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Brush-tailed Rabbit-rat (Conilurus penicillatus)

The brush-tailed rabbit-rat is a 150 g, partly arboreal native rodent of monsoonal northern Australia and southern New Guinea. It is listed as Vulnerable under the EPBC Act and is sensitive to clearing of tall eucalypt forest, severe fire, loss of hollow-bearing trees and logs, and predation by feral cats, so suitable habitat and shelter resources need to be checked before clearing or construction.

Conservation status

Commonwealth, EPBC Act 1999: Vulnerable.

Queensland, Nature Conservation Act 1992: Vulnerable.

Western Australia, Biodiversity Conservation Act 2016: Vulnerable.

Northern Territory, Territory Parks and Wildlife Conservation Act 1976: Endangered.

Breeding season

The species breeds from March to October. Detection is highest in the late dry season, July to September, and juveniles are most often recorded from the mid to late dry season.

Month values run from January to December. A value of 0 means not typical, 1 means occurs, and 2 means peak or highest risk.

  • Breeding: Breeding extends from March to October, with females producing at least two litters where conditions allow.
  • Young: Juveniles predominantly enter the population during the mid to late dry season, especially June to September.
  • Survey detection and local activity: Detectability is about three times higher in the late dry season, July to September, than in the early dry season, April to June. The species is nocturnal and often active at dusk.
  • Highest clearing risk: Clearing and disturbance are most likely to harm the species from March to October because breeding and dependent young occur during this period. Habitat and shelter loss remain risks in all months, so seasonal timing does not remove the need for pre-clearing surveys and mitigation.

Identification

The brush-tailed rabbit-rat is a medium-sized, partly arboreal rodent with a distinctive tufted tail. Identification should be confirmed carefully because several northern Australian tree-rats use similar eucalypt woodland habitat.

Adults weigh about 150 g. The fur is relatively uniform brown or grey to golden brown above and white to cream below, sometimes with a rufous patch on the neck. It has long ears and a long tail with a dense brush at the tip; the distal part of the tail may be black or white.

Average male weight: 163 g

Average female weight: 144 g

Habit: Ground and tree-dwelling

Activity: Nocturnal, often active at dusk

Identification: Distinguishing features

It is distinctly smaller than the northern Australian tree-rats in the genus Mesembriomys. The golden-backed tree-rat has a distinct golden dorsal band and an entirely whitish tail, whereas the brush-tailed rabbit-rat has a darker basal tail and a dense black or white terminal brush. It is also smaller than the black-footed tree-rat and lacks black feet and ears.

Identification: Field detection

The species is most likely to be encountered at dusk or during the night, on the ground or climbing in trees. Daytime searches should target large rough-barked trees with hollows, hollow logs, perennial grass seed sources and areas that have not been recently severely burnt.

The supplied sources do not describe diagnostic tracks, scats, calls or eyeshine. A suspected record should therefore be documented with clear photographs, location, habitat, time, detection method and, where appropriate, expert confirmation. Live trapping, cage trapping and camera trapping are recognised survey options for this species.

  • Do not treat a single unconfirmed small-rodent observation as a brush-tailed rabbit-rat record.
  • Record hollow-bearing trees, hollow logs, dense ground cover and recent fire evidence around any suspected detection.

Distribution: National range

The species formerly occupied much of the monsoonal, near-coastal north of Australia. Its current distribution is patchy, with remaining populations concentrated in parts of the Kimberley, the Top End and several northern islands.

In Western Australia, the species persists in parts of the northern Kimberley, including the northern coastal end of the Mitchell Plateau and Mount Trafalgar in Prince Regent National Park. It has declined from lower rainfall parts of the Kimberley.

In the Northern Territory, records include the Cobourg Peninsula, Kakadu National Park, the Tiwi Islands, Groote Eylandt, Inglis Island and other islands in the Gulf of Carpentaria region. Current Northern Territory strongholds identified in the supplied material include Cobourg Peninsula, Groote Eylandt, Bathurst Island, Melville Island and Inglis Island.

In Queensland, historical and recent records include Bentinck Island in the Wellesley Group and the Gulf country. The species formerly extended towards the Camooweal area, based on fossil and sub-fossil records. Two specimens have also been collected from savannah woodland in southern Papua New Guinea.

Australian states and territories: Western Australia, Northern Territory and Queensland

Broad bioregional distribution: Northern Kimberley, Top End, Tiwi Islands, Gulf of Carpentaria islands and adjacent Gulf country

Former range: Monsoonal, near-coastal northern Australia from the northern Kimberley to around Burketown in Queensland

Estimated extent of occurrence: 120,000 km2

Estimated area of occupancy: 400 km2

Distribution: Strongholds and decline

The species remains relatively common and widespread on parts of Cobourg Peninsula and the Tiwi Islands, although monitoring indicates decline on the Tiwi Islands. Groote Eylandt and associated islands remain important populations. Kakadu National Park has experienced a severe decline, with the last known population record in 2008 and possible local extinction reported in the supplied conservation advice.

It is known from eight populations in the supplied national conservation advice. Centre Island may no longer support the species, and several former mainland and island localities have no recent records.

Known populations in the conservation advice: Eight

Last record from Bentinck Island: 1963

Last record from Centre Island: 1966

Last record from Kakadu National Park: 2008

Last record from Groote Eylandt and Inglis Island in the cited summary: 2012

Recorded decline basis for Vulnerable listing: Past, current and projected decline greater than 30 percent over 10 years, based on monitoring data and continuing threats

Distribution: Project screening

For project work, treat suitable habitat in the northern Kimberley, Top End, Tiwi Islands, Groote Eylandt, Cobourg Peninsula, Kakadu and relevant Gulf islands as potential habitat even where the species has not been recently recorded. Absence from a short survey should not be taken as proof of absence, because detection varies by season and is higher in the late dry season.

  • Check current state and territory records, Indigenous ranger knowledge, recent monitoring data and the approved survey guidelines before finalising survey effort.
  • Map habitat patches and likely movement links, with particular attention to tall eucalypt forest, large trees and areas with low recent fire impact.

Habitat: Vegetation communities

The main habitat is tall, open eucalypt forest and woodland in the monsoonal tropics. Habitat suitability is associated with taller trees, tree hollows, perennial grasses, lower recent fire impact and dry upland sites away from wet areas and watercourses.

Most records are from lowland eucalypt forests and woodlands dominated by Darwin woollybutt, Eucalyptus miniata, and Darwin stringybark, Eucalyptus tetrodonta. On the Tiwi Islands, the species is associated with tall eucalypt forest away from watercourses.

Other recorded habitats include coastal she-oak, Casuarina equisetifolia, open woodland, coastal grassland next to woodland, stunted eucalypt woodland on stony slopes and beaches on or near Cobourg Peninsula.

Primary habitat: Tall open eucalypt forest and woodland

Important tree species: Eucalyptus miniata and Eucalyptus tetrodonta

Other recorded habitats: Coastal she-oak woodland, coastal grassland, stunted eucalypt woodland, stony slopes and beaches

Habitat: Structural features

Preferred sites have taller trees, a sparse to moderate mid-storey, perennial grass understorey and available tree hollows or fallen logs. Sites with less recent severe fire are more likely to support the species. On the Tiwi Islands, occupancy was associated with canopy height, canopy cover, fire impact and distance from the nearest watercourse.

The supplied documents do not provide a reliable elevation limit. The species is associated with lowland and near-coastal monsoonal environments, with a strongly seasonal wet and dry climate.

  • Retain large rough-barked and hollow-bearing trees, fallen hollow logs, perennial grass cover and fruiting understorey shrubs.
  • Avoid treating recently burnt, heavily grazed or weed-dominated ground as equivalent to intact habitat, even where the tree canopy remains.

Habitat: Habitat condition

Recent severe or intense fire can reduce perennial grass diversity, food availability, ground cover, hollow logs and fruit-bearing shrubs. Frequent extensive fire can also simplify vegetation and increase exposure to feral cat predation.

Clearing for plantation forestry removed about 30,000 ha of preferred habitat on the Tiwi Islands. Mining, urban development and other clearing can remove habitat directly and divide remaining habitat patches.

Foraging habitat: Diet

The brush-tailed rabbit-rat feeds mainly on the ground, but climbs and forages in trees. Perennial grass seeds are the main recorded food, so retaining grass diversity and seed-producing understorey is important.

The diet consists primarily of seeds, especially seeds of perennial grasses such as cockatoo grass, Alloteropsis semialata. Other recorded foods include seeds of other grasses, fruits including fleshy fruits, foliage, grass and termites or other invertebrates.

Main food: Seeds, especially perennial grass seeds

Named food plant: Cockatoo grass, Alloteropsis semialata

Additional foods: Fruits, foliage, grass, termites and other invertebrates

Foraging habitat: Foraging sites and behaviour

Individuals primarily forage on the ground in eucalypt woodland and forest, but also climb and feed in trees. They may forage on beaches and in coastal grasslands near woodland.

Food availability can be reduced by frequent intense fire, introduced grasses and grazing. Fire can replace diverse perennial grasses with a smaller number of annual grasses, including Sorghum species, and can reduce fruit-bearing shrubs.

  • Inspect ground-layer vegetation for perennial grasses, seed heads, fruits and recent grazing or fire impacts.
  • Retain connected foraging habitat around hollow-bearing trees and logs rather than isolating shelter sites within cleared areas.

Foraging habitat: Foraging range

A study cited in the supplied material reported a mean home range of 0.79 ha. Males had larger home ranges than females, with no significant difference among study sites or between seasons in that study.

Mean home range: 0.79 ha

Sex difference: Males had larger home ranges than females in the cited study

Breeding habitat: Breeding biology

Breeding occurs through much of the wet to dry seasonal transition and dry season. Females use hollow trees and logs for shelter and rearing, so breeding habitat depends on retained shelter structures as well as food and cover.

Females can produce at least two litters during the long breeding season. Juveniles enter the population mainly during the mid to late dry season. The supplied documents do not provide a gestation period.

Breeding season: March to October

Litters: At least two sets of young may be produced

Litter size: Usually two to three young; reported range one to four

Gestation: Not stated in the supplied documents

Female sexual maturity: About 11 weeks

Life expectancy in the wild: At least two years

Generation length: 1 to 2 years

Breeding habitat: Breeding habitat features

Breeding and denning sites are mainly hollow logs and hollows in eucalypts and bloodwoods. Large rough-barked trees are particularly important because they are more likely to contain hollows. Pandanus canopies and sand-palm crowns may be used occasionally.

Suitable breeding habitat generally combines tall eucalypt forest or woodland with low recent fire impact, perennial grass food resources and ground cover. The documents do not specify a nest chamber size or a minimum hollow entrance size.

  • Retain hollow-bearing trees and fallen hollow logs within the work area and along habitat connections.
  • Protect dense ground cover and leaf litter from unnecessary removal, especially during the March to October breeding period.
  • Schedule any unavoidable disturbance outside the period when dependent young are most likely, where project constraints allow and after advice from the relevant regulator.

Sheltering habitat: Primary refuges

The species shelters during the day in tree hollows and fallen hollow logs. Shelter sites can be lost through clearing, intense fire, removal of fallen timber and deterioration of large trees.

Day refuges are mainly hollows in large rough-barked eucalypts and hollow logs on the ground. The species may occasionally shelter in Pandanus canopies, Pandanus fronds or sand-palm crowns.

The SPRAT profile reports use of trees with trunks at least 24 cm in diameter for dens. This should be treated as a useful search threshold, not as evidence that smaller trees are unsuitable.

Reported tree trunk size for dens: At least 24 cm diameter

Main shelter sites: Tree hollows and fallen hollow logs

Occasional shelter sites: Pandanus canopies or fronds and sand-palm crowns

Sheltering habitat: Site inspection

Before clearing, inspect large rough-barked trees, trees with visible hollows, fallen logs, Pandanus and sand palms. Search for active animals, fresh disturbance around hollows and other signs, but do not rely on signs alone because diagnostic tracks, scats and nests are not described in the supplied documents.

Map each shelter resource and record whether it will be retained, disturbed, felled or affected by machinery access, fire or changes to ground cover.

  • Retain hollow-bearing trees and hollow logs wherever practicable.
  • Use a qualified fauna spotter catcher during clearing in potential habitat and follow the approved species survey and handling requirements.
  • If a live animal is found, stop work in the immediate area and apply the project fauna handling and release procedure.

Sheltering habitat: Fire and cover

High intensity fire can destroy hollow logs, reduce hollow-bearing trees and remove dense ground cover used for shelter. Retaining a fine-scale mix of vegetation ages, including some long-unburnt patches, is recommended for occupied or potential habitat.

  • Keep fire records for potential habitat and occupied sites.
  • Avoid post-fire grazing or trampling until ground cover has recovered.

Threats: Clearing and fragmentation

The main project-related risks are clearing and fragmentation of habitat, severe fire, loss of hollow resources and increased predation after disturbance. Feral cats, introduced rodents, invasive grasses and grazing can add pressure to populations already reduced across much of the former range.

Clearing removes feeding habitat, hollow-bearing trees, fallen logs and ground cover. It can divide small populations and reduce connectivity, particularly in areas subject to forestry, mining, roads and other intensive land use. About 30,000 ha of preferred habitat was cleared for plantation forestry on the Tiwi Islands.

  • Avoid clearing tall eucalypt forest and woodland containing large trees, hollows, perennial grasses or fallen logs.
  • Keep habitat patches connected and avoid creating narrow isolated remnants around retained trees.
  • Include direct and indirect impacts from access tracks, compounds, drainage, lighting, noise and increased fire access in the impact assessment.

Threats: Fire

Frequent, extensive and intense fire reduces perennial grass diversity, seed availability, fruiting shrubs, dense cover and hollow logs. Late dry season fires can reduce juvenile and adult survival and may increase hunting efficiency by feral cats in recently burnt areas.

  • Use patchy, lower intensity fire regimes that retain long-unburnt habitat, dense ground cover, hollow logs and large woody debris.
  • Prevent construction activities, hot works and machinery from starting unplanned fires in potential habitat.
  • Control invasive grasses that increase fuel loads and late dry season fire intensity.

Threats: Predators and introduced species

Feral cats occur across mainland populations and on several islands. Predation is considered a likely major contributor to decline, although the conservation advice describes the direct impact as plausible rather than demonstrated for every population. Black rats may compete with native rodents and introduce disease.

Gamba grass, grader grass, mission grass and other invasive grasses can alter food resources and intensify fire. Introduced herbivores can remove ground cover by grazing and trampling, reducing shelter and potentially food availability.

  • Prevent cats and black rats from entering islands or isolated project areas through quarantine and waste controls.
  • Undertake cat control after fire where this is part of an approved management programme.
  • Minimise grazing and trampling in occupied or potential habitat, particularly after fire.

Threats: Other project risks

The supplied documents identify habitat loss, fragmentation, fire, feral cats, black rats, invasive grasses and introduced herbivores as the main documented threats. They do not provide species-specific evidence for road mortality, hydrology change or a named disease. Roads, drainage and altered water movement should still be assessed where they remove dry woodland, increase wet ground, interrupt habitat connections or increase access for predators.

  • Assess whether drainage, culverts, watercourse works or changed surface water will alter the dry upland habitat preferred by the species.
  • Record roadkill and animal interactions during construction monitoring, but do not assume that road mortality is a demonstrated primary threat for this species.
  • Refer any disease concern to the relevant wildlife authority or veterinarian because the supplied sources identify disease as a research priority rather than a quantified threat.

Survey methodology: 1. Daytime habitat and den searches

Survey this species in suitable northern Australian habitat before clearing or construction. Combine habitat assessment with repeat trapping or camera surveys, and account for seasonal differences in detection.

Search the project area and representative sampling sites during the day for tall open eucalypt forest and woodland, large rough-barked trees, tree hollows, hollow logs, dense ground cover and perennial grasses.

Outside the Cobourg Peninsula, prioritise taller open forest with less frequent or less intense fire, sparse grass cover, distance from watercourses or wet areas, and mature trees likely to contain hollows.

On the Cobourg Peninsula, also inspect coastal grasslands with scattered tall coastal she-oak, stunted eucalypt woodland on stony slopes and beaches.

Record tree diameter, hollow-bearing trees, hollow logs, fire history, grass structure, weeds, signs of cats and black rats, and any connected retained habitat.

Species weight: About 150 g

Important shelter: Tree hollows, hollow logs, and occasionally pandanus canopies

Survey area covered by the guideline method: Up to 5 ha

Survey methodology: 2. Elliott and cage trapping

Use Elliott traps and cage traps in suitable habitat, following the threatened mammal survey guideline and the project fauna survey plan.

As a species-specific reference, the Tiwi Islands baseline survey used twenty Elliott traps around the perimeter of a 50 by 50 m quadrat and one large cage trap at each corner.

Run traps for three consecutive nights where the method and risk assessment support live trapping, with traps checked early each day and animals released unmarked at the capture site unless an approved handling or marking plan applies.

Prioritise tall eucalypt forest away from wet areas, sites with perennial grasses and nearby shelter features, while avoiding locations where trapping could expose animals to heat, flooding, fire or predators.

Schedule repeat visits in the late dry season, July to September, where practicable, because detection was three times higher than in the early dry season, April to June, in the Tiwi Islands study.

Tiwi Islands baseline effort: Twenty Elliott traps, four large cage traps, three consecutive nights per site

Reference quadrat: 50 by 50 m

Higher detection period: Late dry season, July to September

Lower comparison period: Early dry season, April to June

Survey methodology: 3. Remote cameras and repeat detection surveys

Use motion-sensor cameras as a non-invasive option where live trapping is unsuitable, where access is difficult, or where repeated monitoring is needed during clearing stages.

Place cameras near likely travel routes, hollow logs, den entrances, perennial grass seed sources and other retained shelter or feeding features, without blocking animal movement.

Use repeated visits and analyse detections with methods that account for imperfect detection, because a failure to record the species does not demonstrate absence.

Keep the season, camera placement, baiting approach and deployment period consistent between monitoring rounds so that changes in records are less likely to reflect changes in detectability.

Activity pattern: Nocturnal, with activity often beginning at dusk

Detection issue: Late dry season detection was about three times higher than early dry season detection in the Tiwi Islands study

Alternative method: Motion-sensor cameras can collect observations over longer periods without repeated animal handling

Survey methodology: Minimum effort and reporting

  • Use a qualified ecologist to select survey sites and confirm that the method, effort, season and animal welfare controls meet the current Australian Government threatened mammal survey guideline.
  • For a small project area, inspect all potential habitat resources and use repeat trapping or camera visits rather than relying on a single negative survey.
  • Where trapping is used, document the number and type of traps, trap nights, checking times, weather, bait, captures, releases and any welfare incidents.
  • Record every detection with date, time, location, method, habitat description, fire history, photographs where appropriate and the identity of the observer.
  • Submit confirmed records and negative survey results where requested to the relevant state or territory wildlife database, and provide records to the project approval authority and land manager.
  • Report the result to the Commonwealth species information system or approval process where the project is subject to the EPBC Act.

Before habitat disturbance: Avoid and minimise habitat loss

Treat any suitable habitat as potential brush-tailed rabbit-rat habitat until current survey evidence supports another conclusion. The species is nationally Vulnerable and is listed as Endangered in the Northern Territory and Vulnerable in Western Australia and Queensland according to the supplied project status information and conservation material.

Redesign the project to retain tall eucalypt forest and woodland, mature rough-barked trees, hollow-bearing trees, hollow logs, perennial grass patches and dense ground cover.

Avoid clearing connected habitat patches and retain movement links between occupied or suitable areas, especially around known populations and island refuges.

Do not remove large trees or fallen logs unless the ecological assessment demonstrates that the action is unavoidable and the approval conditions address the species.

Avoid works in recently burnt areas and in habitat with severe fire impacts where animals may have lost cover, food resources and den sites.

Before habitat disturbance: Approvals and project planning

Check whether the action is likely to have a significant impact on this EPBC Act listed species and obtain an EPBC referral or approval where required.

Check Northern Territory, Queensland and Western Australian threatened species laws, permits and fauna handling requirements before survey, clearing, trapping, relocation or rehabilitation.

Prepare a species-specific fauna management plan that identifies habitat, survey results, exclusion zones, clearing limits, animal handling roles, stop-work triggers, release sites and reporting duties.

Stage clearing so that retained habitat, escape routes and relocation areas remain available while machinery is operating.

Before habitat disturbance: Timing and site preparation

Plan major clearing outside the March to October breeding period where practicable, while recognising that breeding and juvenile recruitment can extend through the dry season and that a current survey remains necessary.

Complete a pre-clearance survey before works, with extra attention to dusk and night activity, tree hollows, hollow logs and ground cover.

Mark all retained hollow-bearing trees, hollow logs, connected habitat and no-go areas before machinery arrives.

Install exclusion fencing only where it will guide animals towards retained habitat and will not trap animals, block escape routes or create predator concentration points.

Brief machinery operators and spotter catchers on the species appearance, shelter features, release procedure, exclusion zones and stop-work triggers.

Breeding period: March to October

Generation length: 1 to 2 years

Maturity: Females reach sexual maturity at about 11 weeks

During habitat disturbance: Daily controls and machinery interface

Use a controlled clearing sequence and keep a fauna spotter catcher with the work crew whenever habitat features are being disturbed. The spotter catcher must have authority to pause machinery and must work within the approved handling and welfare arrangements.

Complete a daily pre-start inspection of the work area, exclusion fencing, marked trees, logs, cameras and any known den or release locations.

Clear progressively from the least disturbed edge towards retained habitat, where safe, so animals have an escape route rather than being surrounded by machinery.

Keep machinery outside marked exclusion zones and stop the machine immediately when the spotter catcher signals a pause.

Lift or move vegetation and habitat features only after the spotter catcher has inspected the feature and confirmed that it is safe to proceed.

Do not burn, mulch or bury hollow logs, large woody debris or fallen trees until they have been inspected and the fauna management plan allows that action.

During habitat disturbance: Habitat feature handling

Inspect hollow-bearing trees, hollow logs, pandanus or palm shelter, dense ground cover and any other likely den before disturbance.

Retain hollow-bearing trees where possible, and use an approved staged-felling method if an occupied or potentially occupied tree must be removed.

Place suitable salvaged logs and woody debris in nearby retained habitat where this is safe and consistent with fire and biosecurity controls.

Do not disturb wetlands or wet drainage lines unnecessarily, because the species generally uses drier upland forest away from wet areas, although local habitat can vary.

Control introduced grasses, avoid spreading weeds through machinery and prevent post-clearing grazing from removing the ground cover used for shelter.

During habitat disturbance: Animal finds, injuries and stop-work triggers

Stop work in the immediate area if a brush-tailed rabbit-rat is found, an occupied hollow or den is suspected, an animal is injured, or the approved clearing controls fail.

Allow the animal to move into nearby retained habitat where safe, and do not chase it into open ground or towards machinery.

Only an appropriately authorised fauna handler may capture, handle, transport or release the animal, and handling must be limited to what is needed for safety, assessment and approved relocation.

Relocate a healthy animal only to suitable nearby retained habitat identified in the fauna management plan, with shelter, food resources and protection from immediate works.

Place an injured animal in a secure, quiet, temperature-appropriate container and arrange prompt assessment by a veterinarian or authorised wildlife carer.

Notify the project ecologist, environmental officer and relevant regulator of a confirmed capture, injury, death or unauthorised disturbance, as required by the approval.

During habitat disturbance: Records and incident control

  • Record the location, time, condition, sex if known, photographs, handling time, release location, person responsible and outcome for every animal encounter.
  • Record all cleared trees, hollow logs and other habitat features that were inspected, retained, relocated or destroyed.
  • Record machinery stoppages, fauna escapes, injuries, mortalities, breaches of exclusion zones, fire events, cat sightings and corrective actions.
  • Keep daily records with the project environmental file and provide the required records to the approval authority and relevant wildlife database.

After habitat disturbance: Post-clearance checks

Post-clearance work must confirm that animals were not left within the disturbance footprint and that retained habitat remains connected and usable. Continue controls until the project ecologist confirms that the site is stable.

Inspect the cleared area, retained edges, logs, tree bases, exclusion fencing and access tracks for trapped, injured or displaced animals.

Check retained hollow-bearing trees and salvaged logs after clearing, particularly where vibration, felling or fire may have affected them.

Remove temporary fencing or other barriers only after confirming that no animal is enclosed and that movement to retained habitat is safe.

Repeat targeted camera or trapping surveys where the pre-clearance survey recorded the species, suitable habitat was disturbed, or approval conditions require post-clearance monitoring.

After habitat disturbance: Monitoring and reporting

Use the same survey season, sites and detection method where possible so that post-work results can be compared with pre-work records.

Account for imperfect detection and seasonal detectability when interpreting a non-detection.

Monitor retained habitat for fire impact, perennial grass cover, hollow logs, weeds, introduced herbivores, black rats and feral cats.

Report survey results, incidents, mortalities, habitat loss, rehabilitation progress and corrective actions to the project approval authority and relevant state or territory database.

After habitat disturbance: Offsets and residual impacts

Assess residual habitat loss or degradation against the EPBC approval, state approval and any offset conditions after avoidance and mitigation measures have been applied.

Do not treat rehabilitation or an offset as a substitute for retaining occupied habitat, hollow-bearing trees, logs and connected habitat within the project area.

Record the area and condition of habitat affected and the location, condition and management arrangements for any approved offset or conservation area.

Rehabilitation actions: Restore shelter and food resources

Rehabilitation should restore the shelter, food and fire conditions used by brush-tailed rabbit-rats. Set measurable targets for habitat structure and threats, then monitor whether the species returns or continues to use the area.

Re-establish locally appropriate eucalypt woodland or open forest using species and provenances suited to the site and project region.

Restore perennial grass cover and understorey diversity that can provide grass seed, fruit and ground shelter, rather than creating a dense stand of annual invasive grasses.

Retain or reinstate suitable hollow logs and large woody debris where this does not create a fire, safety or biosecurity hazard.

Protect mature retained trees and plan for replacement hollow-bearing trees because the species uses large rough-barked trees and tree hollows for daytime shelter.

Use artificial nest boxes only where a site-specific design and monitoring plan supports them, because the conservation advice identifies nest boxes as a research and management priority rather than a guaranteed substitute for natural hollows.

Rehabilitation actions: Control fire, weeds, grazing and predators

Manage fire to reduce frequent, extensive and intense burns, retain a fine-scale mix of vegetation ages, and maintain some areas of long-unburnt habitat.

Retain dense ground cover and leaf litter during prescribed burning, and protect hollow logs, large woody debris and hollow-bearing trees from high intensity fire.

Control gamba grass, grader grass, mission grass, annual Sorghum dominance and other invasive grasses where they increase late dry season fire intensity or reduce food availability.

Exclude or manage livestock and feral herbivores until vegetation has recovered, because grazing and trampling can remove shelter and food resources.

Implement approved feral cat control and black rat control, and maintain island quarantine where relevant to prevent new predators or competitors reaching isolated populations.

Important fire target: Fewer late dry season burns, fewer areas burnt annually and more patchy fire effects

Post-fire protection: Retain dense ground cover and leaf litter, hollow logs and large woody debris

Rehabilitation actions: Monitoring and success measures

Monitor planted vegetation, perennial grass cover, hollow and log availability, invasive grass cover, fire history, grazing pressure and feral predator activity.

Use repeat camera or trapping surveys in late dry season, July to September, where practicable, and use repeat visits rather than a single survey.

Measure success by increasing or maintained suitable habitat, surviving mature and recruiting trees, retained shelter features, reduced severe fire impacts, controlled invasive grasses and confirmed use by brush-tailed rabbit-rats or other agreed ecological indicators.

Review management if monitoring shows declining occupancy, increasing severe fire impact, loss of ground cover, rising cat activity or failure of planted vegetation.

Sources