Injured flying-foxes (Pteropus spp.) are frequently taken into care in eastern Australia. In particular, the grey-headed flying-fox (P. poliocephalus), a vulnerable species, is affected by several threats, which are partly mitigated through rescue and rehabilitation. This study examined patterns in flying-fox rescues in New South Wales (NSW) between 2011–12 and 2016–17 using annual reporting data from wildlife rehabilitation organisations. Specifically, we examined (1) species and demographic patterns in flying-foxes rescues; (2) the geographical distribution of flying-fox rescues; (3) reported causes of injury; and (4) release rates of rehabilitated flying-foxes. P. poliocephalus accounted for the largest proportion of flying-fox rescues. Most rescues occurred in coastal regions, with more than one-third of P. poliocephalus rescues occurring in the Sydney region and more than one-third of black (P. alecto) and little red (P. scapulatus) flying-fox rescues occurring on the NSW Far North Coast. A broad range of factors was involved in flying-foxes coming into care, the main ones being entanglements, heat stress, orphaned pups and electrocutions. Release rates of rehabilitated flying-foxes were high, especially in pups and juveniles. These results demonstrate the potential conservation value of flying-fox rehabilitation. High proportions of injuries caused by entanglements, heat stress and electrocutions highlight the importance of ongoing threat mitigation efforts.

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The Red-whiskered Bulbul Pycnonotus jocosus naturally occurs from the Indian subcontinent to the northern Malay Peninsula. Its anthropogenic spread also encompasses Australia, Japan, the southern Malay Peninsula, Singapore, Florida, California, 11 islands in the Indian Ocean, and Oahu, Hawaii. The earliest known introduction occurred in Sydney in 1865, with subsequent releases in the 1900's leading to establishment. It was first released in Melbourne, Victoria in 1915, with a population establishing in the late 1950's. Sightings have been reported in Coffs Harbour since 1972, forming a population in the Northern Rivers region. There has also been a small population in Mackay, Queensland since 1983. Redwhiskered Bulbuls had been recorded in South Australia between the 1940's and 1980's, but did not proliferate and are no longer present. The main ecological impact identified is the dispersal of exotic weeds, although evidence in Australia remains anecdotal. There has also been preliminary evidence of interspecific competition on islands and predation of nestlings. While aesthetically appreciated and a predator of some invertebrate pests, it causes crop failure in soft-fruit and citrus orchards and damage to garden plants. Impacts should be further investigated to justify management directions. Eradication in Australia may be achievable due to populations being mostly restricted to settled areas.

Mass mortalities in flying-foxes occur in summers that reach extremely hot temperatures. In this study, we examine the spatiotemporal distributions of mortality from pup abandonments and extreme heat events in Australian flying-fox camps during the 2019–20 summer. We recorded data on flying-fox mortality in known affected camps and applied a standard method to estimate the number of deaths. Pup mortalities from abandonments were recorded in 10 camps in New South Wales. A minimum estimate of 2612 flying-foxes died in pup abandonments, the majority of which occurred in one camp in Bomaderry. Die-offs from extreme heat events were recorded in 40 camps associated with eight separate heat events in south-eastern Australia. A minimum estimate of 72 175 flying-foxes died during these heat events, which all occurred within the range of the threatened grey-headed flying-fox (Pteropus poliocephalus). Further, 409 and 2251 live flying-foxes were taken into care from pup abandonments and heat events respectively. The minimum mortality estimated represents the highest recorded mortality of Australian flying-foxes within a single summer. This highlights a need to restore vegetation in flying-fox foraging areas and camps, address anthropogenic climate change and gather more empirical data to inform heat stress interventions to minimise flying-fox mortalities.

The invasive Red-eared Slider Trachemys scripta elegans has spread extensively, forming naturalised populations on all continents except Antarctica. Ranked among the 100 worst invasive species, there are biosecurity concerns that native turtles become outcompeted and displaced, as well as other speculative impacts. The actual ecological impacts in Australia have not been properly studied, however impacts shown in other countries are concerning. Incursions have presented in New South Wales, Queensland, Victoria, Western Australia and the Australian Capital Territory. A number of sightings have been reported from southern Sydney, including six sites where more than one slider has persisted. The incursions at Yeramba Lagoon in the Georges River National Park and the Centennial Parklands have been the most documented, whereas incursions in the Lime Kiln Bay Wetland, Rockdale Wetlands Corridor and Audley in the Royal National Park appear to have occurred recently. To date, breeding in southern Sydney has only been confirmed at Yeramba Lagoon. A range of removal techniques have been successfully applied to eradicate isolated incursions in Brisbane and Melbourne. However, these options are difficult to implement in southern Sydney sites where incursions occur in high visitation public lands.

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The permanent exclusion of flying-foxes from camps (camp dispersal) near human settlements is a management tool commonly used to mitigate human–wildlife conflict. We summarised information on the costs and outcomes of 48 camp dispersals in Australia. Our aim was to improve the information base on which camp management decisions are made. Camp dispersals were largely triggered by impacts on neighbouring residents (75%). A disproportionately high number occurred in 2013–14, associated with changes in Queensland flying-fox management policy following an increase in the number of urban camps. Repeat actions over months or years were typically required to exclude flying-foxes from camps (58%). In 88% of cases, replacement camps formed within 1 km and became sites of transferred conflict. Only 23% of dispersal attempts were successful in resolving conflict for communities, generally after extensive destruction of roost habitat. Costs were poorly documented, although no dispersal attempt costing less than AU$250 000 proved successful. We conclude that camp dispersal is a high-risk, high-cost tool for mitigating human–wildlife conflict, in situ management strategies and tools should be developed, evidence-based information on management options should be made available to stakeholders via a nationally curated resource library, and research is required on impacts of camp management practices on flying-foxes.

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