Bellinger-Kalang Rivers Ecohealth Project, Assessment of River

Bellinger-Kalang Rivers Ecohealth Project Assessment of River and Estuarine Condition 2009-2010

Final Technical Report to the Bellingen Shire Council

Darren Ryder, Rob Veal, Carla Sbrocchi & John Schmidt

Cover Photo: Bellinger River catchment from Dorrigo National Park. Photo by D.Ryder 2010.

Bellinger-Kalang Rivers Ecohealth Project Assessment of River and Estuarine Condition 2009-2010

Final Technical Report to the Bellingen Shire Council. March 2011.

Darren Ryder and Rob Veal. School of Environmental and Rural Science, University of New England, Armidale, NSW 2350.

Carla Sbrocchi. Northern Rivers Catchment Management Authority, 41 Belgrave St Kempsey, NSW 2440.

John Schmidt. NSW Department of Environment, Climate Change and Water, 41 Belgrave St Kempsey, NSW 2440.

Acknowledgements

This project was funded by the Bellingen Shire Council with supporting funds from the NSW Department of Environment, Climate Change and Water. Special thanks to the Ecohealth Technical Reference Group for providing valuable information and for their ability to help overcome hurdles.

The people below provided significant support for the proct, our thanks to each of them.

Ian Turnbull and Andrew Rickert: Bellingen Shire Council. Michael Healey and Tod Lockridge: NSW Office of Water Tony Broderick, Nigel Blake and Max Osborne: NRCMA Maxine Rowley, Geoff Code and Yoshi Kobayashi: NSW DECCW Thor Aaso: Port Macquarie Hastings Council Hamish Malcolm: Solitary Island Marine Parks Authority Malcolm Robertson: Coffs Harbour Council Marion Costigan, Adrienne Burns, Morag Stewart, Jake Chandler and Peter Berney: University of New England

This report should be cited as:

Ryder, D, Veal, R, Sbrocchi, C and Schmidt, J (2011). Bellinger-Kalang Rivers Ecohealth Project: Assessment of River and Estuarine Condition 2009-2010. Final Technical Report to the Bellingen Shire Council. University of New England, Armidale 75pp.

Project Contact Dr Darren Ryder School of Environmental and Rural Science University of New England, Armidale, NSW 2350 Email: [email protected] Ph. 02 6773 5226

Table of contents

Summary i 1. Background 1 2. Scope 1 3. Project Objectives 2 4. Report Structure 3 PART 1. Study Area, Design and Site Descriptions 5. Study Area and Design 4 6. Study Sites 8 PART 2. Ecological Indicators: Water Quality, Macroinvertebrates and Riparian Condition 7. Water Quality Indicators 7.1 Background 34 7.2 Field and Laboratory Methods 35 7.3 Results 39 7.4 Summary of Findings 52 8 Macroinvertebrates 8.1 Background 53 8.2 Field and Laboratory Methods 53 8.3 Data Analyses 54 8.4 Results 54 8.5 Summary of Findings 58 9 Riparian Condition 9.1 Background 59 9.2 Development of a Sub-tropical Rapid Assessment of Riparian Condition 59 9.3 Field methods 62 9.4 Results 62 9.5 Summary of Findings 65 PART 3. Management Recommendations and Future Monitoring Water Quality 66 Macroinvertebrates 68 Riparian Condition 68 References 70 Appendices 71

Summary

The development of a standardised means of collecting, analysing and presenting riverine, coastal and estuarine assessments of ecological condition has been identified as a key need for coastal Catchment Management Authorities and Local Councils who are required to monitor natural resource condition, and water quality and quantity in these systems. This project was conducted over a 12 month period in the Bellinger and Kalang Rivers to contribute to the assessment of the ecological condition of the catchment. The project aimed to

 assess the health of coastal catchments using standardised indicators and reporting for estuaries, and upland and lowland river reaches using hydrology, water quality, riparian vegetation and habitat quality, and macroinvertebrates assemblages as indicators of ecosystem health in the Bellinger/Kalang system,

 contribute scientific information to the development of a report card system for communicating the health of the estuarine and freshwater systems in the Bellingen Shire.

Hydrology

Indicative discharge for the region was calculated from mean daily discharge at the Thora Gauge on the Bellinger River. Peak discharge during the study period of October 2009 to September 2010 was 5157 ML/day recorded on November 8th 2009. The minimum discharge recorded was 68 ML/day on September 14th 2010. Mean monthly discharge ranged from 98.2 ± 38.5 ML/day in September 2010 to 1290.8 ± 1003.9 ML/day in March 2010 (Figure 2). The absence of high flow events during the study period must be considered when interpreting the results from the water quality monitoring.

Water Quality

Water chemistry variables; pH, conductivity and salinity, dissolved oxygen (DO), temperature and turbidity were measured in situ from 22 sites (10 freshwater, 12 estuarine) each month in the Bellinger and Kalang Rivers from October 2009 to September 2010. Samples for TN, TP, SRP and NOx were also sampled from each site.

ANZECC trigger values for pH, dissolved oxygen, nitrogen and phosphorus, and turbidity were exceeded in some months at sites within both river systems. Spicketts Creek in the Kalang catchment was particularly noteworthy as a freshwater site that exceeded the trigger values for nitrogen, phosphorus, DO and turbidity. Tributaries in both catchments had higher turbidity than the main stem of each river, suggesting these systems may be a source of suspended material.

Calculation of nutrient loads entering the estuary of each river system revealed the Bellinger River supplies a disproportionate amount of N (460 tonnes/year), P (86 tonnes/year) and

iii

suspended solids (4320 tonnes/year) compared to the inputs from the Kalang River. These differences arise from the higher discharge in the Bellinger River rather than higher concentrations. The highest loads of N, P and suspended sediment were associated with high discharge levels, suggesting flood flows contribute substantial volumes of sediments to downstream reaches.

Macroinvertebrates

Macroinvertebrates were collected from 10 freshwater sites in Spring 2009 and Autumn 2010. This included five sites in the Kalang catchment (including one on Spicketts Creek as major tributary) and 5 sites in the Bellinger catchment (including one in Rosewood River and one in Never Never River as major tributaries). In Autumn, a total of 2003 individual macroinvertebrates from 22 families were collected from the Bellinger River, while abundance was lower in the Kalang River with 826 individuals collected from 23 families. In Spring, the pattern in abundance was reversed with a total of 1330 individuals collected in the Kalang River from 22 families, with 747 individuals from 21 families collected from the Bellinger River.

SIGNAL grades for macroinvertebrate Families ranged from 2 to 10 in main stem reaches on the Bellinger and Kalang Rivers, with a median score of 5 to 6 for both rivers and seasons. Tributaries generally ranged from 2-8, with Spicketts Creek displaying a consistently low SIGNAL score, reinforcing the poor water quality and habitat condition documented in this study.

Riparian Condition

An assessment of the riparian condition was undertaken from 10 freshwater sites in 2010. This included five sites in the Kalang catchment (including one on Spicketts Creek as major tributary) and 5 sites in the Bellinger catchment (including the Rosewood and Never Never Rivers as major tributaries).

The Bellinger catchment had an average riparian condition score of 7.14/10, ranging from 6.75 to 7.48. Sites in the Kalang catchment had an average riparian condition score of 5.27/10 ranging from 3.89 to 7.50. The most upstream sites in each river consistently had the best condition score.

Sub-index scores revealed that the Bank Condition indicator contributed most to a positive riparian condition score in the Bellinger catchment sites. In the Kalang catchment, riparian condition scores were consistently low across all indicators.

Major disturbances to the riparian zone identified by this study that have reduced the riparian condition score are weeds, reduced number of vertical strata leading to simplified canopy structure, and minimal riparian habitat in the form of organic litter and woody debris. Poor bank condition as evidenced by undercutting and bank slumping were consistent issues in all

tributaries, and may provide a link to increased suspended sediment loads recorded from these systems.

Recommendations

 Interpreting water quality variables relies on trigger values generic to a broad range of systems. Recommend the development of regional-scale or system-specific trigger values for water quality indicators relevant to current or predicted water quality issues in the catchment.

 Determination of estuarine health is currently limited to water quality variables. Recommend the development of biotic indicators for estuarine environments to compliment water quality indicators. Biota provide a temporally-integrative indicator of change as they have a longer residence time in any location that a parcel of water.

 Broaden future monitoring to incorporate an increased number of tributaries in each catchment to help identify sub-catchment level sources of poor water quality.

 Continue to monitor water quality in reaches approximate to the limit of tidal influence for water quality as the impacts on these reaches are more pronounced.

 Develop long-term water quality sample sites at locations with active discharge measurements to determine load-based nutrient and sediment inputs to estuarine environments.

 This project was conducted during a period of consistently low discharge and an absence of flood flows. Recommend developing a flood-based monitoring program to sample high flows of various magnitudes to develop load-based calculation for different flow events.

 Continue to collect samples for macroinvertebrate community composition in Autumn and Spring on an annual basis. In addition it is recommended to incorporate macroinvertebrate sampling into the recommended flood-based sampling protocol as measures of resilience and recovery post flood disturbance.

 Priority actions for riparian zones in all reaches should focus on weed management, increasing structural complexity of canopy such as native vines, improving riparian habitat in the form of organic litter and woody debris, and addressing undercutting, exposed roots and slumping of channel banks. Priority areas for riparian restoration are Spicketts Creek, Kalang River @ Scotchman, Kalang River @ Brierfield, and Never Never River.

1. Background

The NSW Natural Resources Monitoring Evaluation and Reporting (MER) Strategy was prepared by the Natural Resources and Environment CEO Cluster of the NSW Government in response to the Natural Resources Commission standard and targets and was adopted in August 2006. The purpose of the Strategy is to refocus the resources of NSW natural resource and environment agencies and coordinate their efforts with CMAs, Local Governments, landholders and other natural resource managers to establish a system of monitoring, evaluation and reporting on natural resource condition.

At this time there was no consistent monitoring of estuarine ecological condition in NSW. Working groups were formed to consider the most appropriate indicators and sampling designs to enable a statewide assessment of the ecological condition of rivers and estuaries. This report outlines the approach taken by stakeholders in the Bellinger LGA to supplement the MER monitoring and is aligned with the objectives of the Bellinger River Health Plan 2010.

2. Scope

Estuarine and coastal lagoon systems are focal points for the cumulative impacts of changed catchment land-use, and increasing urbanisation and development in coastal zones (Davis and Koop 2006). As a result, these ecosystems have become sensitive to nutrient enrichment and pollution, and degraded through habitat destruction and changes in biodiversity. The development of a standardised means of collecting, analysing and presenting riverine, coastal and estuarine assessments of ecological condition has been identified as a key need for coastal Catchment Management Authorities and Local Councils who are required to monitor natural resource condition, and water quality and quantity in these systems.

This project will review and integrate information from the following sources to develop an Ecohealth framework: The NSW Monitoring, Evaluation and Reporting (MER) Program currently monitoring NSW estuaries on a bi- or tri-annual basis; NSW State of Environment (SoE) and proposed State of Catchments (SoC) reports, EHMP Healthy Waterways program; proposed estuary report cards from the NLWRA (through WA D of Water), NSW Estuary Management Policy and Coastal Zone Management Manual and relevant Estuary Management Plans, sampling protocols developed by the CRC for Coastal Zone, Estuary and Waterway Management.

The Ecohealth Waterways Monitoring Program outlines a framework for the development of a catchment-based aquatic health monitoring program for rivers and estuaries in the Northern

Rivers CMA with the aim of providing consistency in monitoring and reporting, and establish the partnerships required for local and regional dissemination of outcomes. This project brings together major stakeholders in the coastal management of Northern NSW; State agencies (NRCMA, DECCW, DII Fisheries), Local Council (Bellingen) and University Researchers (UNE) to develop, refine, report and promote a standardised estuarine health assessment tool for the Bellinger/Kalang system.

This project is a pilot program to trial designs, methods and variables that may contribute to the Ecohealth framework. The main output will be specific monitoring and management plans for the study areas, with a generic framework outlining a standardised (and trialled) set of partnership, monitoring, data management and reporting protocols for implementation in coastal catchments throughout NSW. This framework will facilitate an effective reporting mechanism to communicate water quality and resource condition information to the general public stakeholders and managers through a simple report card system to be developed by the NRCMA.

3. Project Objectives

 to assess the health of coastal catchments using standardised indicators and reporting for estuaries, and upland and lowland river reaches using hydrology, water quality, riparian vegetation and habitat quality, and macroinvertebrates assemblages as indicators of ecosystem health in the Bellinger/Kalang system,

 to contribute scientific information for the development of a report card system for communicating the health of the estuarine and freshwater systems.

4. Report Structure

Part 1 of the report outlines the catchment characteristics of the Bellinger and Kalang Rivers as context of the need for river and estuarine monitoring, and to provide the background to study design and site selection processes.

5. Study Area and Study Design provides information on the catchment characteristics of the Bellinger and Kalang Rivers such as area, hydrology and land-uses. A detailed description of the study design and protocols developed for site selection are provided.

6. Study Sites section provides a detailed site description for the 22 study sites, including the range of water quality conditions measured, physical measures of channel and bank characteristics, riparian features and local disturbance issues.

Part 2 of the report provides a detailed report on the monthly water chemistry and biophysical data collected from October 2009 to September 2010. Results from the three groups of indicators used are reported at spatial scales of river and site, and temporal scales of year, season and month.

7. Water Quality section identifies trends in nutrient (nitrogen and phosphorus), chlorophyll a and suspended solids values, as well as static variables such as pH, salinity, dissolved oxygen and temperature. Sites that exceed NSW MER or ANZECC guideline thresholds are identified.

8. Macroinvertebrate assemblages collected from 10 freshwater sites in Spring 2009 and Autumn 2010 are used to assess long-term condition of in channel habitats. The taxonomic richness, abundance and diversity are reported, as well as health indicators using SIGNAL2 scores and percent EPT.

9. Riparian Condition assessment provides information for the 10 freshwater sites on the cover, structure and habitat as indicators of a health riparian ecosystem at each site, as well as an identification of local-scale disturbances to riparian zones.

Part 3 provides management recommendations for the future management of the instream and riparian condition in the Bellinger and Kalang Rivers, and identifies priorities for future monitoring within the Ecohealth framework.

PART 1

STUDY AREA, DESIGN AND SITE DESCRIPTIONS

5. Study Area and design

Study Area

The Bellinger catchment is situated on the Mid North Coast of NSW encompassing approximately 1,110 km2 (Figure 1). The two main rivers in the catchment are the Kalang River (330 km2) to the south and the Bellinger River (780 km2) to the north. The catchment is approximately 70km long and 20km wide. Most of the catchment is mountainous with limited areas of flat land associated with river and creek valleys and the coastline. Major tributaries of the Bellinger River are the Never Never and Rosewood Rivers, and Spicketts Creek and Pickett Hill Creek in the Kalang River. The Bellinger-Kalang estuary covers an area of approximately 160 km2, with the rivers sharing a common entrance to the Pacific Ocean at Urunga.

The regional climate is sub-tropical with warm, wet humid summers and mild, dry winters. Annual average rainfall for the area is 1526 mm with the majority of rainfall occurring in the summer period of December to April with average monthly rainfalls of 138─218mm (BoM 2010).

The upper catchment of the Bellinger/Kalang Rivers is predominantly forested. More than half the catchment area is contained within State Forest, National Parks and Nature Reserve boundaries (Lawson and Treloar 2003). Logged native forests are a next major land use type, with agricultural use of the floodplain for beef cattle, dairy cattle, small fruit, vegetable and nut operations. Urban areas within the catchment are dominated by the towns of Bellingen and Urunga, and a number of small settlements throughout the catchments.

The long-term flow record for the catchment is limited to gauges at Thora (205002) and a new gauge upstream of Bellingen (Fosters) on the Bellinger River, as well as rainfall-runoff models that estimate mean annual runoff is approximately 1,482,000 ML/yr (BoM 2010). Discharge data are available for additional sites and tributaries relevant to this study but the BoM would not release data due to unreliable cusum curves for these sites. Long-term flow modeling is available in Telfer and Cohen (2010).

Indicative discharge for the region was calculated from mean daily discharge at the Thora Gauge on the Bellinger River. Discharge during the study period of October 2009 to September 2010 did not include any major flooding, with a peak discharge of 5157 ML/day recorded on November 8th 2009. The minimum discharge recorded was 68 ML/day on September 14th 2010. Mean monthly discharge ranged from 98.2 ± 38.5 ML/day in September 2010 to 1290.8 ± 1003.9 ML/day in March 2010 (Figure 2). Variability in discharge was highest from October 2009 to March 2010 with the standard deviation of discharge ranging from 0.8 to 2.2 times the mean indicating highly variable (but low magnitude) flow regimes during this period. From April to September 2010 a standard deviation of 0.17 to 0.4 of the mean discharge was recorded indicating a period of relatively stable discharge.

Figure 1: Bellinger and Kelang Catchments (Source Northern Rivers Catchment management Authority, 2011)

ML/day

Discharge

Daily

Mean

Figure 2: Mean daily discharge ± standard deviation at Thora gauge (205002) on the Bellinger River from October 2009 to September 2010.

Study Design The design of the Ecohealth freshwater/estuarine monitoring program for the Bellinger and Kalang Rivers is based on the NSW Monitoring, Evaluation, Reporting (MER) protocols for Rivers and Estuaries, and aligned for reporting outcomes used in the South-East Queensland Ecosystem Health Monitoring program (EHMP) methodologies, as well as previous ecosystem health assessments undertaken within the local region. The number and location of sample sites has been designed to be statistically robust, and as such, will provide a data set that can be used to assess spatial and temporal variability of the system, and in time, further refine the monitoring program. Constraints on study design from available budgets limited the project to 22 sample locations and monthly sampling for water quality.

The location of the 10 freshwater monitoring sites (5 sites on each river) was based on selection criteria to:  identify longitudinal change within the main stem of each river system,  represent major tributaries of each river system or were identified by stakeholders as tributaries of interest for management;  compare River Styles and elevations within and across catchments,  locate ecological changes at the point of the tidal limit.

The location of the 12 estuarine monitoring sites (5 on the Bellinger River and 7 on the Kalang River) was based on selection criteria to:  identify longitudinal change within the main stem of each river system,  represent paired sites within salinity categories of; 0-15ppt, 15-30ppt and 30+ppt;  compare River Styles and elevations within and across catchments,  locate ecological changes at the point of the tidal limit.

Sampling schedule Monthly sampling for water chemistry, bi-annual sampling for freshwater macroinvertebrates, and a once-off assessment of riparian condition were undertaken from October 2009 to September 2010 (Table 1).

Each water chemistry sampling event was undertaken over a 3-day period to ensure consistency in sampling with tidal regime. The estuarine sites on the Bellinger and Kalang Rivers were sampled consistently on an incoming high tide to maximize access to all sites via boat. The average 40 minute difference in mean high tide on consecutive days facilitates comparable data collection, and required adjusted start times for each sampling event. Sites BR4 to BR8 on the Bellinger River, and KR 5 – KR11 on the Kalang River were sampled using a boat supplied by DECCW. All other sites were sampled via road access and vehicles.

Table 1: Sampling regime for field collection of water quality and biota.

Event Date Variables from Variables from freshwater sites estuary sites

1 Oct 19-23 2009 Water Quality, Water Quality Invertebrates 2 Nov 23-25 Water Quality Water Quality 3 Dec 21-23 Water Quality Water Quality 4 Jan 25-27 2010 Water Quality Water Quality 5 Feb 22-243 Water Quality Water Quality 6 March 22-24 Water Quality Water Quality 7 April 25-29 Water Quality, Water Quality Invertebrates 8 May 24-26 Water Quality Water Quality 9 June 28-30 Water Quality Water Quality 10 July 26-28 Water Quality Water Quality 11 August 23-25 Water Quality Water Quality 12 Sept 27-29 Water Quality Water Quality

6. Study Sites

Twenty two sites were selected on the Bellinger and Kalang Rivers that conform to the selection criteria outlined above (Table 2, Figure 3).

Estuarine sites are consistent with tidal river River Styles, and we have followed the MER approach of duplicating sites within known salinity zones (0-15ppt, 15-30 ppt, and 30+ppt), and are consistent with those salinity zones used by the MER process (Figure 3). Freshwater sites are representative of mountainous headwater stream, confined bedrock river with discontinuous floodplain, and alluvial meandering gravel river bed, and are consistent with the elevation zones used by the MER process (Figure 4).

Detailed site descriptions identifying the range of water quality conditions measured, physical measures of channel and bank characteristics, riparian features and local disturbance issues are provided to provide context for the ecological results.

Table 3. Names and locations of field sampling sites in the Bellinger and Kalang Rivers.

ID Location Decimal Degrees UTM 56J Elevation (m) Latitude Longitude Easting (E) Northing (S) Bellinger River

BR1 86 Richardsons Bridge -30.430113 152.666755 467993.60 6633605.16 Crossing BR2 41 Darkwood Bridge crossing -30.428820 152.770473 477961.08 6633667.52 RW1 54 Rosewood River, -30.416825 152.777546 478637.47 6635012.47 Summersville Rd Crossing

BR3 20 Gordonville Cutting (0-15ppt) -30.418012 152.847011 485305.87 6634885.00 NN1 42 Never Never River, Keoghs -30.387211 152.886018 489046.67 6638306.99 Reserve BR4 7 Marx Hill (0-15ppt) -30.465562 152.927178 493009.54 6629646.94 BR5 3 Fernmount (15-30ppt) -30.462971 152.965871 496734.22 6629918.34 BR6 3 Pacific Hwy Bridge (15- -30.459181 153.000190 500046.18 6630352.81 30ppt) BR7 1 Repton (30 + ppt) -30.444610 153.026136 502418.41 6632050.62 BR8 0 Mylestom (30+ ppt) -30.466249 153.041791 503997.81 6629453.88

Kalang River KR1 76 Kalang Rd Ford @ Kalang -30.500220 152.753223 476315.80 6625757.61 KR2 40 Pearns Bridge, Kalang Rd -30.462536 152.838124 484460.38 66299448.94 KR3 22 Sunny Corner Rd -30.481556 152.870773 487592.49 6627843.63 SC1 16 Spicketts Creek, Bowraville -30.505213 152.893608 489789.28 6625227.31 Rd KR4 14 Brierfield Bridge, Bowraville -30.502375 152.895736 489993.65 6625539.23 Rd (0-15ppt) KR5 13 South Arm Rd (0-15ppt) -30.511765 152.904935 490882.48 6624497.96 KR6 12 Pine Creek Bend (15-30ppt) -30.517845 152.922819 492592.05 6623828.43 KR7 11 Tarkeeth (15 - 30ppt) -30.509747 152.941966 494429.92 6624715.44 KR8 5 Upstream Newry Island (30+ -30.506826 152.970701 497193.61 6625061.61 ppt) KR9 4 North channel Newry Island -30.491428 152.999367 499931.17 6626752.01 (30+ppt) KR10 2 South Channel Newry Island -30.509023 152.996002 499613.15 6624803.74 (30+ppt) KR11 0 Urunga Boat ramp (30+ ppt) -30.490694 153.014087 501331.62 6626837.58

NN1

RW1 BR3 BR1 BR7 BR2 BR4 BR5 BR6

KR2 KR11 BR8 KR3 KR9 KR7 SC1 KR5 KR1 KR8 KR4 KR6 KR10

Figure 3. Location of the 22 monitoring sites in the Bellinger and Kalang Rivers. 10

Figure 4. Location of estuarine monitoring sites and salinity zones on the Bellinger and Kalang Rivers.

Bellinger River: SITE ID: BR1 Freshwater. Confined bedrock river with discontinuous floodplain Location: Most upstream site at Richardsons Bridge Crossing

Downstream Reach Upstream Reach

Water Chemistry min max pH 6.64 8.08 EC (mS/cm) 0.063 0.083 Turbidity (NTU) 0 1.0 DO (mg/L) 5.85 8.65 Water Temperature (°C) 13.35 27.5 Salinity (%) 0 0.04 Chlorophyll a (µg/L) 0.04 0.28 NOx (mg/L) 0.0038 0.212 Reactive Phosphorus (mg/L) 0.0052 0.0135 TN (mg/L) 0.0775 0.858 TP (mg/L) 0.0119 0.232 TSS (mg/L) 0 6.4 Physical left bank right bank Valley Shape assymetrical floodplain Channel Shape two stage Bar Types side/point bars UNVEGETATED Dominant Particle Size on Bars gravel Bank Shape convex concave Bank Slope (°) low (10-30°) low (10-30°) Bedform features Bed Compaction packed, unarmoured Sediment Matrix matrix filled contact framework Vegetation left bank right bank Riparian Average Cover (%) 45 75 Continuity isolated/scattered continuous Woody Debris 5 logs Native v Exotic 25n/75e Machrophyte Cover (%) <5 Disturbance left bank right bank Local Impacts/Landuse native forest native forest Channel Midofications no modifications Bed Stability Rating bed stable Vegetation Disturbance Rating moderate disturbance

Bellinger River: SITE ID: BR2 Freshwater. Confined bedrock river with discontinuous floodplain Location: Leans Bridge Crossing

Downstream Upstream

Water Chemistry min max pH 6.31 7.46 EC (mS/cm) 0.065 0.086 Turbidity (NTU) 0.5 1.0 DO (mg/L) 6.45 9.74 Water Temperature (°C) 13.93 28.7 Salinity (%) 0 0.04 Chlorophyll a (µg/L) 0.01 0.39 NOx (mg/L) 0.0037 0.0717 Reactive Phosphorus (mg/L) 0.0033 0.0077 TN (mg/L) 0.1009 0.1799 TP (mg/L) 0.009 0.0146 TSS (mg/L) 0 1.9 Physical left bank right bank Valley Shape assymetrical floodplain Channel Shape flat u-shape Bar Types bars absent Dominant Particle Size on Bars - Bank Shape concave convex Bank Slope (°) low (10-30°) steep (60-80°) Bedform features Bed Compaction moderate compaction Sediment Matrix framework dilated Vegetation left bank right bank Riparian Average Cover (%) 65 85 occasional Continuity clumps continuous Woody Debris 5 logs Native v Exotic 25n/75e Machrophyte Cover (%) <5 Disturbance left bank right bank Local Impacts/Landuse grazing native forest Channel Midofications no modifications Bed Stability Rating bed stable Vegetation Disturbance Rating moderate disturbance

Rosewood River SITE ID: RW1 Freshwater. Confined bedrock river with discontinuous floodplain Location: Rosewood River, Summersville Rd Crossing

Downstream Upstream Water Chemistry min max pH 6.4 8.76 EC (mS/cm) 0.052 0.61 Turbidity (NTU) 0 1.6 DO (mg/L) 7.5 9.09 Water Temperature (°C) 12.01 25.9 Salinity (%) 0 0.04 Chlorophyll a (µg/L) 0 0.36 NOx (mg/L) 0.0168 0.1741 Reactive Phosphorus (mg/L) 0.0021 0.008 TN (mg/L) 0.0791 0.2866 TP (mg/L) 0.005 0.0111 TSS (mg/L) 0 1.5 Physical left bank right bank Valley Shape shallow valley Channel Shape flat U shaped Bar Types side point bars VEGETATED Dominant Particle Size on Bars boulder/cobble Bank Shape concave concave Bank Slope (°) moderate (30-60) low (10-30) Bedform features Bed Compaction moderate compaction Sediment Matrix open framework Vegetation left bank right bank Riparian Average Cover (%) >85 75 Continuity continuous continuous Woody Debris 2 logs Native v Exotic 75n/25e Machrophyte Cover (%) 0 Disturbance left bank right bank Local Impacts/Landuse native forest native forest Channel Midofications no modifications Bed Stability Rating bed stable Vegetation Disturbance Rating very low disturbance

Bellinger River SITE ID: BR3 Freshwater – Limit of Tidal influence. Alluvial meandering gravel bed river Location: Gordonville Cutting

Downstream Upstream

Water Chemistry min max pH 6.54 8.43 EC (mS/cm) 0.026 0.086 Turbidity (NTU) 0 10 DO (mg/L) 0.5 1.9 Water Temperature (°C) 14.7 29.6 Salinity (%) 0 0.04 Chlorophyll a (µg/L) 0 0.36 NOx (mg/L) 0.0123 0.0974 Reactive Phosphorus (mg/L) 0.0024 0.0077 TN (mg/L) 0.0858 0.2577 TP (mg/L) 0.0074 0.0138 TSS (mg/L) 0 2.3 Physical left bank right bank Valley Shape symmetrical floodplain Channel Shape U shaped Bar Types side/point bars VEGETATED Dominant Particle Size on Bars boulder/cobble Bank Shape undercut convex Bank Slope (°) vertical (80-90) low (10-30) Bedform features Bed Compaction tightly packed, armoured Sediment Matrix framework dilated Vegetation left bank right bank Riparian Average Cover (%) 30 20 semi- Continuity none continuous Woody Debris 0 Native v Exotic 25n/75e Machrophyte Cover (%) 0 Disturbance left bank right bank Local Impacts/Landuse grazing grazing Channel Midofications no modifications (flood damage) Bed Stability Rating severe erosion Vegetation Disturbance Rating very high disturbance

Never Never River SITE ID: NN1 Freshwater. Alluvial meandering gravel bed river Location: Never Never River, Keoghs Reserve

Downstream Upstream Water Chemistry min max pH 6.68 7.9 EC (mS/cm) 0.038 0.048 Turbidity (NTU) 0 2.0 DO (mg/L) 5.8 9.5 Water Temperature (°C) 13.44 23.9 Salinity (%) 0 0.03 Chlorophyll a (µg/L) 0 0.32 NOx (mg/L) 0.0214 0.1946 Reactive Phosphorus (mg/L) 0.0013 0.0052 TN (mg/L) 0.0737 0.2847 TP (mg/L) 0.0021 0.0101 TSS (mg/L) 0 1.3 Physical left bank right bank Valley Shape symmetrical floodplain Channel Shape U shaped Bar Types side/point bars VEGETATED Dominant Particle Size on Bars boulder/cobble Bank Shape convex concave Bank Slope (°) low (10-30) low (10-30) Bedform features Bed Compaction tightly packed, armoured Sediment Matrix framework dilated Vegetation left bank right bank Riparian Average Cover (%) 40 75 Continuity continuous continuous Woody Debris 2 Native v Exotic 25n/75e Machrophyte Cover (%) 0 Disturbance left bank right bank Local Impacts/Landuse grazing grazing Channel Midofications no modifications Bed Stability Rating moderate erosion Vegetation Disturbance Rating high disturbance

Bellinger River SITE ID: BR4 Estuarine 0-15ppt. Tidal River Location: Marx Hill

Upstream view

Water Chemistry min max pH 6.83 8.04 EC (mS/cm) 0.068 18.5 Turbidity (NTU) 0 1.2 DO (mg/L) 4.75 7.53 Water Temperature (°C) 14.5 28.1 Salinity (%) 0.01 10.91 Chlorophyll a (µg/L) 0.04 1.4 NOx (mg/L) 0.0057 0.0656 Reactive Phosphorus (mg/L) 0.0012 0.0065 TN (mg/L) 0.0531 0.2677 TP (mg/L) 0.0084 0.0168 TSS (mg/L) 0 5.5 Physical left bank right bank Valley Shape Channel Shape Bar Types Dominant Particle Size on Bars Bank Shape To be assessed Bank Slope (°) Bedform features Bed Compaction Sediment Matrix Vegetation left bank right bank Riparian Average Cover (%) Continuity Woody Debris To be assessed Native v Exotic Machrophyte Cover (%) Disturbance left bank right bank Local Impacts/Landuse Channel Midofications To be assessed Bed Stability Rating Vegetation Disturbance Rating

Bellinger River SITE ID: BR5 Estuarine 15-30ppt. Tidal River Location: Fernmount

Downstream Reach Upstream Reach

Water Chemistry min max pH 6.64 8.23 EC (mS/cm) 0.113 31 Turbidity (NTU) 0 2.6 DO (mg/L) 3.98 6.76 Water Temperature (°C) 14.7 29.2 Salinity (%) 0.27 19.04 Chlorophyll a (µg/L) 0.08 .79 NOx (mg/L) 0.0019 0.0498 Reactive Phosphorus (mg/L) 0.0017 0.0047 TN (mg/L) 0.1081 0.3649 TP (mg/L) 0.0077 0.0388 TSS (mg/L) 1.4 5.3 Physical left bank right bank Valley Shape Channel Shape Bar Types Dominant Particle Size on Bars Bank Shape To be assessed Bank Slope (°) Bedform features Bed Compaction Sediment Matrix Vegetation left bank right bank Riparian Average Cover (%) Continuity Woody Debris To be assessed Native v Exotic Machrophyte Cover (%) Disturbance left bank right bank Local Impacts/Landuse Channel Midofications To be assessed Bed Stability Rating Vegetation Disturbance Rating

Bellinger River SITE ID: BR6 Estuarine 15 - 30ppt. Tidal River Location: Pacific Hwy Bridge

Downstream Reach Upstream Reach Water Chemistry min max pH 6.27 9.03 EC (mS/cm) 0.232 43.2 Turbidity (NTU) 0 1.2 DO (mg/L) 3.9 6.86 Water Temperature (°C) 15.2 29.5 Salinity (%) 0.88 21.99 Chlorophyll a (µg/L) 0.08 0.04 NOx (mg/L) 0.0009 0.0727 Reactive Phosphorus (mg/L) 0.0014 0.0065 TN (mg/L) 0.0858 0.4669 TP (mg/L) 0.005 0.0295 TSS (mg/L) 2.2 9.4 Physical left bank right bank Valley Shape Channel Shape Bar Types Dominant Particle Size on Bars Bank Shape To be assessed Bank Slope (°) Bedform features Bed Compaction Sediment Matrix Vegetation left bank right bank Riparian Average Cover (%) Continuity Woody Debris To be assessed Native v Exotic Machrophyte Cover (%) Disturbance left bank right bank Local Impacts/Landuse Channel Midofications To be assessed Bed Stability Rating Vegetation Disturbance Rating

Bellinger River SITE ID: BR7 Estuarine 30+ppt. Tidal River Location: Repton

Right Bank Left Bank

Water Chemistry min max pH 6.73 9.04 EC (mS/cm) 5.29 53.7 Turbidity (NTU) 0 2.1 DO (mg/L) 4.7 6.57 Water Temperature (°C) 15.3 28.8 Salinity (%) 1.61 28.95 Chlorophyll a (µg/L) 0.04 0.83 NOx (mg/L) 0.0002 0.0834 Reactive Phosphorus (mg/L) 0.0013 0.0071 TN (mg/L) 0.0947 0.6392 TP (mg/L) 0.0042 0.0278 TSS (mg/L) 1.7 15.2 Physical left bank right bank Valley Shape Channel Shape Bar Types Dominant Particle Size on Bars Bank Shape To be assessed Bank Slope (°) Bedform features Bed Compaction Sediment Matrix Vegetation left bank right bank Riparian Average Cover (%) Continuity Woody Debris To be assessed Native v Exotic Machrophyte Cover (%) Disturbance left bank right bank Local Impacts/Landuse Channel Midofications To be assessed Bed Stability Rating Vegetation Disturbance Rating

Bellinger River SITE ID: BR8 Estuarine 30+ ppt. Tidal River Location: Mylestom

Downstream Reach Upstream Reach

Water Chemistry min max pH 6.83 9.03 EC (mS/cm) 15.5 66.2 Turbidity (NTU) 0 0.9 DO (mg/L) 5.2 7.09 Water Temperature (°C) 16 28.5 Salinity (%) 2.62 32.54 Chlorophyll a (µg/L) 0.04 0.47 NOx (mg/L) 0.0005 0.03 Reactive Phosphorus (mg/L) 0.0008 0.055 TN (mg/L) 0.117 0.2776 TP (mg/L) 0.0024 0.0167 TSS (mg/L) 5.4 14.6 Physical left bank right bank Valley Shape Channel Shape Bar Types Dominant Particle Size on Bars Bank Shape To be assessed Bank Slope (°) Bedform features Bed Compaction Sediment Matrix Vegetation left bank right bank Riparian Average Cover (%) Continuity Woody Debris To be assessed Native v Exotic Machrophyte Cover (%) Disturbance left bank right bank Local Impacts/Landuse Channel Midofications To be assessed Bed Stability Rating Vegetation Disturbance Rating

Kalang River SITE ID: KR1 Freshwater. Confined bedrock river with discontinuous floodplain Location: Most upstream site Kalang Rd Ford @ Kalang

Downstream Upstream Water Chemistry min max pH 6.64 8.85 EC (mS/cm) 0.008 0.086 Turbidity (NTU) 0 3 DO (mg/L) 5.06 9.06 Water Temperature (°C) 12.4 26.7 Salinity (%) 0 0.05 Chlorophyll a (µg/L) 0 0.15 NOx (mg/L) 0.009 0.0555 Reactive Phosphorus (mg/L) 0.0013 0.0121 TN (mg/L) 0.0519 0.2001 TP (mg/L) 0.0036 0.0088 TSS (mg/L) 0 5.1 Physical left bank right bank Valley Shape assymetrical floodplain Channel Shape U shaped Bar Types bars absent Dominant Particle Size on Bars gravel Bank Shape concave concave Bank Slope (°) moderate (30-60) steep (60-80) Bedform features Bed Compaction low compaction Sediment Matrix matrix dominated Vegetation left bank right bank Riparian Average Cover (%) Continuity continuous continuous Woody Debris 4 logs Native v Exotic 60n/40e Machrophyte Cover (%) 0 Disturbance left bank right bank Local Impacts/Landuse grazing urban residential recreation recreation irrigation pumps irrigation pumps Channel Midofications no modifications Bed Stability Rating bed stable Vegetation Disturbance Rating low disturbance

Kalang River SITE ID: KR2 Freshwater: Confined bedrock river with discontinuous floodplain Location: Pearns Bridge, Kalang Rd

Riffle site at Bridge Pool downstream of Bridge Water Chemistry min max pH 7 7.89 EC (mS/cm) 0.085 0.098 Turbidity (NTU) 0 2.1 DO (mg/L) 5.89 9.47 Water Temperature (°C) 13.24 29.1 Salinity (%) 0 0.05 Chlorophyll a (µg/L) 0 0.43 NOx (mg/L) 0.0043 0.028 Reactive Phosphorus (mg/L) 0.0008 0.0043 TN (mg/L) 0.0434 0.1306 TP (mg/L) 0.0031 0.0122 TSS (mg/L) 0 1.7 Physical left bank right bank Valley Shape assymetrical floodplain Channel Shape two stage side/point + mid-channel Bar Types VEGETATED Dominant Particle Size on Bars gravel Bank Shape concave convex Bank Slope (°) steep (60-80) low (10-30) Bedform features Bed Compaction low compaction Sediment Matrix matrix dominated Vegetation left bank right bank Riparian Average Cover (%) occassional Continuity continuous clumps Woody Debris 8 logs Native v Exotic 60n/40e Machrophyte Cover (%) 0 Disturbance left bank right bank Local Impacts/Landuse native forest grazing Channel Midofications no modifications Bed Stability Rating bed stable Vegetation Disturbance Rating moderate disturbances

Kalang River SITE ID: KR3 Freshwater. Confined bedrock river with discontinuous floodplain Location: Sunny Corner Rd

Downstream riffle Upstream pool Water Chemistry min max pH 6.67 7.61 EC (mS/cm) 0.081 0.102 Turbidity (NTU) 0 2.6 DO (mg/L) 5.3 9.91 Water Temperature (°C) 13.74 28.6 Salinity (%) 0 0.05 Chlorophyll a (µg/L) 0.08 0.9 NOx 0.0036 0.0156 Reactive Phosphorus (mg/L) 0.0008 0.0043 TN (mg/L) 0.0532 0.4212 TP (mg/L) 0.0045 0.0121 TSS (mg/L) 0.7 9.32 Physical left bank right bank Valley Shape asymmetrical floodplain Channel Shape flat U shaped Bar Types bars absent Dominant Particle Size on Bars gravel Bank Shape undercut undercut Bank Slope (°) vertical (80-90) vertical (80-90) Bedform features Bed Compaction low compaction Sediment Matrix matrix dominated Vegetation left bank right bank Riparian Average Cover (%) Continuity occassional clumps occassional clumps Woody Debris 1 log Native v Exotic 20n/80e Machrophyte Cover (%) <5 Disturbance left bank right bank Local Impacts/Landuse grazing grazing Channel Midofications no modification (flood damage) Bed Stability Rating severe erosion Vegetation Disturbance Rating very high disturbance

Spicketts Creek SITE ID: SC1 Freshwater tributary. Confined bedrock river with discontinuous floodplain Location: Spicketts Creek, Bowraville Rd

Downstream reach Upstream reach

Water Chemistry min max pH 5.88 8.01 EC (mS/cm) 0.093 0.155 Turbidity (NTU) 0 72 DO (mg/L) 3.1 7.82 Water Temperature (°C) 12.04 25.1 Salinity (%) 0 0.06 Chlorophyll a (µg/L) 0 0.55 NOx 0.0061 0.072 Reactive Phosphorus (mg/L) 0.0008 0.0402 TN (mg/L) 0.0758 0.3979 TP (mg/L) 0.0047 0.0596 TSS (mg/L) 0.2 17.1 Physical left bank right bank Valley Shape symmetrical floodplain Channel Shape deepened U shape Bar Types bars absent Dominant Particle Size on Bars - Bank Shape convex undercut Bank Slope (°) low (10-30) steep (60-80) Bedform features Bed Compaction low compaction Sediment Matrix matrix filled contact framework Vegetation left bank right bank Riparian Average Cover (%) occasional semi- Continuity clumps continuous Woody Debris 1 log Native v Exotic 60n/40e Machrophyte Cover (%) 0 Disturbance left bank right bank Local Impacts/Landuse grazing grazing Channel Midofications no modifications Bed Stability Rating severe erosion Vegetation Disturbance Rating very high disturbance

Kalang River SITE ID: KR4 Limit of Tidal influence Location: Brierfield Bridge, Bowraville Rd

Downstream reach Upstream reach Water Chemistry min max pH 6.33 8.37 EC (mS/cm) 0.085 0.168 Turbidity (NTU) 0 1.0 DO (mg/L) 4.79 8.82 Water Temperature (°C) 13.8 26.9 Salinity (%) 0 0.08 Chlorophyll a (µg/L) 0 0.6 NOx 0.0097 0.0206 Reactive Phosphorus (mg/L) 0.0008 0.0056 TN (mg/L) 0.0783 0.2147 TP (mg/L) 0.0054 0.0133 TSS (mg/L) 0 3.3 Physical left bank right bank Valley Shape shallow valley Channel Shape flat U shaped Bar Types side/point bars VEGETATED Dominant Particle Size on Bars boulder/cobble Bank Shape undercut undercut Bank Slope (°) vertical (80-90) vertical (80-90) Bedform features Bed Compaction moderate compaction Sediment Matrix open framework Vegetation left bank right bank Riparian Average Cover (%) Continuity occassional clumps continuous Woody Debris 2 logs Native v Exotic 60n/40e Machrophyte Cover (%) 0 Disturbance left bank right bank Local Impacts/Landuse grazing grazing Channel Midofications no modifications Bed Stability Rating severe erosion Vegetation Disturbance Rating very high disturbance

Kalang River SITE ID: KR5 Estuarine 0-15ppt Location: South Arm Rd

Right Bank

Water Chemistry min max pH 6.32 8.14 EC (mS/cm) 0.137 21.6 Turbidity (NTU) 0 0.8 DO (mg/L) 5.15 8.58 Water Temperature (°C) 14.5 27.6 Salinity (%) 0.17 12.83 Chlorophyll a (µg/L) 0 0.67 NOx 0.0018 0.0324 Reactive Phosphorus (mg/L) 0.0011 0.004 TN (mg/L) 0.0966 0.2377 TP (mg/L) 0.003 0.0113 TSS (mg/L) 1 6.4 Physical left bank right bank Valley Shape Channel Shape Bar Types Dominant Particle Size on Bars Bank Shape To be assessed Bank Slope (°) Bedform features Bed Compaction Sediment Matrix Vegetation left bank right bank Riparian Average Cover (%) Continuity Woody Debris To be assessed Native v Exotic Machrophyte Cover (%) Disturbance left bank right bank Local Impacts/Landuse Channel Midofications To be assessed Bed Stability Rating Vegetation Disturbance Rating

Kalang River SITE ID: KR6 Estuarine 15-30ppt Location: Pine Creek Bend

Downstream Reach Water Chemistry min max pH 6 8.2 EC (mS/cm) 0.22 28.2 Turbidity (NTU) 0 1.2 DO (mg/L) 4.19 9.7 Water Temperature (°C) 15 28.3 Salinity (%) 0.66 17.2 Chlorophyll a (µg/L) 0.04 0.79 NOx 0.0009 0.0331 Reactive Phosphorus (mg/L) 0.0008 0.0039 TN (mg/L) 0.0634 0.2093 TP (mg/L) 0.0007 0.0078 TSS (mg/L) 2.8 6.6 Physical left bank right bank Valley Shape Channel Shape Bar Types Dominant Particle Size on Bars Bank Shape To be assessed Bank Slope (°) Bedform features Bed Compaction Sediment Matrix Vegetation left bank right bank Riparian Average Cover (%) Continuity Woody Debris To be assessed Native v Exotic Machrophyte Cover (%) Disturbance left bank right bank Local Impacts/Landuse Channel Midofications To be assessed Bed Stability Rating Vegetation Disturbance Rating

Kalang River SITE ID: KR7 Estuarine 15-30ppt Location: Tarkeeth

Downstream Reach Upstream Reach

Water Chemistry min max pH 6.35 8.67 EC (mS/cm) 7.08 258 Turbidity (NTU) 0 2.0 DO (mg/L) 5.1 9.44 Water Temperature (°C) 15.8 30.1 Salinity (%) 1.66 26.24 Chlorophyll a (µg/L) 0 1.38 NOx 0.0005 0.0137 Reactive Phosphorus (mg/L) 0.0008 0.0034 TN (mg/L) 0.0868 0.2918 TP (mg/L) 0.0006 0.0133 TSS (mg/L) 0 11.5 Physical left bank right bank Valley Shape Channel Shape Bar Types Dominant Particle Size on Bars Bank Shape To be assessed Bank Slope (°) Bedform features Bed Compaction Sediment Matrix Vegetation left bank right bank Riparian Average Cover (%) Continuity Woody Debris To be assessed Native v Exotic Machrophyte Cover (%) Disturbance left bank right bank Local Impacts/Landuse Channel Midofications To be assessed Bed Stability Rating Vegetation Disturbance Rating

Kalang River SITE ID: KR8 Estuarine 15-30ppt Location: Upstream Newry Island

Downstream Reach Water Chemistry min max pH 6.84 8.93 EC (mS/cm) 13.5 52 Turbidity (NTU) 0 2.1 DO (mg/L) 4.1 6.21 Water Temperature (°C) 15.5 29.6 Salinity (%) 1.9 28.36 Chlorophyll a (µg/L) 0.04 1.03 NOx 0.0008 0.0209 Reactive Phosphorus (mg/L) 0.0008 0.0047 TN (mg/L) 0.0634 0.3386 TP (mg/L) 0.0007 0.0107 TSS (mg/L) 3.6 109.7 Physical left bank right bank Valley Shape Channel Shape Bar Types Dominant Particle Size on Bars Bank Shape To be assessed Bank Slope (°) Bedform features Bed Compaction Sediment Matrix Vegetation left bank right bank Riparian Average Cover (%) Continuity Woody Debris To be assessed Native v Exotic Machrophyte Cover (%) Disturbance left bank right bank Local Impacts/Landuse Channel Midofications To be assessed Bed Stability Rating Vegetation Disturbance Rating

Kalang River SITE ID: KR9 Estuarine 15-30ppt Location: North Channel Newry Island

Upstream Reach Water Chemistry min max pH 6.78 8.91 EC (mS/cm) 20.7 51.5 Turbidity (NTU) 0 1.7 DO (mg/L) 4.39 9.06 Water Temperature (°C) 16.1 30 Salinity (%) 2.27 30.08 Chlorophyll a (µg/L) 0.08 1.11 NOx 0.0015 0.019 Reactive Phosphorus (mg/L) 0.0008 0.006 TN (mg/L) 0.1217 0.2377 TP (mg/L) 0.0013 0.005 TSS (mg/L) 5.6 15.7 Physical left bank right bank Valley Shape Channel Shape Bar Types Dominant Particle Size on Bars Bank Shape To be assessed Bank Slope (°) Bedform features Bed Compaction Sediment Matrix Vegetation left bank right bank Riparian Average Cover (%) Continuity Woody Debris To be assessed Native v Exotic Machrophyte Cover (%) Disturbance left bank right bank Local Impacts/Landuse Channel Midofications To be assessed Bed Stability Rating Vegetation Disturbance Rating

Kalang River SITE ID: KR10 Estuarine 30+ppt Location: South Channel Newry Island

Upstream Reach Water Chemistry min max pH 6.66 8.95 EC (mS/cm) 23.2 59.9 Turbidity (NTU) 0 1.7 DO (mg/L) 4.31 6.5 Water Temperature (°C) 16.3 29.7 Salinity (%) 2.44 31.53 Chlorophyll a (µg/L) 0.08 0.97 NOx 0.0009 0.0159 Reactive Phosphorus (mg/L) 0.0008 0.0208 TN (mg/L) 0.1154 0.4233 TP (mg/L) 0.0016 0.0097 TSS (mg/L) 5.3 28.7 Physical left bank right bank Valley Shape Channel Shape Bar Types Dominant Particle Size on Bars Bank Shape To be assessed Bank Slope (°) Bedform features Bed Compaction Sediment Matrix Vegetation left bank right bank Riparian Average Cover (%) Continuity Woody Debris To be assessed Native v Exotic Machrophyte Cover (%) Disturbance left bank right bank Local Impacts/Landuse Channel Midofications To be assessed Bed Stability Rating Vegetation Disturbance Rating

Kalang River SITE ID: KR11 Estuarine 30+ ppt Location: Urunga Boat Ramp

Left Bank Upstream Reach Water Chemistry min max pH 6.45 8.75 EC (mS/cm) 42.6 66.8 Turbidity (NTU) 0 0.7 DO (mg/L) 5.53 7.21 Water Temperature (°C) 17.5 27.4 Salinity (%) 3.39 37.18 Chlorophyll a (µg/L) 0 1.38 NOx 0.0002 0.0511 Reactive Phosphorus (mg/L) 0.0021 0.0106 TN (mg/L) 0.0992 0.3276 TP (mg/L) 0.0016 0.016 TSS (mg/L) 3.8 20.1 Physical left bank right bank Valley Shape Channel Shape Bar Types Dominant Particle Size on Bars Bank Shape To be assessed Bank Slope (°) Bedform features Bed Compaction Sediment Matrix Vegetation left bank right bank Riparian Average Cover (%) Continuity Woody Debris To be assessed Native v Exotic Machrophyte Cover (%) Disturbance left bank right bank Local Impacts/Landuse Channel Midofications To be assessed Bed Stability Rating Vegetation Disturbance Rating

PART 2

ECOLOGICAL INDICATORS: WATER QUALITY, MACROINVERTEBRATES AND RIPARAIN CONDITION

The indicators chosen focus on the condition of the system to best identify the stressors and pressures that cause change in ecological condition. The selection of indicators (and groupings of indicators) represents elements of the structure, function and composition of riverine and estuarine ecosystems.

7. Water Quality Indicators 7.1 Background

Assessing the impacts of land-use change on the ecological health of rivers and streams is an important issue for the management of water resources in Australia. Traditionally, these assessments have been dominated by the measurement of patterns in species distribution and abundance which contribute important information such as the status of threatened species and their habitat requirements. However, many goals of river management refer to concepts of sustainability, viability and resilience that require an implicit knowledge of ecosystem or landscape-level interactions and processes influencing these organisms or populations

The water chemistry of rivers and estuaries can be an ideal measure of their ecological condition by providing an integrated response to a broad range of catchment disturbances. Nutrients such as nitrogen, phosphorus, and carbon can play an integral role in regulating rates of primary production these systems. However, anthropogenic changes to catchment land-use have led to increased supply of nutrients from diffuse or point sources, and altered light and turbidity regimes through increased suspended sediment loads and loss of riparian vegetation. These landscape-level processes define the supply of contaminants to a stream and provide the framework within which other processes operate at smaller spatial scales and shorter temporal scales to regulate their supply and availability.

Table 4. Water quality measurements taken each month from all sites.

In situ measurements Water quality samples for laboratory analysis

 Water depth  Total nutrients (nitrogen and phosphorus)  pH  Dissolved nutrients (nitrate, nitrite, and phosphate)  Temperature  Chlorophyll a  Salinity  Total Suspended Solids (TSS)  Dissolved oxygen  Turbidity

7.2 Field and laboratory methods At each sampling site, insitu water quality measurements were measured with the use of a Horiba water quality multi-probe or Hydrolab Quanta multi-probe (pH, Conductivity, Dissolved Oxygen (DO), Temperature, Turbidity). The following procedural steps are outlined to standardise the collection of these data and to identify quality control.

Water Quality Probe Calibration and Use The water quality probe(s) were calibrated each day prior to use in the field. At each sample site, field measurements for the water column profile was taken at near surface (approx. 0.2m below surface), and at 1 m intervals through the water column to a depth of 0.5m from the bottom (epibenthic). Measurements for each water quality parameter using the multi- probe were recorded at each interval. In freshwater sites that were less than 1 meter in depth, surface and epibenthic measurements were taken and maximum sampling depths noted. Data were recorded on proforma data recording sheets (Appendix 1).

Water Quality Sampling Water samples were collected at each site for the determination of Chlorophyll a, total and dissolved nutrients, and total suspended solids. Samples were collected at near surface (<0.2m) and obtained with the use of a hand held sampling device to ensure sample is taken at least 1.5m from the edge of the boat or riverbank. Samples were transferred to acid-washed and rinsed (3x rinsed with sample water) 125mL containers. Duplicate samples for each parameter were taken from each site, and a third sample of each parameter was collected from a random subset of sites for quality assurance (QA) processing at an independent laboratory. The following procedures for sample collection and treatment are provided for each determination.

Chlorophyll a Water column chlorophyll a is a measure of the photosynthetic biomass of algae/phytoplankton. These organisms are central to important nutrient and biogeochemical processes, and as such may respond to disturbance before effects on higher organisms are detected. This is because the higher organisms depend on processes mediated by algal communities. Consequently, they form the base of food webs supporting zooplankton, grazers such as crustaceans, insects, molluscs and some fish. The short generation time, responsiveness to environmental condition and the availability of sound, quantitative methodologies such as chlorophyll a make these measures of phytoplankton ideally suited as indicators of disturbance in aquatic systems. Information can be collected, processed and analysed at time scales relevant to both scientific and management interests.

In the field, a 1 litre bottle of water from a 0.5m depth was collected using the hand held sampling device at each site, labelled, and placed on ice in an esky for transport to the laboratory. Sample processing was carried out within 48 hours of collection. After filtration, samples were stored at below minus 4 degrees C and protected from the light. a) Place a GF/F filter, using forceps, textured side up into the filtration apparatus just prior to filtration. b) Filter a sufficient amount of sample (100-1,000ml measured with a graduated cylinder), to produce a green colour on the filter paper, or until the flow through the filter paper at ½ atmosphere pressure (approx. 7PSI) is reduced to a trickle. When approximately 10-15mL of sample remains on the filter, add 5-10 drops of the MgCO3 powder to preserve the chlorophyll. Thoroughly rinse the filter apparatus and graduated cylinder, using a squirt bottle with deionised water. Drain the filter thoroughly to remove all signs of moisture. c) Record the sample volume filtered on the field data sheet. The amount of water filtered is subject to the level of turbidity at the sampling site. d) Using forceps, fold and remove the filter and carefully place into the bottom portion of the prelabled culture tube and close tightly, wrap in aluminium foil, place into a labelled ziplock bag and immediately freeze. e) The concentration of chlorophyll-a was measured by filtering 1 L of unfiltered sample water was through 934-AH RTU Glass Microfiber filter paper using an EYELA Tokyo Rakahikai Coorperation Aspirator A-35. The filter paper was then placed in 10 ml of 90% ethanol. The solution was then refrigerated for 24 hours. The samples were then centrifuged. The absorption spectra were recorded using a UV-1700 Pharmaspec UV-visible spectrometer at 666 nm and 750 nm.

Total Suspended Solids Total suspended solids is a direct measure of turbidity of the water In the field, collect a 1 litre bottle of water from a 0.5m depth at each site using the hand held sampling device, label, and place in a cool dark esky. a) Place a pre-weighed GF/F filter, using forceps, textured side up into the filtration apparatus just prior to filtration. b) Filter a sufficient amount of sample (100-1,000ml measured with a graduated cylinder), to produce a colour on the filter paper, or until the flow through the filter paper at ½ atmosphere pressure (approx. 7PSI) is reduced to a trickle. Thoroughly rinse the filter apparatus and graduated cylinder, using a squirt bottle with deionised water. Drain the filter thoroughly to remove all signs of moisture. c) Using forceps, fold and remove the filter and carefully place into the bottom portion of the prelabled culture tube and close tightly, wrap in aluminium foil, place into a labelled ziplock bag and immediately freeze.

d) TSS were measured by filtering 1L of sample water through a 934-AH RTU Glass Microfiber filter paper, with a known weight, using a EYELA Tokyo Rakahikai Coorperation Aspirator A-35. The filter paper with retained material was then placed into a foil envelope and dried in an oven at 50ºC. They were reweighed after they dried to gain a measure of the weight of the TSS on each sample. The organic content of the TSS was then analysed by placing the filter paper into the furnace for 4 hours at 500ºC. The filter paper was then reweighed and the organic content calculated.

Inorganic Nutrients For inorganic nutrients, we collected 3 x 125mL bottles of water from a 0.2m depth at each site using the hand held sampling device. Samples for total nitrogen and total phosphorus remain as separate unfiltered samples. Water is transferred into a pre-rinsed, pre-labelled, clean 125mL sample container and immediately placed in a cool dark esky. Samples remained frozen until time of analysis. Duplicate samples for quality assurance processing at an independent laboratory remained frozen until analyzed. For organic nutrients, we collected 3 x 125ml bottle of water from a 0.5m depth at each site using the hand held sampling device. Approximately 125mL of water is passed through a GF/C filter paper (effective pore size 0.7µm) in the field and collected into a pre-rinsed, pre-labelled, clean sample container and immediately placed in a cool dark esky. Samples remained frozen until time of analysis. Duplicate samples for quality assurance processing at an independent laboratory remained frozen until analyzed.

Nitrogen was measured by digesting an unfiltered water sample in a digestion tube with 10 ml of digestion mixture. This contained 40 g of di-potassium-peroxodisulfate (K2S2O8) and 9 g of sodium hydroxide (NaOH) in 1000 ml of Milli Q water. This sample was then digested in the autoclave for 20 minutes. 5 ml of the sample was then placed into a 50 ml acid washed measuring cylinder and diluted to 50 ml (Hosomi & Sudo 1986). 5 ml of buffer solution was added; 100 g of NH4Cl, 20 g sodium tetra borate and 1 g EDTA to 1 L with Milli Q water. 50 ml of each sample was measured into a numbered jar. The samples were then filtered. Firstly, the cadmium reduction column was rinsed with 10% buffer solution, making sure the cadmium granules remained covered at all times by either the 10% buffer of the sample. The column was drained to 5 mm above the cadmium granules, and 25 ml of the first sample added. This was collected in a separate beaker for wastes as it drained through to rinse the column and discarded. The column was then filled with the sample and 20 ml was collected in the same sample jar. 1 ml of sulfanilamide solution was added and mixed thoroughly. After 2 minutes 1 ml of dihydrochloride solution was added and mixed. This was repeated for all water samples. After 10 minutes, the absorbance of each sample was measured using a UV-1700 Pharmaspec UV-visible spectrometer at 543 nm. This colormetric determination of nitrogen can be used when nitrogen is in the range 0.0125 to 2.25 g/ml. Samples must also be prepared before analyzing the samples

to calculate linear regression at 0 g/ml, 0.05 g/ml, 0.2 g/ml, 0.5 g/ml, 1 g/ml, 2 g/ml and 5 g/ml of known nitrogen concentration.

Phosphorus was measured by digesting an unfiltered water sample in a digestion tube with 10 ml of digestion mixture. This contained 40 g of di-potassium-peroxodisulfate (K2S2O8) and 9 g of sodium hydroxide (NaOH) in 1000 ml of Milli Q water. This sample was then digested in the autoclave for 20 minutes. 20 ml of sample was then added to a plastic SRP tube with 2 ml of colour reagent; 20 ml of ascorbic acid solution with 50 ml of molybdate antimony solution. This was repeated for all water samples. After 8 minutes, the absorbance of each sample was measured using a UV-1700 Pharmaspec UV-visible spectrometer at 705 nm. Samples must also be prepared before analyzing the samples to calculate linear regression at 0 g/ml, 0.05 g/ml, 0.2 g/ml, 0.5 g/ml, 1 g/ml, 2 g/ml and 5 g/ml of known nitrogen concentration.

Laboratory QA/QC Quality control was maintained with the laboratory by the use of standard analytical methods, analysis of QA/QC samples at the DECCW Lidcombe Laboratories, and the regular calibration and maintenance of laboratory instrumentation. An additional water chemistry sample was collected (via random number generator) from selected sites on each sample occasion and sent to an independent laboratory for analysis. These QA samples represented 5% of the total number of samples collected. Results confirmed no significant difference between results for N and P between laboratories.

ANZECC and MER water quality guidelines

The ANZECC Water Quality Guidelines (the guidelines) established in 1992 under the Commonwealth’s National Water Quality Management Strategy (NWQMS), provide a scientifically informed framework for the water quality objectives required to maintain current and future water resources and environmental values (ANZECC, 2000b). The ANZECC guidelines were created in response to growing understanding of the potential for water quality to be a limiting factor to social and economic growth. The guidelines were derived from reviewing water quality guidelines developed overseas. However; Australian guidelines were also incorporated where available (ANZECC, 1994b).

The ANZECC Australian Water Quality Guidelines for Fresh and Marine Waters was released in 1992, and developed using two approaches: 1. an empirical approach which used the Precautionary Principle to create conservative trigger values from all available and acceptable national and international data. This method implemented data from only the most sensitive taxa in order to ensure the protection of these species.

2. the modeling of all available and acceptable national and international data into a statistical distribution with the confidence intervals of 90% and 50%. Trigger values are conservative thresholds or desired concentration levels for different water quality indicators. When an indicator is below the trigger value there is a low risk present to the protection of that environment. However, when an indicator is above the trigger value there is a risk that the ecosystem will not be protected. In cases where the trigger value is exceeded further research and remediation of the risk identified should be conducted. Where a numerical value cannot be derived for a water quality indicator a target load may be set, for example the salinity guideline, or a descriptive statement for example for oil there should be no visible surface film, or an index of ecosystem health for example percentage cover of an algal bloom. The Australian and New Zealand Environment Conservation Council (ANZECC) Guidelines (2000 and 2006) provide threshold values for freshwater and estuarine systems for pH, dissolved oxyegen (DO), electrical conductivity (EC), salinity and nutrients such as nitrogen (N) and phosphorus (P). In addition, we used region-based trigger values for estuarine chlorophyll and turbidity developed by DECCW as part of the MER program.

7.3 Results

Trends in Water Chemistry pH

All of the estuarine sites in the Bellinger and Kalang Rivers (except Kalang Site 6) had pH values below the pH 7 ANZECC trigger value at least once during the study period, and all estuarine sites exceeded the upper pH trigger of 8.5 during the study (Table 5) . Values for pH ranged from 5.88 in Spicketts Creek, to 9.03 at the Bellinger River estuary (BR8) (Figures 5, 8). Depth profiles in Bellinger River estuarine sites did not display consistent patterns of change in pH with depth, yet sites in the Kalang River Estuary had a consistent decrease in pH with increased depth. Similarly, there was no longitudinal trend evident for changes in pH in either river system.

Salinity

An expected increase in salinity/conductivity with distance downstream was evident in both river systems. None of the locations sampled exceeded the trigger value for salinity during the study, with freshwater riverine sites consistently below 0.1 mS/cm (Figures 5, 8). Estuarine sites that were replicated within salinity categories of 0-15 ppt, 15-30ppt and >30ppt were consistently within these ranges of salinity. A surface lens (<0.2m) of freshwater was often recorded at sites within the 15-30ppt category, and these sites also consistently displayed salinity stratification with increasing salinity with depth.

Dissolved Oxygen

All of the estuarine sites in the Bellinger and Kalang Rivers had dissolved oxygen (DO) concentrations consistently lower than freshwater sites (except for Spicketts Creek), and consistently lower that the ANZECC trigger value of 80% saturation for estuarine reaches. This is seen as a clear trend of decreasing DO saturation with distance downstream in both river systems (Figure 5, 8). There was also a consistent pattern in both estuaries for a decrease in DO saturation with depth, most pronounced in the reaches categorized as 15-30ppt salinity.

Temperature

Temperature ranged from 16.3 degrees at Spicketts Creek to 30.1 degrees at BR5 in the Bellinger 15-30 ppt salinity zone, a site with no riparian vegetation (Figure 6, 9). Temperatures were consistently lower in upper reaches and tributaries due to elevation and shading reducing temperatures, and higher in estuarine reaches. In estuarine reaches there was a consistent reduction in temperature with increasing depth, with differences between surface and epibenthic temperatures (maximum 5m) of approximately 2 degrees often recorded between October and April. There was no concomitant reduction in DO concentrations at depth to suggest persistent temperature stratification leading to hypolimnetic anoxia.

Turbidity

The trigger value for turbidity for freshwater sites was exceeded only in Spicketts creek, and only on one occasion (Figure 6, 9). In estuarine sites, the NSW MER turbidity value of 3.3NTU was not exceeded at any site. In both catchments, the tributaries sampled had relatively higher turbidity that the main stem of the river, suggesting these systems may be a source of suspended material. In the main stem of the Bellinger and Kalang Rivers, turbidity consistently increases in the 0-15ppt reaches suggesting the residence time for transported material is increased as the gradient, and therefore flow is reduced. However, the trend displayed by these data are not consistent with the direct measurement of total suspended solids, that shows a clear increase in concentration of suspended material with distance downstream, and is most pronounced in the Bellinger River (Figures 6, 9). This increase in suspended material may result from longitudinal transport, tidal exchange and resuspension, and planktonic organisms.

Chlorophyll a

Algal biomass as measured by Chlorophyll a did not exceeded the NSW MER trigger value of 2.3µg/L at any estuary site or 5µg/L at freshwater sites. There is a trend in both rivers of increasing water column concentrations of chlorophyll a with distance downstream, with estuarine sites consistently having higher concentrations. This result is expected in unregulated river systems as warmer temperatures and increased irradiance.

Nutrients

Available nitrogen was high relative to the ANZECC thresholds in a number of sites. All freshwater sites in the Bellinger catchment and Spicketts Creek in the Kalang River were above trigger values for available nitrogen (Figure 7, 10). The trigger value for available phosphorus was exceeded in Spicketts Creek. The most upstream site on the Bellinger River had extremely high values for TN and TP, and again Spicketts Creek exceeded the ANZECC trigger value for TP. Available nitrogen was high relative to the ANZECC thresholds in all of the estuarine sites except for site 7 on the Kalang River. In the Bellinger catchment, available phosphorous exceeded the trigger value at 4 of the 5 sites, whereas in the Kalang River only the 3 most downstream estuarine sites exceeded this value during the study. Only site 5 on the Bellinger River marginally exceeded the trigger value for TP. However, 3 of the 5 estuarine sites exceeded the trigger value for TN in both Rivers.

Spatial and temporal trends

The a priori determination of salinity categories based on known regimes of tidal exchange was supported by salinity concentration measured within these categories throughout the study period. However, there were no minor or major flood events during the sample period to influence the downstream gradient of tidal influence. For all water chemistry variables measured, there were no significant differences between the two replicate sites within each salinity zone in each river system. This suggests that replicating sites within salinity zone in these systems during a period of prolonged low flows does not contribute additional information to the analysis or interpretation of data.

Data for this project were collected monthly from the 22 study sites for a 12 month period. Figures 5 to 10 identify spatial patterns in data and present means and standard deviations for each site over the 12 month period. Analyses of differences between sampling periods revealed no significant difference in any water chemistry variable within defined seasons, suggesting reduced temporal sampling to a seasonal-based protocol would lose minimal resolution in detecting ecological change. However, as already stated, these data were collected during a period of reduced flow disturbance, and may more pronounced within season difference may emerge in periods of higher discharge.

BELLINGER RIVER

Figure 5. Average pH, EC (mS/cm), Turbidity (NTU) and Dissolved Oxygen (mg/L) from monthly recordings from Oct 2009 to Sept 2010.

BELLINGER RIVER

Figure 6. Average Tepmerature, Salinity (ppt), Chlorophyll a (mg/L) and TSS (mg/L) from monthly recordings from Oct 2009 to Sept 2010.

BELLINGER RIVER

Figure 7. Average nitrite-nitrate (mg/L), SRP (mg/L), TN (mg/L) and TP (mg/L) from monthly recordings from Oct 2009 to Sept 2010.

KALANG RIVER

Figure 8. Average pH, EC (mS/cm), Turbidity (NTU) and Dissolved Oxygen (mg/L) from monthly recordings from Oct 2009 to Sept 2010.

KALANG RIVER

Figure 9. Average Tepmerature, Salinity (ppt), Chlorophyll a (mg/L) and TSS (mg/L) from monthly recordings from Oct 2009 to Sept 2010.

KALANG RIVER

Figure 10. Average nitrite-nitrate (mg/L), SRP (mg/L), TN (mg/L) and TP (mg/L) from monthly recordings from Oct 2009 to Sept 2010.

Table 5. ANZECC water quality guidelines for freshwater and estuarine systems of south-east Australia. Values identified represent sites that exceeded the guideline thresholds and minimum and/or maximum value for that indicator during October 2009 to September 2010. Number in parentheses indicates number of times exceeding trigger value in 12 month period.

ANZECC Guidelines (2000) and NSW MER ‐ Min. and Max Values pH EC Turbidity Chl a N0x SRP TN TP 6.5 8 125‐ 50NTU 5µgL 40µgNL 20µgPL 500µgNL 50µgPL 2200µScm NN1 194.6 (7) RW1 6.4 8.76 174 (9) BR1 8.08 212 (6) 858 232 Sites

BR2 6.31 71.7 (4) BR3 8.43 97.4 (8) River SC1 5.88 8.01 72 72 (3) 40.2 59.6 KR1 8.85 55.5 (3)

Lowland KR2 KR3 KR4 6.33 8.37 pH EC Turbidity Chl a N0x SRP TN TP 7 8.5 no 10NTU 3.3µgL 15µgNL 5µgPL 300µgNL 30µgPL ANZECC values BR4 6.83 65.6 (8) 6.5 (3) BR5 6.64 49.8 (6) 364.9 38.8 BR6 6.27 9.03 72.7 (5) 6.5 466.9 (2) BR7 6.73 9.04 83.4 (4) 7.1 (4) 639.2 (3) BR8 6.83 9.03 30 55 (4) Sites KR5 6.32 32.4 KR6 33.1

Estuary KR7 6.35 8.67 KR8 6.84 8.93 20.9 338.6 KR9 6.78 8.91 19 6 KR10 6.66 8.95 15.9 (2) 20.8 423.3 (3) KR11 6.45 8.75 51.1 (6) 10.6 327.6

Nutrient and Sediment Loads

Discharge data supplied by the NSW DECCW from gauge 205016 (Bellinger River @ Fosters) for the study period was used to model the loading of nutrients and sediment entering the estuary. No discharge data were available for the Kalang River, so modeled data were used to estimate discharge. Historical discharge data from gauge 205013 (Kalang River @ Koroowi) for a 20 year period from 1974 to 1994 were used to model mean monthly discharge at this site. Current and modeled discharge data were used to calculate loading of total nitrogen and total phosphorus (from BR3 and KR4), as well as suspended material entering the Bellinger and Kalang Estuaries.

Although the previous section highlighted the relatively low concentrations of suspended material in the main river reaches, the calculation of loadings (discharge x concentration) clearly identifies the Bellinger River as a major source of nutrients to the estuary (Figure 11). Loadings of nutrients in November and March when river discharge was highest show over 100 tonnes/month of TN and TP passing this point in the river. Consistent with most coastal river systems, TN is considerably higher than TP on all occasions as represents the expected ratio of these nutrients for unregulated coastal systems. As an annual load, this equates to over 460 tonnes of nitrogen and 38 tonnes of phosphorus exported from the upper reaches of the Bellinger River.

Figure 11. Estimated monthly load of TN and TP entering the Bellinger Estuary.

Importantly for management of these river systems, the loadings of TN and TP from the Kalang River to the estuarine reaches are orders of magnitude smaller than those in the Bellinger driven by reduced discharge rather than lower concentrations. Using modeled data peak loadings of nutrients in November and March when river discharge was highest could not be calculated. Long-term data identify over 10 tonnes/month of TN and TP passing this point in the river (Figure 12). Consistent with most coastal river systems, TN is considerably higher than TP on all occasions as represents the expected ratio of these nutrients for unregulated coastal systems. As an annual load, this equates to over 43 and 2.7 tonnes/year of TN and TP respectively are exported from the upper reaches to the Kalang River estuary.

Figure 12. Estimated monthly load of TN and TP entering the Kalang Estuary.

Similar to the export of nutrients, the loading of suspended material is linked to higher discharge events in November and March. The suspended sediment load is clearly dominated by the Bellinger River, with peaks of 1400 tonnes/month entering the estuary, and resulting in an annual load of over 4320 tonnes past this point in the Bellinger River in a year with peak discharge not exceeding 6,000 ML/day (Figure 13). The suspended sediment load from the Kalang was again much reduced compared to the Bellinger River, with peak load of 28 tonnes/month determined from modeled data, and a total annual loading of 86 tonnes entering the estuary.

Figure 13. Estimated monthly load of suspended sediment entering the Bellinger and Kalang Estuary.

7.4 Summary of findings – Water Quality indicators

 Water chemistry was sampled from 22 sites (10 freshwater, 12 estuarine) in the Bellinger and Kalang Rivers from October 2009 to September 2010. The study was undertaken in a period with particularly low discharge, with no minor or major flood events occurring during the study.

 ANZECC trigger values for pH, dissolved oxygen, nitrogen and phosphorus, and turbidity were exceeded at some sites during the study.

 Tributaries in both catchments had higher turbidity that the main stem of each river, suggesting these systems may be aninput of suspended material. Spicketts Creek was particularly noteworthy as a freshwater site that exceeded the trigger values for nitrogen, phosphorus, DO and turbidity.

 In the main stem of the Bellinger and Kalang Rivers, turbidity consistently increases in the 0-15ppt reaches suggesting the residence time for transported material is increased as the gradient, and therefore flow is reduced. However, the direct measurement of total suspended solids shows a clear increase in concentration of suspended material with distance downstream, and is most pronounced in the Bellinger River. This increase in suspended material may result from longitudinal transport, tidal exchange and resuspension, and planktonic organisms.

 Dissolved oxygen concentrations were consistently lower than the trigger values in estuarine habitats. Temperature stratification was not evident in any site during the study, resulting in low benthic DO concentrations arising from tidal exchange indicating no persistent negative ecological impacts arising from reduced DO concentrations.

 Calculation of nutrient loads entering the estuary of each river system revealed the Bellinger River supplies a disproportionate amount of N (460 tonnes/year), P (86 tonnes/year) and suspended solids (4320 tonnes/year) compared to the Kalang River. These differences arise from the higher discharge in the Bellinger River rather than higher concentrations.

 The highest loads of N, P and suspended sediment were associated with high discharge levels, suggesting flood flows contribute substantial volumes of sediments to downstream reaches.

8. Macroinvertebrates

8.1 Background Aquatic macroinvertebrates are non-vertebrate aquatic animals (e.g., insects, crustaceans, snails and worms) that are visible to the naked eye and which live at least part of their life within a body of freshwater. Freshwater macroinvertebrates are important members of aquatic foodwebs. They feed on a wide range of food sources such as detritus (dead organic matter), bacteria, algal and plant material, and other animals. They in turn provide food for other animals such as fish and aquatic birds. Macroinvertebrates are useful as bio-indicators as many taxa are sensitive to stress and respond to changes in environmental conditions. Because many macroinvertebrates live in a river reach for an extended period of time they can integrate the impacts on the ecosystem over an extended period of time, rather than just at the time of sampling. In addition, many macroinvertebrates have widespread distributions, they are reasonably easy to collect and their taxonomy is reasonably well known.

Macroinvertebrates have been widely used in broad scale assessments of ‘river health’. The most common approach adopted for environmental monitoring has involved the analysis of the taxonomic richness of macroinvertebrates. SIGNAL stands for ‘Stream Invertebrate Grade Number – Average Level.’ It is a simple scoring system for macroinvertebrate samples from Australian rivers. A SIGNAL score gives an indication of water quality in the river from which the sample was collected. Rivers with high SIGNAL scores are likely to have low levels of salinity, turbidity and nutrients such as nitrogen and phosphorus. They are also likely to be high in dissolved oxygen. When considered together with macroinvertebrate richness (the number of types of macroinvertebrates), SIGNAL can provide indications of the types of pollution and other physical and chemical factors that are affecting the macroinvertebrate community. SIGNAL Scores range from 1 (pollution tolerant) to 10 (pollution intolerant). Another classification systems uses the EPT index. This index claims that although different insect taxa vary widely in their sensitivity to sedimentation, the taxa from the orders Ephemeroptera (E), Plecoptera (P), and Trichoptera (T) behave similarly. However, a taxonomic group can exhibit a great deal of heterogeneity, so an assessment method like the EPT may be insensitive to changes in species composition unless composition is altered along with overall taxa richness. Multimetric and multivariate approaches can increase a model’s accuracy. These models evaluate the sampled community by comparing observed conditions to what conditions or taxa are expected to occur in the absence of disturbance.

8.2 Field and laboratory methods Macroinvertebrates were sampled bi-annually (Spring 2009 and Autumn 2010) at the freshwater sites to align with the MER protocols. Kick net samples (250µm mesh) that comprise 10 linear

meters of each of pool, riffle and edge habitats will be taken from each of the 10 freshwater sites on each of the 2 sampling occasions. Only those habitats present at the time will be sampled.

Invertebrates were immediately preserved in 70% ethanol on site and transported to the laboratory for analysis. Each sample was passed through 2mm, 1mm and 250um sieves. All taxa from the 2mm and 1mm sieves were recorded, with material retained on the 250um sieve sorted for a standardized 30 minute period. Macroinvertebrates were identified to Family/genera level and assigned a SIGNAL2 score for pollution tolerance, and EPT score caclulated. Metrics of abundance, richness, diversity and composition will be taken.

8.3 Data analysis

Data for each river, sites within rivers and season were collated to produce summary data on the abundance of macroinvertebrates, number of families, number of taxa, median signal score and EPT score. Multivariate assemblage data were analysed using Primer 6 to produce ordinations to investigate relationships among rivers between invertebrate assemblages and season. Resemblance matrices were based on Bray-Curtis similarity. Data were 4th root transformed prior to analysis. Analysis of similarity in macroinvertebrate assemblages between rivers was conducted using the ANOSIM routine in Primer 6. Analysis of river x season interactions was conducted using PERMANOVA.

8.4 Results

Bellinger – Kalang Rivers

The two major rivers in the study, the Bellinger and Kalang rivers were very similar in their level of macroinvertebrate diversity and taxonomic composition. In April in the Bellinger River (composite of 3 sites; BR1, BR2, BR3), a total of 2003 individual macroinvertebrates from 22 families were collected, while in the Kalang River (composite of 4 sites; KR1, KR2, KR3, KR4), the abundance of invertebrates was lower with 826 individuals collected from 23 families.

In September, the pattern in abundance was reversed with a total of 1330 individuals collected in the Kalang River while 747 were collected from the Bellinger River. The pattern in the number of families remained similar with individuals belonging to 21 families in the Bellinger River and 22 families in the Kalang River (Table 6).

SIGNAL grades give an indication of water and habitat quality in the river from which samples were collected. Both the Bellinger and Kalang Rivers were similar with the median signal grade in the Bellinger River being 6 for both the April and September samplings, and for the Kalang River, the median grades were 5 in April and 6 in September (Table 7). However, in both rivers there was a wide range in SIGNAL scores with some taxa having grades as high as 10 while others being as low as 2.

Table 6. Abundance, number of families, number of taxa and EPT scores for individuals and families from macroinvertebrate samples collected in April and September 2010 in the Bellinger, Never Never, Rosewood and Kalang Rivers and Spickett’s Creek, NSW.

River Season Abundance Families Taxa EPT (ind) EPT (fam) No. EPT families

Bellinger April 2003 22 23 55.62 45.45

September 747 21 21 68.01 66.67 16

Never Never April 281 16 17 65.84 56.25

September 136 13 13 57.35 61.54 9

Rosewood April 528 17 17 68.37 47.06

September 109 13 13 58.72 61.54 9

Kalang April 836 23 23 44.14 56.52

September 1330 22 22 51.05 45.45 12

Spickett's April 32 8 8 59.38 62.50

September 52 10 10 57.69 60.00 5

Table 7 SIGNAL grades for study rivers based on invertebrate sampling in April and May 2010.

River Season Median SIGNAL SIGNAL score Score range Bellinger April 6 10 ‐ 2 September 6 10 ‐ 2 Never Never April 6 10 ‐ 3 September 6 8 ‐ 2 Rosewood April 6 10 ‐ 3 September 5 8 ‐ 2 Kalang April 5 10 ‐ 2 September 6 10 ‐ 2 Spicketts April 5.5 8 ‐ 3 September 5 8 ‐ 2

Analysis of the macroinvertebrate assemblage structure using the ANOSIM routine in Primer showed that the Bellinger and Kalang River have a high level of similarity in their macroinvertebrate communities (ANOSIM R value of 0.111) (Table 8). The nMDS of macroinvertebrate assemblages from rivers sampled shows that the Bellinger, Kalang, Never Never and Rosewood Rivers are relatively close to each other in ordination space indicating these rivers have greater similarity in macroinvertebrate composition, sharing many taxa in common among these rivers. Spickett’s Creek is spatially removed from all these other sites and has a significantly different macroinvertebrate community, dominated by taxa that tolerate poor habitat and water quality conditions (Hemiptera, Coleoptera, Diptera).

2D Stress: 0 River Bellinger Never Never Rosewood Rosewood Kalang Spicketts Never Never

Spicketts Bellinger

Kalang

Figure 12. nMDS ordination of macroinvertebrate assemblage in Bellinger, Kalang, Never Never and Rosewood Rivers and Spickett’s Creek based on sampling in April and September 2010.

Spickett’s Creek is characterized by having lower abundance of macroinvertebrates compared with other river systems in the study (Table 6). The macroinvertebrate assemblage is dominated by taxa with lower SIGNAL grades on both sampling occasions. ANOSIM results indicate that the largest differences in community assemblage existed among Spickett’s Creek and the Bellinger and Kalang Rivers. The ANOSIM statistic for the Bellinger River – Spickett’s Creek was R = 0.672 and for the Kalang River was R = 0.441. ANOSIM value between the Never Never River and Spickett’s Creek was much smaller R = 0.169 and for the Rosewood River and Spickett’s Creek R = 0.188 (Table 8).

Table 8. ANOSIM R statistic values and significance levels. Bold signifies significant difference.

Groups R Statistic Significance Level %

Bellinger, Never Never 0.184 4.6

Bellinger, Rosewood 0.242 3.9

Bellinger, Kalang 0.111 1.4

Bellinger, Spicketts 0.672 0.1

Never Never, Rosewood ‐0.07 68.6

Never Never, Kalang 0.102 20.8

Never Never, Spicketts 0.169 3.5

Rosewood, Kalang 0.199 8.3

Rosewood, Spicketts 0.188 5

Kalang, Spicketts 0.441 0.8

Temporal trends

Analysis of variance on the multivariate macroinvertebrate assemblage data indicated that a significant interaction existed between the factors of river and season. The nMDS of macroinvertebrate communities in rivers sampled shows that the samples from both seasons in the Bellinger, Kalang, Never Never and Rosewood Rivers are relatively close to each other in ordination space in both seasons indicating these rivers have greater similarity in macroinvertebrate composition compared with Spickett’s Creek (Figure 13), and that differences between these rivers are persistent throughout the year.

2D Stress: 0.04 Season April Spicketts Sept Rosewood

Never Never

Spicketts Bellinger Kalang

Never Never

Bellinger Rosewood Kalang

Figure 13. nMDS of macroinvertebrate assemblages in study rivers from sampling in April and September 2010.

8.5 Summary of findings – Macroinvertebrate indicators

 Macroinvertebrates were collected from 10 freshwater sites in Spring 2009 and Autumn 2010. This included five sites in the Kalang catchment (including one on Spicketts Creek as major tributary) and 5 sites in the Bellinger catchment (including one in Rosewood River and one in Never Never River as major tributaries).

 In Autumn, a total of 2003 individual macroinvertebrates from 22 families were collected from the Bellinger River, while in the Kalang River the abundance of invertebrates was lower with 826 individuals collected from 23 families. In Spring, the pattern in abundance was reversed with a total of 1330 individuals collected in the Kalang River from 22 families, with 747 individuals from 21 families collected from the Bellinger River.

 SIGNAL grades ranged from 2 to 10 in main stem reaches on the Bellinger and Kalang Rivers, with a median score of 5 to 6 for both rivers and seasons. Tributaries generally ranged from 2-8, with Spicketts Creek consistently displaying a low SIGNAL score, indicating poor water quality and habitat condition.

9. Riparian Condition

9.1 Background A riparian zone is found where any body of water directly influences, or is influenced by adjacent land (Boulton & Brock 1999).Riparian zones are dynamic environments regularly influenced by freshwater, and characterised by strong energy regimes, considerable habitat diversity, a variety of ecological processes and multidimensional gradients (Naiman et al. 2005). The riparian land is an intermediary semi-terrestrial zone with boundaries that extend outward from the waters edges to the limits of flooding and upward into the canopy of the riverside vegetation (Naiman et al. 2005).

The area within a riparian zone contains valuable water resources, highly fertile soil and supports high levels of biodiversity (Jansen et al. 2007). In regards to natural ecosystems and agricultural production, riparian land is often considered the most productive and fertile area in a landscape and hence they are considered to be a vital element of an ecosystem. Riparian zones contribute to numerous ecological functions as well as fulfill many social and economic functions, both directly and indirectly. The ecological functions of a riparian zone can be grouped into four main categories: nutrient flux, geomorphology, temperature and light, and litter input (Boulton & Brock 1999). Each of the four categories involves different attributes of the riparian zone and may encompass significantly different areas of channel bank.

9.2 Development of a Sub-Tropical Rapid Assessment of Riparian Condition

The sub-tropical rapid appraisal for riparian condition (STRARC) is a multi-metric index of riparian condition, which has been modified from the original Rapid Appraisal for Riparian Condition (RARC) (Jansen et al. 2007a) and the adapted Tropical Rapid Appraisal of Riparian Condition (TRARC) (Dixon et al. 2006). The STRARC is comprised of 24 indicators which are grouped into four sub-indices which when combined; calculate to an overall index of riparian condition. The four sub-indices help to identify the general components that contribute to the condition of a site (Dixon et al. 2006). These sub-indices and their indicators are listed below in Table 9. In summary the four sub-indices describe:

1. The overall condition of the riparian vegetation (VEGETATION CONDITION). 2. The extent of habitat found within the riparian zone (HABITAT). 3. The degree of bank stability along the channel (BANK CONDITION). 4. The amount of overall disturbance to the riparian zone (DISTURBANCES).

Table 9. STRARC sub-indices and their indicators

Sub‐indices and their indicators Assessment (each given a score of 1‐5) VEGETATION CONDITION

‐ Midstorey cover Percentage cover of vegetation 1.5‐5m tall ‐ Midstorey weeds Percentage of weeds in midstorey cover ‐ Understorey cover Percentage cover of vegetation <1.5m tall ‐ Understorey weeds Percentage of weeds in understorey cover ‐ Grass cover Percentage cover of grass ‐ Grass weeds Percentage of weeds in grass cover ‐ Organic litter Percentage cover of leaves and fallen branches <10cm in diameter ‐ Organic weeds Percentage of weeds in organic litter ‐ Vines Present native, present exotic, absent ‐ Vegetation layers Number of layers ‐ Canopy cover Percentage cover of trees >5m tall ‐ Large trees Number of large trees with >30cm trunk diameter at 1.3m from base HABITAT

‐ Organic litter Percentage cover of leaves and fallen branches <10cm in diameter ‐ Organic weeds Percentage of weeds in organic cover ‐ Standing dead trees Number of standing dead trees >30cm trunk diameter at 1.3m from base ‐ Fallen trees Number of fallen trees (i.e as a result of flooding) ‐ Large trees Number of large trees with >30cm trunk diameter at 1.3m from base ‐ Reeds Present native, present exotic, absent. ‐ Logs Abundance of logs >10cm diameter ‐ Proximity Nearest patch of native vegetation BANK CONDITION

‐ Bank slope >70 degrees, 45‐75 degrees, <45 degrees ‐ Undercutting Combined width of undercutting ‐ Slumping Combined width of slumping ‐ Exposed tree roots Extent of exposed tree roots due to erosion DISTURBANCES

‐ Tree clearing Present, absent ‐ Fencing Present, absent ‐ Livestock Evidence of livestock ‐ Proximity Nearest patch of native vegetation

Riparian condition

The percentage cover of each vegetation layer (midstorey, understorey, grass and organic litter) and the number of vegetation layers present is used as an indicator of the overall presence of riparian vegetation. This was chosen as it provides a well-rounded representation of the vegetation within the site and its distribution among different strata, as well as resilience to major flood events. The percentage of weeds within each stratum was measured as they pose threats to the ecological integrity and productivity of many Australia vegetation communities. The abundance of large trees was chosen as an indicator of riparian condition as the presence of such trees represents mature growth and undisturbed conditions. This is a particularly important indicator considering the history of logging and land clearing within the Bellinger catchment. Vines were included as an indicator of riparian condition as they can contribute to the vegetation strata. However, it was desirable that the vines were natives as exotics tend to outcompete the original vegetation.

Habitat

Riparian zones occupy only a small fraction of the landscape, but they frequently have high levels of biodiversity. Habitats within riparian zones are an important characteristic of condition as they represent the presence of food, water, shelter from predators and harsh physical conditions, and safe sites for nesting and roosting. Organic litter is an indicator of habitat as it provides shelter for smaller invertebrates, nesting materials for birds and is a source of course particulate organic matter. Standing dead trees, fallen trees and large trees provide hollows in which approximately 15% of all Australian terrestrial vertebrate fauna use as habitat at some point in time (Gibbons & Lindenmayer 2000). Fallen trees and logs provide in-stream habitat for spawning sites and areas for fish to hide from predators, and to avoid intense sunlight and high current velocities (Crook and Robertson 1999). Logs also provide habitat for biofilm and invertebrates that maintain essential links in the food web for fish (Ryder 2004).

Bank condition

Bank condition is a measure of the overall bank stability of a river. The sub-tropical rivers of the Bellinger catchment are prone to irregular flooding therefore the stream banks that have been cleared of vegetation are more susceptible to erosion (Telfer & Cohen 2010). The indicators used include undercutting, slumping and exposed tree roots. These attributes are essential in the sub- tropical regions of the Bellinger catchment which has a history of forestry and agricultural land clearing and features steep asymmetrical floodplains.

Disturbances

Vegetation clearing and the presence of livestock continue to accelerate the deterioration of riparian condition within the Bellinger catchment. The presence of fencing indicates that there has been an attempt made to exclude livestock from the site. The evidence of livestock within a

site was used as an indicator to determine whether fencing attempts had failed or if none existed then measured the extent of livestock disturbance. The vegetation surround was chosen as an indicator or disturbance as it is seen as an anthropogenic impact on riparian zones. Furthermore, the proximity of the nearest patch of native vegetation was noted in an attempt to measure the extent of tree clearing within the area in question.

9.3 Field methods

All freshwater sites in the Bellinger and Kalang catchments were samples in May and August 2010 using the STRARC method developed for this project. Five sites were sampled in the Bellinger catchment (BR1, BR2, BR3, Rosewood River, Never Never River) and five sites in the Kalang River (KR1, KR2, KR3, KR4, Spicketts Creek). Data were collected at the reach (200m) scale and at 3, 25m2 quadrats within each study reach.

Complete details of the STRARC methods are available in Southwell, E (2010) Development and application of a sub-tropical rapid assessment of riparian condition. Unpublished Honours Thesis, University of New England, Armidale NSW.

9.4 Results

Catchment scale

The Bellinger catchment had an average riparian condition score of 7.14/10 ranging from the most upstream site on the Bellinger River at Richardson’s Bridge Crossing (BR1) with a score of 7.48, to Keoghs Reserve (NN1) on the tributary of Never Never River with a score of 6.75 (Table 10).

The Kalang catchment had an average riparian condition score of 5.27/10 ranging from the most upstream site on the Kalang River at Kalang Ford (KR1) with a score of 7.50, to the site located at Sunny Corner Road (KR3) on the Kalang River with a score of 3.89 (Table 10).

The average condition score for the left bank was 7.15 and the right bank 7.14 on the Bellinger River, and 5.17 and 5.36 on the left and right banks of the Kalang River respectively (Table 10).

Table 10. Summary of individual site and river scores for riparian condition for the Bellinger and Kalang Rivers.

Site Bellinger River Score Site Average

Left Right

BR1 7.59 7.37 7.48

BR2 7.83 6.86 7.35

RW1 7.05 7.11 7.08

BR3 6.46 7.69 7.08

NN1 6.81 6.69 6.75

Average 7.15 7.14 7.14

Site Kalang River Score Site Average

Left Right

KR1 7.01 7.96 7.50

KR2 6.04 5.89 5.97

KR3 3.65 4.12 3.89

SC1 4.26 4.15 4.21

KR4 4.90 4.67 4.79

Average 5.17 5.36 5.27

Bellinger River

The Habitat sub-index scored lowest in the Bellinger catchment with an average score of 2.38/5 across the five sites. The site with the greatest habitat condition was Leans Bridge on Darkwood Road (BR2) which scored 4.88. The habitat condition at Gordonville Cutting (BR3) was the least of the Bellinger sites with a score of only 1.71 (Table 11).

The Bank Condition sub-index in the Bellinger catchment scored an average of 4.15/5. The site with the highest bank condition was BR1 with a score of 4.63, with the two tributaries of Rosewood River (RW1) and the Never Never River (NN1) both with the lowest score of 3.63 with undercutting and bank slumping evident at each site.

The Disturbance sub-index affecting sites in the Bellinger River varied from a lack of adequate fencing of the riparian zone, and distance to adjoining native vegetation.

Vegetation condition within the Bellinger River ranged from the Never Never River (NN1) with a score of 3.10/5 despite one bank dominated by exotic tree species, to site BR3 at Gordonville Cutting with a score of which recorded a score of 2.03 resulting from minimal midstorey and canopy cover, and a high weed count.

Table 11. Summary of sub-index scores for the five sites on the Bellinger River.

Site Vegetation condition Habitat Bank condition Disturbances

Left Right Avg. Left Right Avg. Left Right Avg. Left Right Avg.

BR1 2.19 2.78 2.49 1.75 2.38 2.07 5.00 4.25 4.63 3.00 4.00 3.50

BR2 2.31 2.94 2.63 2.13 2.75 4.88 5.00 3.75 4.40 3.50 3.50 3.50

RW1 3.86 3.47 3.67 3.00 2.79 2.90 3.50 3.75 3.63 3.50 3.50 3.50

BR3 2.17 1.89 2.03 2.08 1.33 1.71 4.00 5.00 4.50 2.67 4.50 3.60

NN1 2.75 3.44 3.10 2.63 2.96 2.80 3.75 3.50 3.63 3.75 2.75 3.50

River 2.78 2.38 4.15 3.47

Kalang River

The Habitat sub-index scored lowest in the Kalang catchment with an average score of 2.08/5 across the five sites. The site with the greatest habitat condition was Pearns Bridge on Kalang River (KR2) which scored 2.5. The habitat condition at (KR3) was the least of the Kalang River sites with a score of only 1.17. The most common indicators within each site lacking condition were the few logs present, the absence of reeds, little to no organic litter and the low number of hollow bearing trees (Table 12).

The Bank Condition sub-index in the Kalang catchment scored an average of 2.81/5. The site with the highest bank condition was KR4 with a score of 4.46, with the site KR3 which only recorded a score of 2.00 with slumping, undercutting and exposed tree roots evident at each site.

The Disturbance sub-index affecting sites in the Kalang River resulted in higher disturbance scores that the Bellinger River with a score of 2.8/5. In contrast Pearns Bridge on Kalang River (KR2) recorded an average score of 5.00, the maximum possible score. At the other end of the

scale, Spicketts Creek was most affected by disturbance with an average of 1.25/5, with poor bank condition and fencing of riparian zone, signs of tree clearing.

Vegetation condition within the Bellinger River ranged from the Pearns Bridge on Kalang River (KR2) with a score of 2.7/5, to site KR3 at Scotchmans with a score of which recorded a score of 2.17 resulting from a lack of groundcover.

Table 12. Summary of sub-index scores for the five sites on the Kalang River.

Site Vegetation condition Habitat Bank condition Disturbances

Left Right Avg. Left Right Avg. Left Right Avg. Left Right Avg.

KR1 2.36 2.94 2.65 2.00 2.50 2.25 4.17 4.75 4.46 4.00 3.67 3.84

KR2 3.22 2.17 2.70 2.83 2.17 2.50 2.58 3.00 2.79 5.00 5.00 5.00

KR3 2.25 2.08 2.17 2.33 1.88 2.11 1.50 2.50 2.00 2.08 2.50 2.29

SC1 2.56 2.56 2.56 1.63 1.79 1.71 2.33 2.00 2.17 0.75 1.75 1.25

KR4 2.64 2.28 2.46 1.75 1.96 1.86 2.50 2.75 2.63 2.50 0.75 1.63

River 2.51 2.08 2.81 2.80

9.5 Summary of Findings – Riparian Assessment

 An assessment of the riparian condition was undertaken from 10 freshwater sites in 2010, five sites in the Kalang catchment (including one on Spicketts Creek as major tributary) and 5 sites in the Bellinger catchment (including Rosewood and Never Never Rivers as major tributaries).  The Bellinger catchment had an average riparian condition score of 7.14/10 and ranging from 6.75 to 7.48. The Kalang catchment had an average riparian condition score of 5.27/10 ranging from 3.89 to 7.50, with the most upstream sites in each river consistently having the best condition score.  Sub-index scores revealed that the Bank Condition indicator contributed most to a positive riparian condition score in the Bellinger catchment sites. In the Kalang catchment, riparian condition scores were consistently low across all indicators.  Major disturbances to the riparian zone identified that have reduced riparian condition scores are weeds, simplified canopy structure, and minimal riparian habitat in the form of organic litter and woody debris. Poor bank condition as evidenced by undercutting and bank slumping were consistent issues in all tributaries, and may provide a link to increased suspended sediment loads recorded from these systems.

PART 3 MANAGEMENT RECOMMENDATIONS AND FUTURE MONITORING

Estuarine and coastal lagoon systems are focal points for the cumulative impacts of changed catchment land-use, and increasing urbanisation and development in coastal zones. As a result, these ecosystems have become sensitive to nutrient enrichment and pollution, and degraded through habitat destruction and changes in biodiversity. The development of a standardised means of collecting, analysing and presenting riverine, coastal and estuarine assessments of ecological condition has been identified as a key need for coastal Catchment Management Authorities and Local Councils who are required to monitor natural resource condition and water quality and quantity in these systems. This project was conducted over a 12 month period in the Bellinger and Kalang Rivers to contribute to the assessment of catchment ecological condition. The project aimed to

 to contribute scientific information for the development of a report card system for communicating the health of the estuarine and freshwater systems.

Water quality

Water chemistry was sampled from 22 sites (10 freshwater, 12 estuarine) in the Bellinger and Kalang Rivers from October 2009 to September 2010. The study was undertaken in a period with particularly low discharge, with no minor or major flood events occurring during the study. The suite of water chemistry indicators collected monthly from the 22 study sites provided a robust dataset to interpret water quality in tributaries, river and estuarine reaches.

Trigger values from the ANZECC and NSW MER guidelines were used to interpret water quality data. Trigger values for pH, dissolved oxygen, nitrogen and phosphorus were exceeded in the estuarine sites of both river systems. However, there was no direct evidence for higher level trophic implications of these breaches of trigger values. As the trigger values are generic for system types found through south-eastern Australia, it is difficult to assign relative condition based on these values. Two recommendations from this point are:

 Develop regional-scale or system specific trigger values for water quality indicators most relevant to current or predicted water quality issues.

 Develop biotic indicators for estuarine environments to compliment water quality indicators. Biota provide a temporally-integrative indicator of change as they have a longer residence time in any location that a parcel of water. A recommendation to pursue is the development of estuarine plankton as an indicator of estuarine health.

Tributaries in both catchments often had higher turbidity than the main stem of each river, suggesting these systems may be a source of suspended material. Spicketts Creek was particularly noteworthy as a freshwater site that exceeded the trigger values for nitrogen, phosphorus, DO and turbidity. One recommendation is:

 As only three tributaries were sampled in this study, a recommendation is to broaden any future monitoring to incorporate an increased number of tributaries in each catchment to help identify sub-catchment level sources of poor water quality.

In the main stem of the Bellinger and Kalang Rivers, turbidity and nutrients consistently increase in the 0-15ppt reaches suggesting the residence time for transported material is increased as the gradient, and therefore flow velocity is reduced in these reaches. One recommendation is:

 Continue to monitor reaches approximate to the limit of tidal influence for water quality as a priority as the impacts on these reaches appears more pronounced.

Calculation of nutrient loads entering the estuary of each river system revealed the Bellinger River supplies a disproportionate amount of N (460 tonnes/year), P (86 tonnes/year) and suspended solids (4320 tonnes/year) compared to the Kalang River. These differences arise from the higher discharge in the Bellinger River rather than higher concentrations. Recommendations are:

 Develop long-term water quality sample sites at locations with existing capacity to measure discharge. This will enable the calculation and communication of load-based data to managers and the public, and determination of long-term changes in water quality relative to climate factors.

 The highest loads of N, P and suspended sediment were associated with relatively higher discharge levels, suggesting flood flows can contribute substantial volumes of sediments to downstream reaches. A recommendation is to develop a flood-based monitoring program to sample flood flows of various magnitudes to develop load-based calculation for different flow events.

The design of the project to incorporate monthly sampling of freshwater and paired sites in estuaries based on salinity categories produced a robust and large dataset. Recommendations for future sample programs in this region are:

 Continue to utilize salinity categories for determination of longitudinal patterns in water chemistry, however based on the lack of significant differences for any variable between pairs within salinity category we recommend including only one site per salinity category.

 Analyses of temporal data revealed no difference in any variable within season, indicating that reduced sampling under non-flood flow conditions will be suitable for detecting trends in water quality similar to those identified in this study.

 The final recommendation for water quality monitoring is to continue to use the range of metrics used in this study, and reduce the temporal design to include seasonal sampling in combination with flood-based sampling (see macroinvertebrate sampling below), and reduce spatial distribution of sites by removing one site in each of the salinity categories.

Macroinvertebrates

Aquatic macroinvertebrates are non-vertebrate aquatic animals that are visible to the naked eye and which live at least part of their life within a body of freshwater. Because many macroinvertebrates live in a river reach for an extended period of time they can integrate the impacts on the ecosystem over an extended period of time, rather than just at the time of sampling. In addition, many macroinvertebrates have widespread distributions, they are reasonably easy to collect and their taxonomy is reasonably well known.

 Continue to collect samples for macroinvertebrate community composition and abundance in Autumn and Spring on an annual basis. In addition it is recommended to incorporate macroinvertebrate sampling into the recommended flood-based sampling protocol. These data will provide valuable evidence for resilience and recovery of the macroinvertebrate assemblages post flood disturbance.

 Consider broadening the macroinvertebrate survey to include more tributary systems (as suggested for water quality) to provide biotic indicators for the condition of sub- catchments.

Riparian condition

The riparian land is an intermediary semi-terrestrial zone with boundaries that extend outward from the waters edges to the limits of flooding and upward into the canopy of the riverside vegetation. The area within a riparian zone contains valuable water resources, highly fertile soil

and supports high levels of biodiversity as well as many social and economic functions. An assessment of the riparian condition was undertaken from 10 freshwater sites in 2010. This included five sites in the Kalang catchment (including one on Spicketts Creek as major tributary) and 5 sites in the Bellinger catchment (including one in Rosewood River and one in Never Never River as major tributaries). Recommendations from the riparian condition assessment are:

 The riparian condition method developed allowed major disturbances to the riparian zone to be identified and therefore management priorities to be determined. Priority actions for riparian zones in all reaches need to focus on weed management, increasing structural complexity of canopy structure such as native vines absent from most sites, and improving riparian habitat in the form of organic litter and woody debris.

 Tributaries were identified as reaches with consistently poor score for Bank Condition relative to main stem reaches, with undercutting, exposed roots and bank slumping evident. The riparian condition assessment also allows the spatial prioritization of sites most in need of management action, and identifies the component of the riparian zone (bank condition, habitat, vegetation) requiring attention.

 The riparian condition assessment for the Bellinger and Kalang Rivers was designed specifically for this study, with the scoring system developed from literature and anecdotal evidence. We believe this condition assessment method is appropriate for the majority of sub-tropical coastal streams, but recommend testing the protocols in other river systems.

 The condition assessment is based on a reach of river identified from a GIS as representative of that River Style. Field data are collected from a single 200m reach and applied to all reaches in that RiverStyle or subcatchment. Increasing the number of sites and linking them to spatial data on catchment characteristics (land-use, tributaries etc) would improve the ability to interpret spatial representativeness of data.

10. References

Boulton, A.J. and Brock, M.A. (1999) Australian Freshwater Ecology: processes and management. Gleneagles Publishing, Adelaide.

Davis, J.R. & Koop, K. (2006) Eutrophication in Australian river, reservoirs and estuaries – a southern hemisphere perspective on the science and its implications. Hydrobiologia 559: 3–76.

Dixon, I and Douglas, M (2006) A field guide to assessing Australia’s tropical riparian zones. Tropical Savannas CRC, Darwin.

Gibbins, P and Lindenmeyer, D (2002) Tree hollows and wildlife conservation in Australia. CSIRO Publishing Australia.

Jansen, A., Robertson, A.I., Thompson, L and Wilson, A (2004) Development and application of a method for the rapid appraisal of riparian condition. River Management Technical Guideline No. 4, land and Water Australia.

Lawson & Treloar (2002) Bellinger and Kalang Rivers Estuary Process Study, Report prepared for the Bellingen Shire Council; Report J2068/R2000; August 2002, Gordon, Australia.

Naiman, R.J., Décamps, H. and McClain, M.E. (2005) Riparia: ecology, conservation, and management of streamside communities. Elsevier Academic Press, California.

Telfer, D and Cohen, T. (2010) Bellinger and Kalang River Estuaries Erosion Study. Report to the Bellingen Shire Council.

Appendices

GPS location

Field Personnel

Time Date

Site ID

Depth (m) Temp pH Cond Sal (ppt) DO (mg/L) Turbidity PAR (mS/cm) (NTU)

Secchi Depth (m)

Water Velocity (m sec)

Chl a volume filtered

TSS volume filtered

Nutrient samples collected

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