1000 G) H) 800 800

600 600 400 EC(µS/cm) EC(µS/cm) 400 200

0 200 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

Figure 42: Water quality data for Macquarie River at Warren Weir

NSW Department of Planning, Industry and Environment | INT17/243328 | 95 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Marthaguy River at Carinda Marthaguy Creek is ephemeral, mostly receiving flows via regulation through the Macquarie Marshes. Correlations between parameters are not as evident as at most other sites. The very fine clay particles in these lowland rivers remain suspended in the water column during low and zero flow, resulting in high turbidity and associated nutrients under all flow conditions. Total nitrogen, total phosphorus and turbidity results exceed the Basin Plan targets in most samples. It may need to be investigated if the Basin Plan targets are appropriate for this site. The median dissolved oxygen is mostly between the upper and lower limits, however there are very large fluctuations. The monitoring site is located in a small weir structure, creating a pool at the gauging station. The variability at the site is primarily driven by the response of instream biota in these conditions. High organic carbon, nutrients and water temperatures result in increased microbial respiration. High turbidity and suspended sediment during these times reduces light availability and likely reduces primary production. High pH results are possibly in response to increased primary production.

Figure 43: Draftsman plots for Marthaguy River at Carinda

NSW Department of Planning, Industry and Environment | INT17/243328 | 96 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

4.5 0.8 A) B) 4.0 0.7 3.5 0.6 3.0 0.5 2.5 0.4 2.0 0.3 TP(mg/L) TN(mg/L) 1.5 0.2 1.0 0.1 0.5 0.0 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

1200 350 C) D) 1000 300 250 800 200 600 150

400 (mg/L) TSS 100 Turbidity(NTU) 200 50 0 0 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

200 10.0 F) E) 9.5 150 9.0 8.5 100 8.0 pH 7.5 DO(%sat) 50 7.0 6.5 0 6.0 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

1000 1200 G) H) 800 1000 800 600 600 400

EC(µS/cm) EC(µS/cm) 400

200 200

0 0 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

Figure 44: Water quality data for Marthaguy River at Carinda

NSW Department of Planning, Industry and Environment | INT17/243328 | 97 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Macquarie River at Bells Bridge There are slight correlations between total nitrogen, total phosphorus and turbidity, but not a correlation between these parameters and flow. Dissolved oxygen and pH are positively correlated. There is not a correlation between electrical conductivity and flow. The median total nitrogen exceeds the target value in all years and total phosphorus exceeds the target most years. The turbidity exceeds the target in wetter years. This site is located downstream of the Macquarie Marshes. In wetter years, floodwater flows through the marshes, making its way eventually to the Barwon River. The highly fertile alluvial clay soil on the floodplain, combined with the high productivity of the wetland, provides a rich source of nutrients. The high nutrient concentrations provide suitable conditions for aquatic plant growth, resulting in some high dissolved oxygen readings. The median pH is stable around the upper limit of 8.0.

Figure 45: Draftsman plots for Macquarie River at Bells Bridge

NSW Department of Planning, Industry and Environment | INT17/243328 | 98 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

2.5 0.40 B) A) 0.35 2.0 0.30

1.5 0.25 0.20 1.0 0.15 TP(mg/L) TN(mg/L) 0.10 0.5 0.05 0.0 0.00 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

200 140 C) D) 120 150 100 80 100 60

TSS (mg/L) TSS 40

Turbidity(NTU) 50 20 0 0 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

160 9.0 E) F) 140 8.5 8.0 120 7.5 pH 100

DO(%sat) 7.0

80 6.5

60 6.0 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

1000 900 G) H) 900 800 800 700 700 600 600

EC(µS/cm) EC(µS/cm) 500 500 400 400 300 300 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

Figure 46: Water quality data for Macquarie River at Bells Bridge

NSW Department of Planning, Industry and Environment | INT17/243328 | 99 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Bogan River at Gongolgon Total phosphorus is positively correlated to turbidity and total nitrogen, but total nitrogen is not correlated to turbidity. Correlation between parameters and flow is not clear, possibly due to the high number of samples collected during zero flow periods. Dissolved oxygen and pH are positively correlated. The median nutrient concentrations exceeded the respective targets in all years. High median turbidity does not appear to be solely linked to years with high flow. The monitoring site is located within the weir pool at Gongolgon. The high nutrient concentrations combined with stable conditions may be promoting increased algal growth, which can increase turbidity. The median pH gradually decreased with time, but remained within the upper and lower target limits. Electrical conductivity increased between 2011 and 2014 following high flows in 2010.

Figure 47: Draftsman plots for Bogan River at Gongolgon

NSW Department of Planning, Industry and Environment | INT17/243328 | 100 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

1.6 0.35 A) B) 1.4 0.30 0.25 1.2 0.20 1.0 0.15 TP(mg/L) TN(mg/L) 0.8 0.10 0.6 0.05 0.4 0.00 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

500 120 D) C) 400 100 80 300 60 200

TSS (mg/L) TSS 40 Turbidity(NTU) 100 20

0 0 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

180 10.0 E) 160 F) 9.5 140 9.0 120 8.5 100 8.0 pH 80 7.5 DO(%sat) 60 7.0 40 6.5 20 6.0 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

1000 1000 G) H) 800 800

600 600

400 400 EC(µS/cm) EC(µS/cm) 200 200

0 0 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015 2007-2008 2008-2009 2009-2010 2010-2011 2011-2012 2012-2013 2013-2014 2014-2015

Figure 48: Water quality data for Bogan River at Gongolgon

NSW Department of Planning, Industry and Environment | INT17/243328 | 101 Water quality technical report for Macquarie Castlereagh surface w ater resource plan area (SW11)

Appendix F. Local and expert knowledge meetings Table 24: Meetings held to develop the Macquarie Castlereagh water quality status and issue report

Stakeholder Key Date Activity Key opportunities/issues Group Coordinator

December Office of Meeting Local and expert input to DPI Water 2015 Environment and status and Issues report Heritage, Dubbo

December DPI Fisheries, Meeting Local and expert input to DPI Water 2015 Dubbo status and Issues report

December DPI Water Meeting Local and expert input to DPI Water 2015 status and Issues report

December Central West Meeting Local and expert input to DPI Water 2015 Councils status and Issues report Environment and Water Alliance

December Local Land Meeting Local and expert input to DPI Water 2015 Services, Dubbo status and Issues report

NSW Department of Planning, Industry and Environment | INT17/243328 | 102