Draft Conservation Advice for the Kangaroo Island Dunnart

THREATENED SPECIES SCIENTIFIC COMMITTEE Established under the Environment Protection and Biodiversity Conservation Act 1999

The Scientific Committee finalised this assessment on dd/mm/yyyy. The Minister amended the list of threatened species to reflect the Committee’s advice on dd/mm/yyyy .

DRAFT CONSERVATION ADVICE FOR PUBLIC COMMENT – DECEMBER 2019

DRAFT Conservation Advice

Sminthopsis aitkeni Kangaroo Island Dunnart

Cover image: Kangaroo Island Dunnart © Jody Gates

Approved on DD MM YYYY

Conservation Status Sminthopsis aitkeni (Kangaroo Island Dunnart) is listed in the Endangered category of the threatened species list under the Environment Protection and Biodiversity Conservation Act 1999 (Cwlth) (EPBC Act). The species is eligible for listing as Endangered because prior to the commencement of the EPBC Act, it was listed as Endangered under Schedule 1 of the Endangered Species Protection Act 1992 (Cwlth).

The Kangaroo Island Dunnart is also listed as Critically Endangered by the International Union for Conservation Nature (IUCN) under the criterion of B1ab(i,ii,iii,iv,v)—i.e. small extent of occurrence, few locations and continuing decline.

Species can also be listed as threatened under state and territory legislation. For information on the current listing status of this species under relevant state or territory legislation, see http://www.environment.gov.au/cgi-bin/sprat/public/sprat.pl

Scientific Name The Kangaroo Island Dunnart is listed under the EPBC Act as Sminthopsis aitkeni.

Taxonomic status is not firmly resolved, and further research is a priority to resolve the affinities and nomenclature of the Sminthopsis fuliginosus aitkeni and Sminthopsis griseoveter aitkeni complex (Jackson & Groves 2015).

Description The Kangaroo Island Dunnart (hereafter referred to as the KI Dunnart) is the only species of dunnart found on Kangaroo Island and is endemic to the island. It is similar in morphology to the Common Dunnart (Sminthopsis murina) and was originally recorded as this species. However, electrophoretic and morphological studies in the early 1980s distinguished the KI Dunnart as a separate species (Baverstock et al. 1984 & Kitchener et al. 1984). More recent studies suggest it may be a subspecies of the Grey Bellied Dunnart (Sminthopsis griseoventer (now fuliginosis) (Kemper et al. 2011). The KI Dunnart is notable for its dark grey sooty dorsal pelage and light grey ventral pelage. The KI Dunnart is differentiated from other small mammals on Kangaroo Island by its pointed snout and wide, square-shaped ears (Hohnen 2019). The thin tail is always longer than the body and clearly bicoloured (Menkhorst and Knight 2004). Adults of this species grow between 80-90 mm long and weigh up to 25 g (Strahan 1998).

Distribution Historical records from 1969-1976 reported that all KI Dunnart sightings were from the central and eastern parts of Kangaroo Island in areas where intensive land clearing was occurring. Its current distribution on Kangaroo Island is unknown, although since 1990, all records of the KI Dunnart are from the western end of the Island within Flinders Chase National Park, Ravine des Casoars Wilderness Protection Area and areas of remnant native vegetation on private land (Figure. 1). Survey work in 1999-2001 by Gates (2001) detected 22 individual KI Dunnarts at six sites, within the Flinders Chase National Park. Surveys by Hohnen et al. (2019) in 2017-2018 detected individuals on seven occasions at five sites all in the western end of the island. Surveys conducted between April 2018 and May 2019 detected KI Dunnarts on 42 occasions at six sites within areas of remnant native vegetation on private land (H Groffen. pers comm 2019).

The majority of survey effort on western Kangaroo Island focussed on easily accessible areas and from this, it is likely that KI Dunnarts occur at other sites within Flinders Chase National Park, Ravine des Casoars Wilderness Protection Area and in surrounding remnants of native vegetation, including large areas of private conservation land. It is estimated that KI Dunnarts occur in approximately 27% (95%CI 7-65%) of the eucalypt woodlands on the western end of Kangaroo Island (Hohnen et al. 2018). The area of occupancy for the KI Dunnart has been identified as approximately 8% (352 km2) of the total area of the island (4405 km2).

Although early records of the KI Dunnart come from the central and eastern parts of the island, clearance, modification and fragmentation of these habitats has reduced the likelihood of KI Dunnarts still occurring there. Since 1979 there have been no confirmed detections of the KI Dunnart east of North Coast Road and Gosse-Ritchie Road (longitude 170°E). Extensive surveys have been conducted on the eastern side of Kangaroo Island (Herbert 1996; Robinson & Armstrong 2000; Jones et al. 2010; Gates 2001 & Molsher et al. 2019), including the Dudley Peninsula, and they have failed to detect KI Dunnarts. However, these surveys have primarily used pitfall traps and rarely reached the 51 days required of this particular method to achieve a 95% detection probability (Hohnen et al. 2019).

Figure 1. The location of identified KI Dunnart records including collected specimens, trapped and photographed individuals.

Figure 2. Predicted dunnart occurrence based on species distribution modelling (Hohnen et al. in review a).

Cultural Significance There are no Indigenous cultural values known for this species.

Relevant Biology/Ecology

Diet Dunnarts (Sminthopsis spp.) are primarily nocturnal, opportunistic foragers and predominantly feed on insects, spiders and other terrestrial arthropods (Van Dyck 2008). One preliminary study using scat analysis (Gates 2001) of 14 captured individuals identified spiders and ants as the most common food group recorded in the diet of the KI Dunnart, occurring in 59% and 56% of scats (n=25) respectively. Beetles and scorpions were also commonly consumed, being recorded within 36% of scats. The remains of a centipede and grasshopper were also recorded in one scat. These results demonstrate the expected diet of KI Dunnarts as all food groups recorded were ground-dwelling invertebrates.

Reproductive Biology There is still limited understanding about the reproductive cycle of KI Dunnarts. Most dunnart species have been found to be polyoestrous (capable of breeding several times a year), with rapid maturation of young that require minimal parental care (Lee & Cockburn 1985). Polyoestry has been shown to provide a survival advantage for the Common Dunnart in the unpredictable and short-lived conditions that categorise early-mid stage post-fire habitat (Fox and Whitford 1982).

All live captures during the 1999-2001 surveys occurred between January and May with over half being juveniles/sub-adults (<16 g). No adult females were caught during this survey (Gates 2001). Of interest though is the fact that at one site, juveniles of less than 11 g were captured in January and March in the same year. The most likely explanation for the two cohorts of juveniles is that females are polyoestrous, which is consistent with reproductive cycles observed for Common Dunnarts (Fox & Whitford 1982). Based on the growth and development of Common Dunnart young (Fox & Whitford 1982), these juveniles were estimated to be approximately 65- 4

115 days old. Taking into consideration that the gestation period is approximately 12 days (Fox & Whitford 1982), it is believed that mating occurred in mid-September to early October and in November to December.

Life History The period of juvenile dependency is unknown, although studies on the similar Common Dunnart have shown this period to be approximately 65 days (Fox & Whitford 1982). As outlined above, the most recent live captures occurred post-breeding season in late summer and autumn (Gates 2001). Although no data exist for the life expectancy of the KI Dunnart, based on the life histories of other Sminthopsis spp., females may survive to breed in a second year, whereas males are less likely to survive beyond one breeding season. The predominance of captures of juveniles in summer and autumn provides circumstantial evidence to support this. Studies at known dunnart sites have shown that dunnarts are consistently detected throughout the year but detections decrease over winter (P. Hodgens. pers. comm 2019).

The home range dynamics and patterns of movement remain a critical gap of knowledge for this species. Radio tracking of some individuals indicated that range lengths are approximately 200- 300 m, however, seasonal patterns of home range use and differences between sexes in use of habitat and space are not clear (Gates 2001). The dispersal patterns of juveniles from their natal range are also unknown. A range of short term movement patterns are displayed by closely related species of dunnart, with differential habitat use a likely explanation (Monamy & Fox 2000). Nomadic movements, which allow individuals to locate to areas where vegetation density is optimal, appear to be a consistent pattern across a range of Dasyurid species. Nomadic movement patterns have been displayed by the Common Dunnart, Julia Creek Dunnart (Sminthopsis douglasi) and the Lesser Hairy-footed Dunnart (Sminthopsis youngsoni) with individuals utilising different resting sites over a period of days to weeks (Haythornthwaite & Dickman 2006; Monamy & Fox 2000; Righetti et al. 2000)

Habitat Use and Home Range Size Limited radio tracking data has shown that a range of micro-habitats are selected for shelter during the day (Gates 2001). KI Dunnarts were found sheltering under Yaccas (Xanthorrhoea spp.) where the fronds are continuous to ground level, in leaf litter under Desert Banksias (Banksia ornata), in holes/burrows and inside a dead Yacca trunk. At the Kurralinga site there appeared to be a preference for sheltering under Yaccas, including ones that had succumbed to Phytophthora cinnamomi dieback. The dunnarts also spent periods of up to four hours using these shelters at night. The capture of dunnarts over a period of 11 and 18 years at multiple sites suggest that some areas provide core habitat, and dunnarts continually occupy such areas for relatively long periods of time (Gates 2001; Jones et al. 2010; Hohnen et al. 2019). The use of the mark-recapture and telemetry studies in future surveys may assist in clarifying some of this information.

Habitat critical to the survival The KI Dunnart occurs across a wide range of native vegetation and habitat types within its area of occupancy. The majority of sites where KI Dunnarts are currently known to occur fall within the higher rainfall areas (>600 mm) of Kangaroo Island. Recent modelling found that rainfall, along with the age of post-fire vegetation are important predictors of dunnart occurrence (Hohnen et al. in review a). This modelling has shown that the highest likelihood of KI Dunnart occurrence are in areas of high rainfall and vegetation age classes of less than 20 years post- fire (Hohnen et al. in review a). However, further research needs to be undertaken in relation to

the impact of fire and suitable habitat. KI Dunnarts have been sighted in vegetation that has not been burnt since 1959 (T Robinson and J Haska. pers. comm).

The major vegetation assemblages in western Kangaroo Island consist of open low mallee, (Kangaroo Island mallee ash Eucalyptus remota, and Coastal Mallee Eucalyptus diversifolia) and low woodland (Brown Stringybark Eucalyptus baxteri), and KI Dunnarts have been recorded within both assemblages. There is considerable variation within these two associations, with a variety of secondary overstorey species, and varying floristics and densities within the understorey species including:

• Desert Banksia (Banksia ornata)

• Silver Banksia (Banksia marginata)

• Guinea-flowers (Hibbertia species)

• Yaccas (Xanthorrhoea semiplana tateana)

• Beaked Hakea (Hakea rostrata)

• rushes (Lepidosperma species)

• Beard-heath (Leucopogon concurvus)

• Kangaroo Island Cone-sticks (Petrophile multisecta)

• Common Fringe-myrtle (Calytrix tetragona).

This floristic diversity suggests that vegetation structure is a stronger driver of dunnart distribution than floristics, and that dunnarts prefer habitats with a less dense, sclerophyllous understorey. However, as suggested above, a precise description of critical habitat features is still not understood.

Broadly, habitat critical to this species includes all intact vegetation in high rainfall areas of Kangaroo Island.

Important populations All populations of KI Dunnart should be considered important for the long-term recovery of the species.

Threats The main identified threats to the KI Dunnarts both directly and indirectly are habitat loss through extensive and high intensity bushfires, land clearing and Phytophthora cinnamomi dieback, the predation from invasive species such as feral cats and the potential loss of genetic diversity through isolation of populations.

Table 1: Threats impacting the Kangaroo Island Dunnart. Threat Threat status Evidence base

1. Habitat Fragmentation and Degradation 1.1 •historical/ The greatest threats to the KI Dunnart are the direct Extensive and current/ future, (mortality) and indirect (loss of habitat) effects of large high-intensity known, severe extent and high-intensity bushfires. However, the bushfires and and across the distributional modelling also suggests that long periods Inappropriate entire range without fire may also be detrimental to the species, with Fire Regimes preferred fire regimes likely to include a mix of post-fire successional stages with at least some early regrowth (approximately 5-20 years post fire) (Hohnen et al in review a).

Large fire events are not uncommon in the western part of Kangaroo Island. In 1990 and 1991, over 50% of Flinders Chase National Park was burnt by bushfire/back burns. In December 2007, approximately 80% of the Ravine des Casaors Wilderness Protection Area and Flinders Chase National Park was burnt by bushfire and associated control burns (Peace & Mills 2012). The 2007 bushfire also meant that the majority of the aforementioned protected areas are of the same vegetation age class. This results in minimal habitat options for dunnart if the vegetation structure and composition becomes unsuitable as it ages.

Extensive and high intensity bushfires and some suppression activities (especially large-scale back burns) pose the greatest threat to the KI Dunnart. These events often result in large expanses of vegetation being burnt with the potential for high rates of direct mortality and loss of large areas of habitat. Large bushfires also reduce the chance for a mosaic of different post-fire age-classes of vegetation to develop which presents an additional threat to the survival of the KI Dunnart. Fire is largely excluded from habitats in the central and eastern parts of Kangaroo Island and older habitats that are present there now may be unsuitable for KI Dunnarts.

In addition, inappropriate fire management or large bushfires may exacerbate the threat to the KI Dunnart by reducing the available habitat and increasing the predation pressure from feral cats post-fire (Hradsky et al. 2017). This is addressed in 2.1.

1.2 current/ future, The loss of habitat through Phytophthora cinnamomi Phytophthora known, severe dieback is also a significant threat to the species. The cinnamomi and across part impacts of Phytophthora cinnamomi are evident in areas Dieback of its range where KI Dunnarts have been recorded (Figure 3).

It is not clear how direct and indirect changes to the habitat structure resulting from Phytophthora cinnamomi may impact on KI Dunnarts. Individuals were recorded sheltering in plant species that are susceptible to Phytophthora cinnamomi infestation such as Yaccas (Xanthorrhoea semiplana tateana). The spread of Phytophthora cinnamomi dieback may lead to a decrease in shelter availability, reduced availability of invertebrates and increased risk of predation in open vegetation. A wide range of understorey plant species are susceptible with Yaccas (Xanthorrhoea semiplana tateana), Desert Banksia (Banksia ornata) and Silver Banksia (Banksia marginata) being indicator species because of their acute susceptibility.

Control mechanisms for Phytophthora cinnamomi primarily focus on removing the potential of spreading via soil attached to vehicles, machinery or footwear. Any activity that moves soil, organic material or water into susceptible native vegetation areas has the potential to introduce and spread soil pathogens (Threat abatement plan Phytophthora 2018). Systematic treatment of phosphate and nutrient has been shown to induce a resistance and reduce the spread of Phytophthora cinnamomi in affected areas (Scott et al. 2015). 1.3 Historical, Historically the KI Dunnart was distributed broadly across Land Clearing severe and the Island. Clearance has resulted in a substantial loss across part of its and fragmentation of habitat and there is still limited range understanding of the size of habitat patches that could support a viable population of KI Dunnarts. The majority of surveying to date has concentrated on relatively large areas of habitat but it is possible that populations may have survived in smaller areas.

Although land clearing does not occur on the scale that it previously did, areas may still be cleared illegally and legally for permitted developments including urbanisation. 1.4 Suspected, Island fauna are known to be particularly susceptible to Climate Change Future, across rapid changes in climate due to an inability of species to the entire range migrate to suitable habitat (Courchamp et al. 2014). The narrow altitudinal and latitudinal range of Kangaroo Island increases the risk that suitable conditions for the KI Dunnart will not be present on the island under future climate scenarios.

Western Kangaroo Island has been identified as an area with a high predicted climate change velocity showing that under current trajectories the temperature conditions on Kangaroo Island will be drastically different over the next 50 years (Guerin et al. 2018). Under all greenhouse gas 8

emissions scenarios, rainfall during winter in southern South Australia is projected to decrease by 15% by 2030 and by as much as 45% by 2060 (CSIRO Australia 2019). Due to the KI dunnarts likely occurrence associated with rainfall, these changes could have severe negative impacts on the species. In addition, changes to rainfall patterns and therefore vegetation structure may influence fire regimes which could compound this threat to KI Dunnart populations. 2. Invasive Species

2.1 Predation by Suspected, Feral Cats (Felis catus) are also suspected to present a Feral Cats current/ future significant threat to the survival of the KI Dunnart. and severe and Feral cats are widespread and in high densities (0.67 across the entire cats/km2) on Kangaroo Island (Hohnen et al. in review b). range Feral cats and/or their faeces have been observed at most dunnart sites (R. Hohnen & P. Hodgens pers. obs) confirming the potential for predation. Furthermore, the presence of feral cats has been shown to increase the extinction risk for small mammals on the Australian mainland and on Australian islands (Burbridge & Manly 2002; Woinarski et al. 2015; Radford et al. 2018).

While there is no direct evidence of cat predation on the KI Dunnart, predation from feral cats is likely to pose a direct threat and is also known to increase in burnt areas following bushfire (McGregor et al. 2016; Leahy et al. 2016). Inappropriate fire management or large bushfires may exacerbate the threat to the KI Dunnart by reducing the available habitat (and especially cover to ground level) and increasing the predation pressure from feral cats post-fire.

Cats also carry toxoplasmosis, a disease that affects dunnarts (Attwood et al 1975; Canfield et al 1990). There is currently no evidence that KI Dunnarts are affected by toxoplasmosis and no research has been undertaken on this potential risk/threat to this species.

A cat eradication program is being carried out on the Eastern end of the Island, and this will progressively be rolled out across Kangaroo Island in the longer term. 3. Poor recruitment and loss of genetic diversity

3.1 Suspected Little is known about the movement patterns and Loss of Genetic population dynamics of KI Dunnarts. Isolation of Diversity populations due to habitat fragmentation may lead to inbreeding and a loss of genetic diversity.

Figure 3. Distribution of suspected and confirmed Phytophthora cinnamomi infestations on Kangaroo Island including status of National Parks and Reserves (DEWNR 2012).

Conservation Objectives, Performance Criteria and Conservation and Management Actions

Long Term Objective Within 20 years the area of suitable habitat is increased and threats are actively managed to support recovery of the KI Dunnart.

It is anticipated that this conservation advice will inform activities at both the landscape-scale level, across the island and at the local level at individual sites, with action supporting and complementing other land management planning.

All actions in this Conservation Advice will contribute to the conservation of the Kangaroo Island Dunnart and will need to be progressively implemented over time to meet objectives. However, to inform timing and urgency of actions, each is assigned a priority: ‘urgent’ (i.e. the conservation future of the species depends upon this action being implemented), ‘essential’ (i.e. the conservation future of the species will be limited if this action is not implemented), or ‘highly beneficial’ (i.e. this action will contribute to the conservation future of this species).

Objective 1. Extent of suitable habitat known is increased, and restored where appropriate

Performance Criteria

• Increase in the number of known KI Dunnart sites within 5 years.

• Identification and increase in the extent of suitable habitat within 5 years.

• Reduce potential impacts of climate change by improving connectivity, fire regimes, and by reducing predator density (this criterion also refers to actions under the Objectives 2 – 6).

Conservation and Management Action

1.1 Based on the recent species distribution modelling (Hohnen et. at.), and potentially climate change predictive future modelling (Action 7.9), map existing habitat patches and identify new habitat. [Priority: essential] 1.2 Investigate the possible restoration of corridors between patches to increase the potential for movement and gene flow for this species. [Priority: essential] 1.3 If appropriate undertake restoration of the corridors on public and private land. [Priority: highly beneficial] 1.4 Survey for new KI Dunnart sites. [Priority: essential]

Objective 2. The risk of fire to known KI Dunnart habitat is reduced.

Performance Criteria

• Within 5 years the fire related requirements of the KI Dunnart and their habitat is better understood and is informing management decisions.

Conservation and Management Action

2.1 Within one year, update the Ecological Fire Management Strategy for the Kangaroo Island Dunnart to ensure improved strategies for the ongoing survival of the species, including the timing of the burns, and a mosaic of fire age classes of vegetation. [Priority: urgent] 2.2 Reduce risk to known and predicted dunnart habitat from large extent high-intensity bushfires through adaptive fire management practices. [Priority: urgent] 2.3 Update the Fire Management Plans for the Flinders Chase National Park and Ravine des Casoars Wilderness Protection Area within two years, incorporating the updated Ecological Fire Management Strategy for the Kangaroo Island Dunnart. [Priority: essential] 2.4 Develop or update, fire management plans for areas that are known KI Dunnart sites on private properties, incorporating the updated Ecological Fire Management Strategy for the Kangaroo Island Dunnart and fire management plans for bordering properties and parks. [Priority: urgent] 2.5 Undertake ecological and prescribed burns on a periodic, rotational basis, to establish and then maintain mosaic pattern of post-fire vegetation age through areas within and around known KI Dunnart sites. [Priority: urgent] 2.6 For prescribed burns at known and predicted KI Dunnart sites and unburnt control sites, where practicable, use fence-line camera traps to detect KI Dunnarts in the summer or spring preceding the burn and in the following four years. [Priority: essential]

Objective 3. Phytophthora cinnamomi does not spread further into KI Dunnart habitat.

Performance Criteria

• Phytophthora has not spread further into KI Dunnart habitat.

Conservation and Management Actions

3.1 Monitor Phytophthora infestations, and undertake mapping at a fine-scale around known KI Dunnart sites. [Priority: urgent] 3.2 Implement risk mitigation and management actions, such as improved hygiene and quarantine measures to protect known KI Dunnart sites from Phytophthora (refer to the threat abatement plan for Phytophthora cinnamomi). [Priority: urgent] 3.3 Monitor and treat Phytophthora infestations at KI Dunnart sites to track and restrict spread of infestations. [Priority: essential] 3.4 Increase education awareness across the island, including landholders and visitors about Phytophthora mitigation to prevent further spread of Phytophthora across the island. [Priority: highly beneficial]

Objective 4. Cat predation does not limit KI Dunnart population size.

Performance Criteria

• Increase in KI Dunnart numbers with a decrease in cat density at known sites.

• Improved clarity on threat of cats to KI Dunnart through cat stomach contents analysis.

Conservation and Management Actions

4.1 Manage the threat of feral cat predation around known KI Dunnart habitats through appropriate feral cat control measures. [Priority: urgent] 4.2 Using camera trap arrays, monitor cat populations at targeted KI Dunnart sites to ensure cat control efforts are effective, leading to decreases in the numbers of cats and increases in the number of KI Dunnarts. [Priority: urgent] 4.3 Investigate the predation threat from feral cats by euthanising at least 30 feral cats annually in areas around known KI Dunnart sites and conducting stomach contents analysis. [Priority: highly beneficial]

Objective 5. Options for ex-situ and in-situ refugia to protect and increase the population of KI Dunnarts are assessed and implemented as required

Performance criteria

• Within two years, the feasibility of ex-situ and in-situ insurance populations has been assessed with an appropriate planning response secured.

• Within five years, recommended actions are underway.

Conservation and Management Actions

5.1 Assess the conservation benefits, feasibility and risks of establishing possible combinations of in-situ refuge, captive breeding or translocated insurance population of KI Dunnarts and develop a comprehensive planning response if appropriate. [Priority: essential] 5.2 Implement plan recommendations. [Priority: essential]

Objective 6. An ongoing monitoring program is effectively implemented that reports on KI Dunnart population trends, status and effectiveness of conservation actions.

Performance Criteria

• Within one year, an ongoing monitoring program is established.

• Monitoring effort is increased.

• Population (or occurrence) monitoring results are reported at least annually, and influence management actions.

Conservation and Management Actions

6.1 Within one year establish an ongoing monitoring program at all known KI Dunnart sites to build on baseline data. [Priority: urgent]

o This should be achieved through camera traps facing drift fence lines for at least 30 nights in autumn, and 17 nights in spring (Hohnen et al 2019). Number of sites surveyed needs to be determined.

6.2 Monitoring is designed appropriately to evaluate the response of KI Dunnarts to inform threats and conservation management actions. [Priority: urgent] 6.3 Undertake additional fence-line camera trap surveys in the vicinity of recently recorded sites, including utilising volunteers, community groups and landholders. [Priority: essential] 6.4 Regularly update Biological Database of South Australia (BDBSA) and Atlas of Living Australia) ALA to ensure that significant dunnart sites can be identified for monitoring, protection and fire management [Priority: highly beneficial]

Objective 7. A research program is established to address key knowledge gaps to ensure management is better informed.

Performance Criteria

• A research program is established, targeting key knowledge gaps.

• Increased understanding of KI Dunnart ecology and biology and threats.

• Management response to new research.

Conservation and Management Actions

7.1. Collect genetic samples and document size, sex and breeding condition of all live captured individuals to improve knowledge of life history, population dynamics and taxonomy of KI Dunnart. [Priority: urgent] 7.2. If practicable, undertake mark-recapture (pitfall trapping) and telemetry studies to clarify population estimates, home range size, movement patterns and habitat use. [Priority: urgent] 7.3. Improve knowledge of KI Dunnart response to fire through monitoring pre- and post-fire in areas of suspected and known KI Dunnart occurrence. [Priority: urgent] 7.4. Conduct vegetation surveys at all known KI Dunnart sites to clarify our understanding of the habitat requirements for the species and as inputs to generalised linear models. [Priority: essential] 7.5. Model suitable habitat under different climate change scenarios, to support the identification of future suitable habitat. [Priority: essential] 7.6. Where appropriate and practicable, undertake experimental burns in sections of long- unburn habitat, and evaluate any responses by KI dunnarts. [Priority: highly beneficial] 7.7. Assess invertebrate resource availability for KI dunnarts in a range of habitat types or post-fire successional stages. [Priority: highly beneficial] 14

7.8. Undertake a research project that assesses habitat suitability (e.g. invertebrate resource abundance, shelter availability) for KI dunnarts in areas exposed to Phytophthora infestation cf. uninfected areas. [Priority: highly beneficial] 7.9. Extend surveys for the KI Dunnart through suitable habitats to confirm and clarify species distribution modelling (Hohnen et al. in review a). [Priority: highly beneficial]

Objective 8. Increased community awareness of, support for, and where relevant involvement in, the implementation of actions to support the recovery of the KI Dunnart.

Performance Criteria

• Community awareness of, support for, and participation in the KI Dunnart recovery is increased.

• A recovery team is established, operates effectively and coordinates implementation of the conservation advice.

• Public information and education materials are developed and implemented.

Conservation and Management Actions

8.1 Engage the community in establishing monitoring sites (see Action 6.2) and in the collection and processing of images from camera traps. [Priority: highly beneficial]

8.2 Advertise planned recovery activities and target local community groups and landholders to encourage and facilitate participation in on-ground management and research actions. [Priority: highly beneficial]

8.3 Establish and maintain an effective recovery team to oversee implementation of the conservation advice. [Priority: highly beneficial]

8.4 Promote and publicise the conservation advice and recovery efforts across Kangaroo Island. [Priority: highly beneficial]

THREATENED SPECIES SCIENTIFIC COMMITTEE Established under the Environment Protection and Biodiversity Conservation Act 1999

The Scientific Committee finalised this assessment on dd/mm/yyyy. The Minister amended the list of threatened species to reflect the Committee’s advice on dd/mm/yyyy .

References cited in the advice

Attwood HD, Woolley PA & Rickard MD (1975) Toxoplasmosis in dasyurid marsupials, Journal of Wildlife Disease 11, 4, pp. 543-551.

Baverstock PR, Adams M & Archer M (1984) Electrophoretic resolution of species boundaries in the Sminthopsis murina complex (Dasyuridae). Australian Journal of Zoology 32, 823-832

Burbidge AA & Manly BFJ (2002) Mammal extinctions on Australian islands: causes and conservation implications, Journal of Biogeography 29, 4, pp. 465-473.

Canfield PJ, Hartley WJ & Dubey JP (1990) Lesion of toxoplasmosis in Australian marsupials, Journal of Comparative Pathology 103, 2, pp. 159-167.

Courchamp F, Hoffmann BD, Russell JC, Leclerc C & Bellard C (2014). Climate change, sea- level rise, and conservation: keeping island biodiversity afloat. Trends in ecology & evolution, 29(3), 127-130.

CSIRO Australia (2019) ‘Climate change in Australia, projections for Australia's NRM regions’, in https://www.climatechangeinaustralia.gov.au/en/climate-projections/future-climate/regional- climate-change-explorer.

Fox BJ & Whitford D (1982) Polyoestry in a predictable coastal environment: reproduction, growth and development in Sminthopsis murina (Dasyuridae, Marsupialia), In ‘Carnivorous Marsupials’, (Ed. M Archer), 1, pp. 39-48.

Gates JA (2001) The distribution and ecology of the Kangaroo Island dunnart Sminthopsis aitkeni, Endangered Species Project (006499).

Guerin GR, O’Connor PJ, Sparrow B & Lowe AJ (2018) An ecological climate change classification for South Australia, Transactions of the Royal Society of South Australia 142, 1, pp. 70-85.

Haythornthwaite A & Dickman CR (2006) Long‐distance movements by a small carnivorous marsupial: how Sminthopsis youngsoni (Marsupialia: Dasyuridae) uses habitat in an Australian sandridge desert, Journal of Zoology 270, 3, pp. 543-549.

Herbert T (1996) Distribution, Habitat Preference and Status of the Kangaroo Island Dunnart (Smithopsis aitkeni). Nature Conservation Society of South Australia, Adelaide

Hohnen R, Murphy BP, Gates JA, Legge S, Dickman CR, Woinarski JCZ (2019) Detecting and protecting the threatened Kangaroo Island dunnart (Sminthopsis fuliginosus aitkeni), Conservation Science and Practice 1, e4, pp. 1-11.

Hohnen R, Murphy BP, Legge S, Dickman CR, Hodgens P, Groffen H, Molsher R, Gates JA & Woinarski JCZ (in review a) Habitat Preferences of the Kangaroo Island dunnart (Sminthopsis fuliginosus aitkeni), Australian Mammalogy.

Hohnen R, Murphy BP, Legge S, Dickman CR, Hodgens P, Groffen H, Molsher R, Gates JA, & Woinarski JCZ (in review b) Uptake of “Eradicat” feral cat baits by non-target species on Kangaroo Island, Wildlife Research.

Hradsky BA, Mildwaters C, Ritchie EG, Christie F & Di Stefano J (2017) Responses of invasive predators and native prey to a prescribed forest fire, Journal of Mammalogy 98, 3, pp. 935-847.

Jackson, S. M., & Groves, C. (2015). “Taxonomy of Australian mammals.” CSIRO publishing.

Jones S, Mooney T, Ross J & Pisanu P (2010) The distribution and ecology of threatened small mammals on Kangaroo Island, Department for Environment and Heritage, Kingscote, South Australia.

Kitchener DJ, Stoddard J & Henry J (1984) A taxonomic revision of the Sminthopsis murina complex (Marsupialia, Dasyuridae) in Australia, including descriptions of four new species. Records of Western Australian Museum 11, 201-48.

Leahy, L., Legge, S., Tuft, K., McGregor, H. W., Barmuta, L. A., Jones, M. E., and Johnson, C. N. (2016). Amplified predation after fire suppresses rodent populations in Australia’s tropical savannas. Wildlife Research 42, 705-716.

Lee AK & Cockburn A (1985). Evolutionary Ecology of Marsupials. Oxford University Press, Cambridge.

McGregor, H. W., Legge, S., Jones, M. E., & Johnson, C. N. (2016). “Extraterritorial hunting expeditions to intense fire scars by feral cats.” Scientific reports, 6, 22559.

Menkhorst P (1995) Common Dunnart, Mammals of Victoria, Oxford University Press and Department of Conservation and Natural Resources, South Melbourne, pp. 66-67.

Menkhorst, P.W & Knight, F. (2004). A Field Guide to the Mammals of Australia. Oxford University Press, Melbourne.

Molsher R, Hodgens P & Dowie D (2019) Kangaroo Island Biodiversity and Rodent Monitoring Progress Report, Natural Resources Kangaroo Island, Kingscote, South Australia.

Monamy V & Fox BJ (2000) Small mammal succession is determined by vegetation density rather than time elapsed since disturbance, Austral Ecology 25, 6, pp. 580-587.

Peace M & Mills G (2012) A case study of the 2007 Kangaroo Island bushfires, CAWCR Technical Report No. 53, CSIRO

Radford, J. Q., Woinarski, J. C. Z., Legge, S., Baseler, M., Bentley, J., Burbidge, A. A., Bode, M., Copley, P., Dexter, N., Dickman, C. R., Gillespie, G., Hill, B., Johnson, C. N., Kanowski, J., Latch, P., Letnic, M., Manning, A., Menkhorst, P. W., Mitchell, N., Morris, K., Moseby, K. E., Page, M., and Ringma, J. (2018). Degrees of population-level susceptibility of Australian mammal species to predation by the introduced red fox Vulpes vulpes and feral cat Felis catus. Wildlife Research 45, 645-657.

Righetti J, Fox BJ & Croft DB (2000) Behavioural mechanisms of competition in small dasyurid marsupials, Australian Journal of Zoology 48, 5, pp. 561-576.

Robinson A and Armstrong D (2000). A Biological Survey of Kangaroo Island South Australia. Department for Environment and Aboriginal Affairs, Adelaide.

Scott PM, Barber PA and Hardy G (2015) Novel phosphite and nutrient application to control Phytophthora cinnamomi disease. Australasian Plant Pathology, 44 (4). pp. 431-436

Strahan R (1998) The Mammals of Australia (2nd ed.) The Australian Museum & Sydney: Reed Books.

Threat Abatement Plan Phytophthora cinnamomi (2018)‘Threat abatement plan for disease in natural ecosystems caused by Phytophthora cinnamomi’, Commonwealth of Australia 2018.

Van Dyck S & Strahan R (2008) The mammals of Australia, New Holland Pub Pty Limited.

Woinarski JCZ, Burbidge AA & Harrison PL (2015) Ongoing unravelling of a continental fauna: decline and extinction of Australian mammals since European settlement, Proceedings of the National Academy of Sciences 112, 15, pp. 4531-4540.