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"November 2009".Project Number: Wetland and waterway condition assessments - M/BUS/329.MDFRC item.119 p.This Technical Report outlines the environmental values and associated watering requirements for seven wetland sites (Lake Leaghur, Lake Meran, Little Lake Meran, Lake Yando, Little Lake Boort, McDonalds Swamp and Round Lake), three waterway sites on the Campaspe River (2/11 Outfall, Cahir’s Billabong and Somerville’s Billabong) and two waterway sites on the Loddon River (Nine Mile Creek and Pennyroyal Creek) with particular reference to: 1. both historical and current environmental values 2. defined ecological objectives and associated water requirements 3. the proposed overall wetland water regime 4. the assumptions, unknowns and gaps in knowledge (to inform the adaptive management framework section of the plans). This document has been developed using the format developed for the Johnson Swamp, Lake Elizabeth and Lake Murphy Technical Report (NCCMA 2009a). The information in this report will form a key component of the Environmental Watering Plans (EWPs) being developed for the Northern Victorian Irrigation Renewal Project (NVIRP). This information was sourced from a variety of reports, from targeted field inspections and from individual knowledge and expertise (in particular Rob O’Brien, Department of Primary Industries, Kerang). The document will be used as a background paper for the Environmental Watering Plan Wetland Workshop to be held in December 2009. Therefore, please note that this report is a working document and should be considered in this context. The information should not be quoted or used for any purpose without the express permission of the North Central CMA.

"June 2009".Project Number: Ecological outcomes of managed flooding & control structures at Webster’s Lagoon - M/BUS/268 & M/BUS/293.MDFRC item.This project reports on ecological responses to the re-instatement of a wet-dry hydrological regime in Webster’s Lagoon via the construction of a regulator at the connection between Webster’s Lagoon and Toupenein Creek. Webster’s Lagoon is a large (c. 80 ha) wetland located on Lindsay Island in northwest Victoria. Construction of Lock and Weir No. 6 in 1930 and subsequent management of the river in this region changed the hydrology of Webster’s Lagoon from an ephemeral to a permanently inundated wetland with a direct connection (at its western end) to the Murray River via Toupenein Creek. Webster’s Lagoon is considered to be of high ecological value on both regional and state levels (SKM and Roberts 2003)and is a high priority site for management intervention. During July 2006, a block bank and regulator was constructed at the western end of the lagoon at the junction of Toupenein Creek and Webster’s Lagoon. Between completion of the regulator in October 2006 and June 2008, Webster’s Lagoon was disconnected from Toupenein Creek and allowed to dry completely. A managed flood was introduced in June 2008 via delivery of 252 ML of environmental water into the wetland. This initial allocation was supplemented by a surcharge filling (283 ML) in October 2008. It was anticipated that construction of a regulator (fitted with a carp screen) and the subsequent imposition of a wet-dry regime would lead to an improvement in the ecological values of the wetland and consequently the icon site. The ecological indicators reported upon here include water quality, macro- and micro- invertebrates, fish and wetland vegetation. Water quality The primary objective of this component of the project was to investigate water quality trends at Webster’s Lagoon. It was anticipated that construction of a regulator and the subsequent imposition of a wet-dry regime would lead to changes in key water quality parameters, and that these changes may have cascade effects on other components of the wetland ecosystem. Because of the low natural organic matter (NOM) loading on the base of Webster’s Lagoon at the time of this study, it is considered likely that a substantial component of the nutrient release observed originated from the wetland soil. Oxygen drawdown did not occur upon re-flooding, however a series of hypoxic periods were observed as the water temperatures decreased. Reductions in turbidity and chlorophyll a were also evident and are considered to be positive ecological outcomes. Acid sulphate soils Assessments were made on the risk of Webster’s Lagoon suffering from acidification following the reinstatement of a wet-dry regime after long-term permanent inundation. Sediments were also assessed post-watering to allow an assessment of the impact of repeated ponded floods on soil salinity. The data collected indicates that there is currently a low risk of the oxidation of any sulfidic material present leading to the liberation of sufficient acid to cause a drop in surface water pH and the subsequent acidification of the wetland. The continuation of a regular wetting/drying regime is considered likely to aid in the control of any sulfidic material present. Macro- and microinvertebrates The primary objective of this component of the project was to investigate temporal trends in the macro- and micro- invertebrate community at Webster’s Lagoon. It was anticipated that a shortterm (flood-pulse) would increase the density and diversity of macro- and micro- invertebrates A “re-setting” of the macro and micro- invertebrate community characterised by a Successional pattern similar to that expected for an ephemeral wetland was observed, providing a food source for larval and planktivorous fish, predatory macroinvertebrates and many waterbirds. Fish The aim of this component of the project was to investigate the influence of constructing a regulator(fitted with a carp screen) at the inlet to Webster’s Lagoon; imparting a drying cycle on the wetland which resulted in complete drying of the site; followed by an inundation phase whereby water was delivered initially through the screened regulator and then by pumping to surcharge the wetland above the standing water level maintained by the Lock 6 weir pool. Results have indicated a significant change in community composition within Webster’s Lagoon. The installation of a carp screen has led to a considerable reduction in the presence of carp with only 5 juveniles captured during the surveys (compared to 166 when permanently inundated). Cumbungi Pre-existing stands (established when the wetland was permanently inundated) had been reduced to desiccated stands that had collapsed upon themselves by the time the pre-flooding survey was undertaken. Consequently, it is concluded that the drying phase led to a substantial reduction in the above ground condition of the cumbungi stands at Webster’s Lagoon. However, following the managed flood, cumbungi was recorded within zones where stands had previously been recorded. Consequently, although the extent of the stands was greatly reduced, cumbungi was not eliminated from the site. It is also of note that a large proportion of the remaining dry foliage material was deliberately burnt for control purposes by Parks Victoria in the days preceding flooding. It is considered likely that the burning of the remnant stands prior to flooding may have contributed to the re-establishment of these stands. Understorey vegetation The objective of this component of the project was to investigate the potential to reinstate a flood dependent understorey vegetation community within the wetland. It was anticipated that the reinstatement of a wet- dry phase would result in an increase not only in the total number of species recorded, but also an increase in plant community diversity through reinstating Successional patterns (e.g. aquatic-dry-aquatic). Presence/absence data was compared before and after the inundation event resulting in an increase in the diversity of aquatic macrophytes, and significant changes in species composition within Webster’s Lagoon. It is of note that a number of significant (i.e. vulnerable, rare and known) plants and noxious weeds (i.e. Field dodder, Cuscuta campestris) were recorded. River red gum saplings The establishment of river red gums within the base of wetlands and creek lines has become a major management issue in recent years, and is an issue present at Webster’s Lagoon. The potential for managed floods to control river red gum saplings within the wet/dry zone via prolonged inundation was investigated. Changes in the size and visual condition of the saplings were documented before and after inundation. Results indicated that the construction of a regulator and the subsequent imposition of an extended period of inundation phase did not negatively impact the existing population of river red gum saplings within Webster’s Lagoon. Furthermore, the observation that additional germination has occurred on the wetland base following the managed flood suggests that the existing population may increase without direct management intervention.

"September 2008".Project Number: Living Murray Monitoring 2005 – 2009 - M/BUS/87-2,3.MDFRC item.142 pages. 1 of 8 reports associated with project see (Part A The Living Murray Initiative: Lindsay-Mulcra-Wallpolla Islands and Hattah Lakes Icon Sites condition monitoring program design), (Part B The Living Murray Initiative: Lindsay-Mulcra-Wallpolla Islands and Hattah Lakes Icon Sites 2006-7 condition monitoring program data), (The Living Murray Initiative: Lindsay-Mulcra-Wallpolla Islands and Hattah Lakes Icon Sites 2006-7 condition monitoring program data), (The Living Murray Condition Monitoring of Lindsay, Mulcra and Wallpolla Islands 2007/08), (The Living Murray Initiative: Lindsay-Mulcra- Wallpolla Islands Icon Site 2006-7 intervention monitoring program data), (The Living Murray Initiative: Monitoring within the Mallee CMA region 2005-06) and (The Living Murray Initiative: Monitoring within the Mallee CMA region 2005-06).No abstract available.

"August 2010".Project Number: 2008-09 Condition Monitoring at Hattah Lakes- M/BUS/87-2,3,4 BW283.MDFRC item.This report details the condition monitoring undertaken at Hattah Lakes Icon Site as part of the 2008/09 Living Murray Condition Monitoring Program. The Hattah Lakes is part of the 48,000 ha Hattah-Kulkyne National Park located in the north west of Victoria. It contains 18 freshwater lakes (12 of which are Ramsar-listed) connected by a series of floodplain channels fed by the Murray River during periods of high flow. River regulation has threatened the ecological values of floodplain areas at Hattah Lakes due to changes in the timing, duration and frequency of wet and dry phases in the lake system. Storage and extraction of water from the Murray River upstream of Hattah Lakes have resulted in the mean discharge in the Murray River near Hattah Lakes being c. 50% of natural and natural overbank flooding has occurred on only one occasion in the past eleven years. Due to the reduced frequency of flooding, pumping has become a necessary management intervention to achieve inundation of the lakes in the current regulated and drought conditions. Intermittent pumping of water into Hattah Lakes from the Murray River has occurred from April 2005 to December 2006 and in June 2009 as an emergency measure to maintain existing River Red Gum communities. Pumping is also expected to remain a long-term management intervention for the Hattah Lakes Icon Site. The Living Murray (TLM) initiative was developed in 2002 in response to evidence of the degraded condition of the Murray River system. The First Step of this program focuses on protecting and improving the ecological condition of six Icon Sites along the Murray River, including Hattah Lakes. The program aims to return the Murray River system to a healthy working river through the accrual and release of an average of 500 GL.y-1 of recovered water and the implementation of a capital works and measures program. The Outcomes Evaluation Framework (OEF) stipulates that measurable management targets be created to unambiguously assess whether a pre-determined level of ecological condition has been achieved. At the time of writing, such targets had not been developed for Hattah Lakes. Therefore, in the absence of defined targets, this report focuses upon the ecological objectives specified in the First Step decision, the Outcomes Evaluation Framework and the Hattah Lakes Icon Site Environmental Management Plan. Where possible, results are compared with those of previous years to determine any directional change in ecological condition. The ecological components monitored at Hattah Lakes in 2008/09 include River Red Gum, Black Box, wetland vegetation, floodplain vegetation, Lignum, Cumbungi and fish. River Red Gum (RRG) at Hattah Lakes is distributed within three previously defined vegetation classes (WRCs) including Red Gum Forest (RGF: 341 ha), Fringing Red Gum Woodland (FRGW-2739 ha) and Red Gum with Flood Tolerant Understorey (RGFTU: 1,533 ha). Achievement of the ecological objectives for RRG at Hattah Lakes requires the maintenance of sustainable RRG populations. Progress towards achievement of this objective was assessed by examining RRG distribution, condition, age-structure and relative abundance across the the three vegetation classes. Low Foliage Vigour (generally less than 30%) scores were common to RRG in all WRCs indicating that condition of RRG within all three communities at Hattah Lakes is generally poor. Analysis of Foliage Vigour data collected in 2007/08 and 2008/09 indicated that an increase in tree condition occurred at 24 of the 27 sites. However, the between year changes in Foliage Vigour detected in the analyses were not supported by photo records and may be attributed to the subjective nature of tree condition assessments. The size-class distributions associated with sampling transects were compared to those considered ideal for population maintenance and sustainability (i.e. those approximating an ‘inverse j-curve' shape or log-normal function). Distributions of RRG in all three WRCs approximate smooth inverse j-curve shapes indicating robust recruitment. Each WRC is well represented within the smallest size class (DBH = 0-15cm) where the proportion of trees was 63.8%, 49.1% and 58.5% in RGF, FRGW and RGFTU respectively. Black Box (BB) at Hattah Lakes is distributed within the two previously defined vegetation classes (WRCs) Riverine Chenopod Woodland (RCW: 6,073 ha) and Black Box Swampy Woodland (BBSW: 339 ha). Achievement of the ecological objectives for BB at Hattah Lakes involves the maintenance of sustainable BB populations. Progress towards achievement of these objectives was assessed by examining BB distribution, condition, age-structure and relative abundance across the two vegetation classes. Analysis of Foliage Vigour data collected in 2007/08 and 2008/09 indicated that an increase in tree condition occurred at all 18 sites. However, mean Foliage Vigour scores were low (generally less than 30%) in both 2007/08 and 2008/09. Low Foliage Vigour scores were common to RCW and BBSW indicating the condition within both BB communities at Hattah Lakes is generally poor. The survival of BB indicates the resilience of this species under stressful conditons, since the Hattah Lakes system has not been flooded for more than ten years. Examination of photo point images taken at each of the sites at the time of each survey indicates that any change in Foliage Vigour between years was minimal. The size class distributions associated with sampling transects were compared to those considered ideal for population maintenance and sustainability (i.e. those approximating an ‘inverse j-curve' or log-normal function). Distributions with both WRCs approximate smooth inverse j-curves, indicative of robust recruitment. However, representation in the smallest size class (DBH = 0-15cm) was slightly higher in RCW (51.0%) than it was in BBSW (40.3%) indicating marginally higher recruitment rates in the less frequently flooded BB communities. However, the monitoring has occurred over a relatively short time frame and consisted of only two samplings and long term trends in recruitment and condition change are yet to be ascertained. Wetland vegetation was surveyed at nine wetlands at Hattah Lakes, all of which were dry during the 2008/09 survey. A total of 89 plant species (76 native) were recorded during this survey, six of which are listed as rare or threatened in Victoria by the Department of Sustainability and Environment. Recorded plant species were classified into functional groups and differences in community composition and abundance were analysed both for functional groups and individual species. There is a clear separation of wetlands at Hattah Lakes into three groups: (i) large, relatively deep wetlands that received environmental water in 2005/06; (ii) small, relatively shallow wetlands that received environmental water in 2005/06; and (iii) wetlands that remained dry during the 2005/06 pumping events. Species and functional groups both showed significant differences in community composition and abundance between 2007/08 and 2008/09. Terrestrial damp and amphibious species appeared at lower elevations, decreased in abundance or disappeared from the deep lakes such as Bulla and Hattah in 2008/09; terrestrial damp species also decreased in abundance or disappeared from Lakes Yerang and Little Hattah (shallow lakes that received water in 2005/06); Lakes Nip Nip and Boich, which have remained dry, were dominated by terrestrial dry species in both 2007/08 and 2008/09. Floodplain vegetation was surveyed at six sites, each containing ‘often', ‘sometimes' and ‘rarely' flooded ‘sub-sites' determined from historical flood-return frequency data. A total of 65 plant species (62 native) were recorded in 2008/09, six of which are listed as rare or threatened in Victoria by the Department of Sustainability and Environment. Sites fell into four groups based on vegetation type at the various flood-return frequencies: (i) site 1,‘often' and ‘sometimes' dominated by RRG Woodland with a sparse understorey; (ii) sites 2 and 3, ‘often' and ‘sometimes' dominated by RRG Woodland with a high cover of leaf litter in the understorey; (iii) sites 5 and 6, mixed RRG and BB Woodland at ‘sometimes'; and ( iv) site 4, mixed RRG, BB and River Cooba Woodland at ‘sometimes' and a sandhill at the ‘rarely' ‘sub-site'. The majority of floodplain sites have not been flooded for more than 12 years. In 2008/09, more than 90% of the species recorded in all six sites were terrestrial and only two species, recorded at very low abundance, were classified as amphibious. The absence of flooding and water in the wetlands and on the floodplain at Hattah Lakes is preventing the ecological objectives relating to sustainable wetland and floodplain vegetation from being met. The ecological objective relating to Lignum at Hattah Lakes is restoration of the macrophyte zone around at least 50% of the lakes. Lignum condition was monitored at five sites in 2006/07, 2007/08 and 2008/09 using the Lignum Condition Index (LCI) scores for Viability and Colour. Assessments of the change in Viability and Colour of Lignum across the various flood regimes indicated a decline in condition of Lignum between 2006/07 and 2007/08 and between 2007/08 and 2008/09 at all sites except one, where there was a slight increase in the mean Viability score from 2007/08 to 2008/09. The Viability and Colour scores indicate that the ‘often' flooded populations are in better condition than the ‘sometimes' flooded populations followed by the ‘rarely' flooded populations, demonstrating the significance of flooding for the survival of Lignum. Reduced frequency of flooding is a threat to the achievement of the ecological objective of a healthy and sustainable Lignum community at Hattah Lakes. Cumbungi (Typha spp.) was

"June 2009".Project Number: Literature review and experimental design to address retaining floodwater on floodplains and flow enhancement hypotheses relevant to native tree species - M/BUS/313.MDFRC item.The following hypotheses, relating to native trees, arose directly from the IMAF development process: 1. 'Suitable habitat for native tree species will be created or maintained through retaining floodwater on floodplains.' 2. 'The health and growth of native tree species will increase through retaining floodwater on floodplains.' 3. 'Native tree species will germinate and recruit through retaining floodwater on floodplains.' 4. 'Suitable habitat for native tree species will be created or maintained through flow enhancement.' 5. 'The health and growth of native tree species will increase through flow enhancement.' 6. 'Native tree species will germinate and recruit through flow enhancement.' 7. 'Suitable habitat for weed vegetation will be created or maintained through retaining floodwater on floodplains.' Information on the validity of these hypotheses is required for improved decision-making, investment and monitoring of TLM sites, and for Basin-wide management.

"March 2011".Project Number: 2009-10 Condition Monitoring at Lindsay-Mulcra-Wallpolla Islands - M/BUS/87-2,3,4 BW283.MDFRC item.This report details the condition monitoring undertaken at Lindsay, Mulcra and Wallpolla (LMW) Islands as part of the 2009/10 Living Murray Condition Monitoring Program. Icon Site condition monitoring has been developed to: Determine the change in environmental condition of individual assets resulting from water application and the implementation of works programs under The Living Murray (TLM). Assess whether sustainable native fish, bird and vegetation communities are being maintained across the Icon Sites. The Outcomes Evaluation Framework stipulates that measurable targets be created to unambiguously assess whether a pre-determined level of condition has been achieved. At the time of writing, such targets had not been developed for LMW. In the absence of defined targets, this report focuses upon Icon Site specific objectives. Icon Site specific objectives presented in the Outcomes Evaluation Framework have been further refined as part of the Lindsay-Mulcra-Wallpolla Environmental Management Plan. Together these objectives form the basis for condition monitoring at Lindsay-Mulcra-Wallpolla of which there are six vegetation components and one fish component. River Red Gum The ecological objectives for River Red Gum (RRG) at Lindsay, Mulcra and Wallpolla are: Current area maintained. Maintain current condition and extent of River Red Gum communities to sustain species assemblages and processes typical of such woodland. Large scale mapping at regular intervals is required to quantify changes in the distribution and areal extent of River Red Gum at LMW. Currently there is no such mapping program underway, so it is not possible to know if current area of RRG is being maintained. Significant increases in Crown Condition scores between the sampling events of 2008/09 and 2009/10 suggest changes in the conditions favourable for tree growth on the LMW floodplain. This is attributed to environmental watering at Mulcra Horseshoe Lagoon and a break in drought conditions. However, with the notable exception of the relatively small area of extant Red Gum with Flood Tolerant Understorey (RGFTU) at Mulcra Island, the recent improvement observed for RRG trees at LMW represents a change in the previous downward trend in condition rather than a return to acceptable condition. Stand condition modelling conducted by Cunningham et al.(2009) reports that the extent of severely degraded stands was higher in the Mallee (Hattah, Chowilla and LMW) than at other TLM Icon Sites, that the majority of stands were in a stressed condition in 2003 and that this had increased by 4% by 2009. Recruitment must keep pace with mortality for a population to remain sustainable and this must occur within the current spatial context if the present distribution is to be maintained (i.e. ecological objectives are to be met). Size-class frequency distributions for Fringing Red Gum Woodland (FRGW) indicate a relative abundance of trees within the smaller size classes suggesting sustainable recruitment. However, despite indications of recent improvement in the condition of trees on average, population viability assessments suggest there are long-term sustainability concerns for Red Gum Forest (RGF) communities at LMW. Black Box The ecological objectives for Black Box (BB) at LMW are: At least 20% of the original area of Black Box vegetation maintained. Improve condition to sustain species assemblages and processes typical of Black Box woodland. Ecological Vegetataion Class (EVC) mapping conducted in 2005 provides the most accurate and up to date information about the areal extent of Black Box at LMW and is therefore the logical choice for a BB areal standard. However, in the absence of an ongoing program mapping the distribution of Black Box at the Icon Site scale, it is not possible to know what proportion of the original area of Black Box is being maintained. Size-class distributions for Black Box communities do not approximate inverse J-shaped curves indicative of sustainable populations. Further, between 2008/09 and 2009/10 there was a reduction in the relative proportion of Diameter at Breast Hight (DBH) 16 ds/m, DPI 2008) and an increase in abundance could be indicative of an increase in site salinity. It is recommended that soil salinity testing be undertaken at the LMW Icon Site. Of concern are the appearances and/or incr

"July 2009".Project Number: Establish Monitoring Program for Darling Anabranch Contract MD187.80 - M/BUS/267.MDFRC item.95 pages.The Great Anabranch of the Darling River (the Darling Anabranch) is an ancestral path of the Darling River, which extends c.450km south from its off take on the Darling River (c. 50km south of Menindee, NSW). The Darling Anabranch is a naturally ephemeral stream which under non-regulated conditions would only receive inflows when flows in the Darling River reach 10,000ML/day. In the intervening period between construction of the Menindee Lakes storage scheme (1960) and 2002, the Darling Anabranch received an annual replenishment flow of up to 50,000ML/year to supply the stock and domestic requirements of adjacent landholders. Of this, only ~3,000 ML was extracted for consumptive purposes. The Darling Anabranch Pipeline was completed in February 2007. One of the overarching objectives of the Darling Anabranch Project was to create a more natural wetting drying cycle. The expectation was that water saved through the construction and operation of the pipeline, could be utilised to generate an environmental flow of c. 60,000ML at a maximum rate of c. 2,000ML/day every 2 to 3 years on average (when water is available in Lake Cawndilla) that would result in an end-of-system flow (Wallace et al. 2007). However, it is considered that flows of this magnitude are not achievable due to constraints associated with the outlet regulator at Lake Cawndilla (maximum release ~1,800 ML/day). Flows into the Darling Anabranch are also possible from the Darling River during periods of moderate to high flow (>10,000ML/day). The ability to deliver environmental flows into the Darling Anabranch (and the delivery route) is dependant on the future management and availability of water in both the Darling River and the Menindee Lakes system.

"April 2009".Project Number: Implications of pumping water on the ecology of Hattah Lakes - M/BUS/210.MDFRC item.1 of 2 reports associated with project see (Implications of pumping and ponding water on water quality and the development of diverse aquatic ecosystems: Intervention Monitoring of the Hattah Lakes Icon Site 2006/07).This report details the intervention monitoring undertaken at Hattah Lakes by the Murray-Darling Freshwater Research Centre in 2007/08 as part of The Living Murray program. The project investigated the ecological responses of river red gum, water quality, wetland vegetation and fish to the pumping of water to Hattah Lakes. The Hattah Lakes is part of the 48,000 ha Hattah-Kulkyne National Park located in the north west of Victoria. It contains 18 freshwater lakes (12 of which are Ramsar-listed) connected by a series of floodplain channels fed by the Murray River during periods of high flow. River regulation has threatened the ecological values of Hattah Lakes due to changes in the timing, duration and frequency of wet and dry phases in the lake system. Storage and extraction of water from the Murray River upstream of Hattah Lakes has resulted in the mean discharge in the Murray River near Hattah Lakes being ≈ 50% of natural. Natural overbank flooding has occurred on only one occasion in the past 11 years. Due to the reduced frequency of flooding, pumping has become a necessary management intervention to achieve inundation of the lakes in the current regulated and drought conditions. The pumping of water into Hattah Lakes from the Murray River occurred on four occasions during the period April 2005 to December 2006. It is expected to remain a long-term management intervention to maintain ecological values at the Hattah Lakes Icon Site. River red gum The greatest increase in river red gum (RRG) crown density (and condition) occurred in the ≈ 6-month period following pumping at Lake Mournpall (treatment), Brockie (treatment) and Yelwell (experimental control that did not receive pumped water). At least part of the increase across all lakes was attributed to the well-above-average rainfall during this period. For the ≈ 6-12 month and ≈ 12-18 month periods following pumping, mean crown densities of RRG have generally been maintained or have decreased at all three lakes. This was not expected, as the environmental watering was predicted to generate increases in crown densities at Lakes Mournpall and Lake Brockie for a longer period. Statistical analysis of the crown density profiles showed significant differences between the lakes that received pumped water and the control lake. These differences were due to a significantly lesser decline in crown density at Lakes Mournpall and Brockie during the ≈ 12-18 month period than occurred at the control Lake Yelwell. The lower rate of decrease in crown density at the treatment lakes may be due to these lakes receiving pumped water. However, it may in part be attributed to the control Lake Yelwell having a RRG population in poorer condition than the treatment lakes at the commencement of the study. Analysis of RRG response with distance from the water edge revealed that the greatest increases in crown density occurred for RRG located upon the lakebeds of the treatment lakes in the 12-month period following inundation. The bases of these trees were directly inundated from the pumped water. In contrast, the RRG located at higher elevations that were not directly inundated responded to a lesser degree. The findings suggest that RRG fringing the lakebeds may require direct inundation to achieve a greater increase in crown condition from environmental watering events. Water quality Water levels at Lakes Mournpall, Hattah, Bulla and Arawak decreased over the study period and held maximum water depths of ≈ 0.3 – 0.5m in mid-September 2008. As water levels decreased, turbidity increased and became more variable due to the increased susceptibility of the lakebed sediments to re-suspension from wind and wave action. This influenced euphotic depth in the lakes which typically ranged from 0.2 – 0.8m across the lakes. Electrical conductivity increased within the lakes as dissolved salts become more concentrated through evaporation but were less than 1,500 μS.cm-1 at the end of the study period. Surface water temperatures remained within the range of 10 – 30oC. Phytoplankton blooms comprising blue-green algae species were present at all four lakes during the study period. Total chlorophyll pigment exceeded 250 μg.L-1 and blue green algae counts exceeded 1 million cells.mL-1 at all lakes for at least one sampling occasion. The blue-green algae communities of each lake remained distinct to one another over the study period with communities changing in a cyclic manner most likely due to seasonal influences. A total of 20 blue-green algae taxa were identified within Hattah Lakes, with four potentially toxic species sampled including (in decreasing abundance) Microcystis aeruginosa, Anabaena spiroides f. spiroides, Cylindrospermopsis raciborskii and Anabaena circinalis. The water quality variables of pH and dissolved oxygen were variable and influenced by the photosynthesis within the water column. Day-time dissolved oxygen concentrations were typically supersaturated (>100% saturation) and pH was elevated (peak of 10.29) when phytoplankton and submerged macrophyte biomass was high. Wetland vegetation The lakebed vegetation communities of Lakes Brockie (treatment that received pumped water) and Lake Boich (control that did not receive pumped water) were monitored over a ≈ 21 month period to determine the effects of pumping upon lakebed vegetation communities. A total of 91 plant species were recorded at Lakes Brockie and Boich during the sampling period; of these 69 were indigenous (76%) and 22 were exotic (24%). These plant species were from ≈ 21 families, with Chenopodiaceae and Asteraceae containing considerably greater numbers of taxa than the other families. Before intervention, 31 plant species were recorded at Lake Brockie and 13 plant species were recorded at Lake Boich. After intervention, the number of plant species recorded at Lakes Brockie and Boich across all four sampling times was 53 and 58, respectively. Statistically significant differences in vegetation community between the two lakes at the High and Medium elevations were measured. However, no statistically significant difference was observed between the lakes over time. This contrasts with the analysis of only the Before and After 1 survey as reported in EPA and MDFRC (2008) and is due to the influence of the three additional After surveys in the 2007/08 analysis. Whilst statistically significant results were not recorded between lakes as a result of Lake Brockie receiving pumped water, there have been notable changes in the vegetation communities at Lakes Brockie and Boich. This is particularly evident when considering the plant functional groups at the lakes. The lakebed vegetation community at Lake Brockie changed from being predominantly terrestrial before inundation to one dominated by flood-responsive species, returning to a predominantly terrestrial lakebed community ≈ 19 months after pumping. A total of 15 flood-tolerant and one aquatic/semi-aquatic species were recorded at this lake following pumping. In contrast, the vegetation community at Lake Boich consisted of predominantly terrestrial species at four or the five sampling times. A total of two flood-responsive species were sampled at this control lake following pumping. Fish The series of pumping interventions at Hattah Lakes has resulted in the development of a significant fish community within the lakes contrary to initial expectations. However, the mismatch between the fish communities of the lakes (e.g. very low abundances of common carp, bony bream and absence of eastern gambusia) and the Murray River indicates that pumping has acted as a screen upon the fish community. In March 2008, a total of 8,248 fish representing four native (golden perch, carp gudgeon, flathead gudgeon and Australian smelt) and two non-native (goldfish and common carp) species were sampled from the four lakes. In June 2008, a total of 2,994 fish representing three native (carp gudgeon, flathead gudgeon, Australian smelt) and one non-native (goldfish) species were sampled from these same lakes using the standard fyke netting technique. The additional use of two gill nets in June 2008 at Lakes Mournpall and Hattah also sampled common carp (n = 17), golden perch (n = 9) and silver perch (n = 1). Native fish comprised 98.8% and 99.9% of the sampled fish in March 2008 and June 2008, respectively. Three small-bodied native fish consisting of carp gudgeon, Australian smelt and flathead gudgeon together comprised over 98% of the total catch for each time. The results of this study were compared with those from five earlier surveys following the commencement of pumping at Hattah Lakes. Whilst relative fish abundance has consistently increased between the first five surveys, the two surveys of 2008 demonstrate a decrease in both abundance and diversity of fish within the Hattah Lakes. This decrease is attributed to the reduction in aquatic habitat as the lakes become shallow and increased vulnerability of the fish community to predation by birds. Fish currently remaining in the lakes will perish by February 2009 if the lakes dry completely as expected. This will mark the third consecutive occasion since 1996 that fish communities have developed within Hattah Lakes but have not had an opportunity to move back to the Murray River and contribute to fish populations more broadly. The near-annual reconnection of Hattah Lakes with the Murray River under natural flow scenarios highlights the changed role of Hattah Lakes for fish due to river regulation and extraction. Management recommendations Based on the results of this project, the autho

"June 2010".Project Number: Post-watering vegetation condition assessment for Lake Yando - M/BUS/347.MDFRC item.This document reports on the results of a vegetation survey which was carried out at Lake Yando in March 2010. Lake Yando is an 83 Ha wetland, located approximately nine kilometres north-east of Boort, Victoria. The wetland filled historically from Venables Creek and in years of larger floods, would have received water from Kinypanial Creek via Lake Boort, as well as Lake Lyndger (NCCMA 2010). Development of irrigation infrastructure in the region led to changes in the wetland flooding regime with connection to the irrigation system causing Lake Yando to become flooded with irrigation outfall water for prolonged periods of time (NCCMA 2010). This increased water permanence contributed to substantial changes in vegetation structure and composition at Lake Yando, including the death of established River Red Gum (Eucalyptus camaldulensis) trees across the wetland base and an increase in the extent of Cumbungi (Typha spp.) stands (NCCMA 2010). Modifications to the water delivery system around 1999 have allowed Lake Yando to dry completely in recent years. Management of the site is currently focused on the reinstatement of a more natural flooding regime, including alternating wet and dry phases. This is designed to support the environmental values of the wetland. A specific environmental watering plan (EWP) is being developed for Lake Yando, as well as a number of other wetland and waterway sites, as part of the Northern Victorian Irrigation Renewal Project (NVIRP). As part of the EWP development process, the vegetation at Lake Yando was surveyed by The Murray-Darling Freshwater Research Centre (MDFRC) staff in October 2009. This survey was conducted to obtain baseline data on vegetation composition, condition and distribution that could be used to identify vegetation water requirements and set watering targets. To maintain and/or improve the integrity of the vegetation community at Lake Yando the recommended goal proposed by NCCMA (2010) was: ‘To provide a watering regime typical of a deep freshwater marsh that supports the maintenance and recruitment of River Red Gum and promotes the growth of a diverse range of aquatic and amphibious plant species offering a variety of habitats to waterbirds, reptiles and amphibians.’ In October 2009 water was delivered to Lake Yando to meet a number of ecological objectives, including those specific to vegetation, as summarised in the goal statement above. The survey reported on here was used to assess how the recent watering event has affected the vegetation community at Lake Yando and to determine whether progress is being made toward achieving the objectives proposed by NCCMA (2010).

"June 2011".Project Number: Part 3 - Natural versus Artificial watering of floodplains and wetlands - M/BUS/248.MDFRC item.1 of 4 reports associated with project see (Ecosystem Services and Productive Base for the Basin Plan), (Clarification of Definitions in the Water Act 2007) and (Feasibility Assessment of Ecological Outcomes (indicators) proposed for the Basin Plan Monitoring and Evaluation Program).At a global scale, society's desire to control water for a range of purposes (e.g. irrigation, industry, stock and domestic supply, flood mitigation) has led to the regulation of a significant proportion of the world's rivers. Alteration of flow regimes is regarded as the most serious and continuing threat to ecological sustainability of rivers and their associated floodplain wetlands. Long-term drying has severely altered the ecology of many freshwater ecosystems, causing unprecedented, long-term or potentially irreversible damage (i.e. species extinctions). It is considered that much of the natural capacity (both resistance and resilience) of aquatic ecosystems to cope with drought has been lost. Re-establishment of natural flow regimes represents a neat theoretical objective. However, the reality is that this is impractical as the demands of society preclude returning our rivers to natural flow. The existing impacts of regulation combined with future impacts of climate change imply that in many river systems, overbank flows may no longer occur frequently enough to maintain ecological processes, and many wetlands and floodplains will become increasingly reliant on targeted environmental water allocations (EWA). New approaches to management will be essential in order to maintain a larger active floodplain than possible under the current water sharing arrangements. However, in order for managers to be successful in achieving the stated ecological objectives of river restoration and ecological management programs, it is necessary to have an appreciation of the role of flow in natural systems and the limitations of methods of delivering EWA. Within this synthesis we: 1. Briefly summarise the role of flow in unregulated floodplain ecosystems; 2. Define key state variables that characterise the flow regime of a floodplain system; 3. Discuss the major types of EWA currently in use; 4. Summarise key ecological processes and the impact of method of EWA delivery; 5. Outline the prevailing management paradigm; and 6. Identify management considerations for progress towards sustainable river systems. Flow is regarded as the key driver regulating processes and diversity in river systems and can be regarded as the master variable. The processes which are influenced by flow and floodplain inundation include hydrodynamics, biogeochemistry and primary productivity. Higher order organisms respond to these habitat and primary productivity drivers. It is not just the presence of water that is important for maintenance of ecosystem function; the provision of water is a critical link in the ecology of wetland and floodplain systems but that does not automatically imply that the link is functional. Flow magnitude, frequency, timing, duration, variability, rate of change and sequence all hold major ecological significance. It is important to note that the quality of water (i.e. chemical and thermal properties) is equally as important as the quantity of water or the temporal patterns of flow. In this context, the method of maintaining inundation (i.e. ponded flood versus flowing flood) and the resultant dilution and downstream dispersal of carbon and nutrients will have a significant impact on water quality via biogeochemically mediated processes. In unmodified catchments natural flooding regimes that are completely unaltered represent the reference condition. However, due to the extent of regulation and development throughout the MDB, there are very few sub-catchments that experience an unimpeded, natural flood. In modified catchments the closest approximation is an uncontrolled flow where the effects of storages and in-stream structures have largely been nullified. River management has skewed river channels and floodplains in opposite directions; towards an anti-drought an engineered drought scenario respectively. Regulated river systems are therefore likely to be in an extreme state of precariousness. Management needs to focus on reinstating resilience as the most pragmatic and effective way of managing ecosystems in order to withstand future droughts and provide ecosystem services. The concept of downsizing rivers has some merit but in reality it is a process of reinstating the small floods that river regulation has removed. It also overlooks the role of the interface between the aquatic (regularly inundated) and terrestrial (never inundated) zones in subsidising terrestrial food webs. Abandonment of large sections of floodplain may create an extremely dysfunctional and potential hostile zone or 'no-man's land' that is neither aquatic or terrestrial, generating a new barrier to energy flux. Enacted as an emergency measure, pumping water to targeted wetlands pumping water into individual sites has been highly successful in achieving a limited set of objectives. There is an emerging risk that construction and operation of new, large infrastructure specifically designed, constructed and operated for environmental outcomes is seen as an alternative to unregulated overbank floods to maintain ecosystems. It is essential to recognise that there there are a number of critical limitations associated with this approach; primarily related to spatial, connectivity and water quality issues. The expectation that fragmented sites will function as refuges that serve as the major sources of propagules and colonists for other areas and lead to improvement of the Murray-Darling Basin is unproven. Furthermore, it is critical to recognise that using a regulator to inundate large floodplains under low flow conditions has not been used as a restoration technique anywhere in the world. Consequently there is no precedence for this management activity and actual responses may differ from those expected. Releases of large volumes of water from storages may lead to the provision of flow-associated cues and conditions otherwise absent during base flows. However, water released from an upstream storage and transferred as an EWA into an individual site during periods of in-channel flow may restrict the ecological outcomes as the productivity gains from upstream flooding are not available to be transported into the managed site. The "missing pieces" are likely to include plant and invertebrate propagules dispersed from upstream sites, increased carbon and nutrient concentrations and other chemical cues resulting from inundation of floodplain soils and plant material, eggs and larvae of fish and other organisms spawned at upstream sites. We propose that there is a hierarchical time scale relationship between inundation events and ecological responses that is associated with all inundations. This relationship can be described as follows; Instantaneous (occur within minutes-hours of inundation), Fast (occur within hours-weeks of inundation), Slow (occur weeks-months after inundation), Delayed (processes that occur within months-years after inundation), and Cumulative (responses that may only occur/be realised after a series of events). We consider that the influence of any EWA delivery method will be related to the rate at which different processes occur. For example, chemically mediated processes occur very quickly (instantaneous) and are therefore unlikely to be affected by the method of delivery of EWA. In contrast, many biogeochemically mediated and biotic processes occur over longer time scales and are more likely to be influenced by the method of EWA delivery. This will be driven by the lag phase in ecological response providing opportunities for differences in responses/processes between natural and managed floods to cascade across multiple levels and manifest into large differences in the quality of outcomes. Methods of delivering environmental water that do not maximise (i) connectivity (i) the provision of appropriate habitat; and (ii) the development of appropriate food resources will deliver minimal benefits and compromise the ability of the EWA to achieve positive ecological outcomes. It must be recognised that the use of EWA's is fundamentally a large-scale manipulative experiment. We currently lack sufficient ecological knowledge to predict how floodplains in different conditions will respond. This represents a major hurdle for managers as volumes of environmental water are limited and resilience is an ecosystem property that can be either created or destroyed. Investment in recovering water and construction of infrastructure for delivery of EWA's needs to be underpinned by investment in research to inform adaptive management to ensure that critical ecological processes and functions are reinstated. If this is not undertaken, there is no way that EWA's will be able to reinstate resilience. The most appropriate method for delivery of an EWA to any site will vary accordingly with a range of factors including but not limited to; availability of water, connectivity of site to water source, and management targets. Environmental water allocations cannot replace the function of natural overbank flows and there is no ‘Silver Bullet' for repairing water-dependant ecosystems deprived of a natural flooding regime. Consequently pragmatic solutions are required to ensure environmental watering at intervals sufficient to enable system preservation and recovery. Reinstating flows and reoperation of existing infrastructure should be actively used during wet and median conditions to build resilience at the system scale. Delivery of EWA to isolated sites should be relegated to use during dry and extreme dry conditions to avoid long-t

The Murray–Darling Basin (MDB) Environmental Water Knowledge and Research (EWKR) project is a five year (2014 - 2019), $10 million project being undertaken by the Centre for Freshwater Ecosystems (formerly Murray–Darling Freshwater Research Centre) in collaboration with scientists from other research organisations to improve the science available to support environmental water management, and thereby contribute to achieving Basin Plan objectives. The MDB EWKR team collaborated with water managers, environmental asset managers, water planners and relevant community groups to identify research priorities and undertake research targeted at addressing those priorities. The client for the project is the Department of the Environment and Energy (DoEE), Commonwealth Environmental Water Office (CEWO). The purpose of this Mid-year Progress Report is to document project progress as required by 5.3 of Schedule 2 of the Funding Agreement for the period 1 July 2018 to 31 December 2018.

Eucalyptus (Myrtaceae) trees are ubiquitous in riparian-floodplain zones of Australia's south-eastern river catchments, where natural ecosystems continue to be affected. In the Murray-Darling Basin (MDB), provision of environmental flows to mitigate tree decline is informed by past field studies. However, broadscale empirical field data on tree nutrition and response to external changes remain scarce. This is the first study to gather soil and plant data across a large area of catchment lowlands to generate a low-resolution regional snapshot of tree nutrition and soil chemistry. Leaves and soils were sampled across and adjacent to the MDB; from and beneath mature trees of three key riverine eucalypts, Eucalyptus largiflorens, E. camaldulensis, and E. coolabah. Foliar sodium concentrations ranged from ���500 mg kg-1 for E. coolabah up to ���4500 mg kg-1 for E. largiflorens, with highest values at the River Murray sites. The results suggest E. largiflorens is highly salt tolerant by foliage accumulation given all trees sampled were in good condition. Further research into these species is needed to determine toxicity thresholds for elements such as sodium to aid early diagnosis of potential tree stress, which could provide an additional line of evidence for when environmental water is required to mitigate decline.

Final report prepared for the Commonwealth Environmental Water Office by La Trobe University.

Final report prepared for the Commonwealth Environmental Water Office by La Trobe University.

Background: Calorie restriction (CR) retards aging and increases longevity in many animal models. However, it is unclear whether CR can be implemented in humans without adverse effects on body composition.Objective: We evaluated the effect of a 2-y CR regimen on body composition including the influence of sex and body mass index (BMI; in kg/m2) among participants enrolled in CALERIE-2 (Comprehensive Assessment of Long-term Effects of Reducing Intake of Energy), a multicenter, randomized controlled trial.Design: Participants were 218 nonobese (BMI: 21.9-28.0) adults aged 21-51 y who were randomly assigned to 25% CR (CR, n = 143) or ad libitum control (AL, n = 75) in a 2:1 ratio. Measures at baseline and 12 and 24 mo included body weight, waist circumference, fat mass (FM), fat-free mass (FFM), and appendicular mass by dual-energy X-ray absorptiometry; activity-related energy expenditure (AREE) by doubly labeled water; and dietary protein intake by self-report. Values are expressed as means ± SDs.Results: The CR group achieved 11.9% ± 0.7% CR over 2-y and had significant decreases in weight (-7.6 ± 0.3 compared with 0.4 ± 0.5 kg), waist circumference (-6.2 ± 0.4 compared with 0.9 ± 0.5 cm), FM (-5.4 ± 0.3 compared with 0.5 ± 0.4 kg), and FFM (-2.0 ± 0.2 compared with -0.0 ± 0.2 kg) at 24 mo relative to the AL group (all between-group P < 0.001). Moreover, FFM as a percentage of body weight at 24 mo was higher, and percentage of FM was lower in the CR group than in the AL. AREE, but not protein intake, predicted preservation of FFM during CR (P < 0.01). Men in the CR group lost significantly more trunk fat (P = 0.03) and FFM expressed as a percentage of weight loss (P < 0.001) than women in the CR group.Conclusions: Two years of CR had broadly favorable effects on both whole-body and regional adiposity that could facilitate health span in humans. The decrements in FFM were commensurate with the reduced body mass; although men in the CR group lost more FFM than the women did, the percentage of FFM in the men in the CR group was higher than at baseline. CALERIE was registered at clinicaltrials.gov as NCT00427193.

One way to investigate seedling establishment under controlled (or partially controlled) conditions isthrough mesocosm studies. Mesocosm studies provide a powerful means of quantifying causalrelationships in a controlled environment. This study will focus on the responses of seedlings to asequence of flooding and drying treatments. Work will be undertaken withinexperimental/laboratory set-ups, so there will be no specific work undertaken at MDB (Murray–Darling Basin) EWKR research sites.Four woody floodplain species, River Red Gum (Eucalyptus camaldulensis Dehnh.), Black Box(Eucalyptus largiflorens F.Muell.) and Coolibah (Eucalyptus coolabah Blakely & Jacobs), and onenative floodplain shrub species, Tangled Lignum (Duma florulenta Meissner), were identified as thekey target species (Burns & Gawne 2014). Seedling-specific literature reviews were undertaken toassess and collate existing information about the recruitment of seedlings of the four key species(Durant et al. 2016). The information collated from the literature review, as well as expertdiscussions and input through workshops, teleconferences and emails, forms the basis of thisexperimental design.The experiment will focus on addressing the primary question:‘What is the relationship between flow parameters such as duration, frequency and interflood-dryperiod (sequential, cumulative events) and establishment?’

2019 Annual Forum presentation - overview of the research delivered over the five year EWKR project

Appendix V1.1. Blue, green and in-between; setting objectives for and evaluating wetland vegetation responses to environmental flowsAppendix V1.2 Conceptualisation Research Activity ReportAppendix V1.3 Vegetation outcomes: what are we seeking and why?Appendix V1.4 Grow with the flowAppendix V2.1. Disentangling flow-vegetation relationships and legacy effects to inform environmental flowsAppendix V2.2. Data Integration and Synthesis Research Activity ReportAppendix V3.1. Field Assessment Experimental Design reportAppendix V3.2. From the four corners of the Basin: assessing vegetation responses to flow regimesAppendix V3.3. Vulnerability of resilient systems to the AnthropoceneAppendix V3.4. Field Site Assessment and Germination Trials Research Activity ReportAppendix V4.1. Recruitment of long-lived floodplain vegetation: literature reportAppendix V4.2. Recruitment of long-lived floodplain vegetation: mesocosm study experimental designAppendix V4.3. Early, late or constant – what are long-lived woody floodplain seedlings looking for?Appendix V4.4. Giving woody seedlings a fighting startAppendix V4.5. Contrasting establishment strategies amongst three dominant tree species of Australian desert floodplainsAppendix V4.6. Seedling Mesocosm Research Activity ReportAppendix V5.1. Vegetation Theme Data and Model InventoryAppendix V5.2. Vegetation Theme OutputsAppendix V5.3. Vegetation Theme Engagement and Communications activitiesAppendix V5.4. Vegetation Theme Final Presentation. Vegetation theme: predicting outcomes in response to flow and other drivers

The ‘Recruitment of Long-lived Floodplain Vegetation’ component of the MDB EWKR Vegetation Theme aims to increase our understanding of how recruitment and seedling establishment occurs in response to varying watering regimes. Four woody floodplain species, River Red Gum, Black Box, Tangled Lignum and Coolibah, were identified as key target species within the Murray–Darling Basin to investigate the drivers of sustainable populations within four field-based research sites, Upper Murray, Lower Murray, Macquarie Marshes and the Lower Balonne floodplain.Species-specific literature reviews where undertaken to assess and collate existing information available about the recruitment and establishment of seedlings. This review focused on understanding how flow and non-flow drivers influence recruitment and seedling establishment responses and the response to water regimes over multi-year timeframes for the key target species.

The EWKR vegetation theme sought to:1. Provide a framework and guiding principles to help define the process of ‘what are we watering for and why?’ to help refine objectives, define function and value, and select indicators across a range of spatial and temporal scales, given the myriad of potential vegetation outcomes; and2. Improve predictive capacity and the underlying knowledge base by determining drivers of responses to watering actions, for:a. Existing understory communitiesb. Seed bank diversityc. Woody seedling establishmentd. Lignum structureThe EWKR vegetation theme shows that there is incredible variation in local plant communities and associated seed banks in space and time. This is even though many wetland and floodplain species have wide distributions, are largely cosmopolitan species and are rarely considered endemic. The vegetation theme looked at what causes this variation and how to predict it, and we are beginning to be able to determine community assembly rules. We’re starting to be able to: i) identify what the significant drivers are; ii) determine their relative importance; and iii) understand their interactions.

In a landscape that is predicted to become increasingly managed, wetlands will become either wetter or drier for longer periods and, as a consequence, the ability of biota with limited dispersal mechanisms to re-colonise when favourable conditions occur will be reduced. Recent swings between drought and flood conditions across a large part of Australia have raised questions about how well wetland/riverine plants disperse and re-colonize in the face of changes in water allocations and under climate change. This ACEAS working group proposed to: 1. Construct a listing of wetland and riparian plants from habitats in different parts of Australia 2. Confirm and apply the empirical models of life history traits to functional groupings of these species under various water regime scenarios for each region 3. Develop response models to projected changes in climate and water regulation.&nbsp