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Banksia Brownii (Feather Leaved Banksia), Proteaceae

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Banksia Brownii (Feather Leaved Banksia), Proteaceae Threatened plant translocation case study: Banksia brownii (Feather Leaved Banksia), Proteaceae DAVE COATES*, REBECCA DILLON AND SARAH BARRETT Department of Biodiversity, Conservation and Attractions, Western Australia. *Email: [email protected] The Species therefore considered to be discrete conservation units • Long-lived non-lignotuberous shrub or small tree. important for the management and recovery of B. brownii (Coates et al. 2015). • Endemic to Western Australia. Banksia brownii has a long juvenile period, requiring a • 18 extant (surviving; in existence) natural populations, fire-free period of at least 15 years to reach maturity and 10 with less than 100 plants, which occur over a 90 km accumulate an adequate seed bank, making it vulnerable range around Albany (to the north and east). to short fire intervals. Two fires in close succession, • Three biogeographically and genetically distinct in 1991 and 2000, in the eastern Stirling Range had a population groups have been identified and are significant impact with no or minimal regeneration of considered to be separate conservation units for several populations (Gilfillan and Barrett 2008; Barrett and management and recovery. Yates 2015). Threatening Processes The species was declared as Rare Flora under the Western Australian Wildlife Conservation Act in November 1980 and • Phytophthora dieback. is currently ranked as Critically Endangered. It is also listed • Inappropriate fire regimes (i.e., too frequent fire and as Endangered under the Commonwealth Environment lack of fire). Protection and Biodiversity Conservation Act 1999. Deciding to translocate The establishment of three translocated populations in new secure and disease-free locations was considered to Banksia brownii is highly susceptible to the introduced be one of the most effective actions to initiate successful soil-borne pathogen Phytophthora cinnamomi, which recovery of the species is considered to be the greatest threat to this species’ ongoing persistence (Shearer et al. 2013). Of 30 known Aim of the translocation populations, 12 are now presumed extinct due to Phytophthora dieback, 10 have less than 100 plants; of The aim of the translocation was to successfully establish these, eight have less than 10 mature plants remaining three viable populations covering the three genetically with the decline in numbers largely due to Phytophthora and biogeographically distinct conservation units dieback. Genetic diversity studies based on material from recognised in B. brownii (Figure 1). For each population extinct (ex situ seed collections) and extant populations the objective was to establish at least 200 mature indicate that some 38% of total genetic diversity, based adult plants in secure sites where threats, in particular on contributions of within population variation and Phytophthora dieback, were absent. An initial assessment differentiation, has been lost from B. brownii due to of viability would be based on the production of viable Phytophthora dieback (Coates et al. 2015). seed and recruitment over subsequent generations. Population genetic studies (using microsatellite Translocation working group and genotyping) have demonstrated significant levels key stakeholders of differentiation among populations of B. brownii corresponding to the three geographically and • Department of Biodiversity, Conservation and historically isolated disjunct population groups; Stirling Attractions (DBCA), Western Australia – to oversee Range National Park (SRNP), Milbrook-Waychinicup and development and implementation of translocation Vancouver Peninsula. These isolated population groups and ongoing monitoring and maintenance of also display ecological differences, and they occupy translocation sites. contrasting habitats in terms of substrate, associated vegetation and climate. The three population groups are Australasian Plant Conservation | Vol 27 No 1 June – August 2018 3 • Department of Biodiversity, Conservation and populations in the SRNP. Translocations of several other Attractions, Western Australia (Botanic Gardens and Critically Endangered species susceptible to P. cinnamomi Parks Authority) – propagation of seedlings. and endemic to the SRNP are also located on this site • Albany District Threatened Flora Recovery Team – to Site 2 was located within remnant vegetation similar oversee implementation of Interim Recovery Plan for to the species’ natural habitat on a Eucalyptus globulus the species, including the translocations. (bluegum) plantation managed by the then Integrated Tree Cropping Pty Ltd (ITC), now Australian Bluegum Biology and Ecology Plantations (ABP). Significant areas of native vegetation • Primarily bird- and mammal-pollinated but insect within the plantation remain undisturbed and in good pollination is also likely. condition. The selected site was located within remnant vegetation on a high-point of a lateritic ridge and is • Seeds are usually retained in the infructescences and remain viable for at least 30 years. They are released Phytophthora-free. after fire. Site 3 was located on Snake Hill in Torndirrup National • Recruitment is primarily confined to post-fire period. Park, within 4.3 km of the natural population of the Vancouver Peninsular population of B. brownii • Population genetic studies have demonstrated in Phytophthora-free habitat similar to that of the significant genetic structure within B. brownii natural population. corresponding to the three geographically disjunct population groups. Higher levels of genetic diversity Translocation proposal in the Stirling Range populations indicate larger and more stable population sizes over longer timeframes. Two Translocation Proposals were developed; one • The historically isolated population groups display for the Stirling Range and Milbrook – Waychinincup ecological differences occupying contrasting populations (Barrett and Jackson 2006) and one for the habitats in terms of substrate, associated vegetation Vancouver Peninsula populations (Barrett et al. 2008). and climate. These were developed using a template provided by the then Department of Environment and Conservation • Climate is Mediterranean with hot dry summers and (DEC), now DBCA, to guide and provide justification cool wet winters. for the translocation. The Proposals were submitted to DEC where they were assessed by two independent Site selection reviewers as to whether they met DEC’s policy on plant Given the recognition of three genetically and translocations, before being given approval for the biogeographically distinct conservation units within translocation process to commence. B. brownii (Figure 1), three separate translocations representing each conservation unit were considered Pre-translocation preparation, design, optimal, to maximise the conservation of genetic diversity implementation and ongoing maintenance within the species. The three translocated populations Each translocation was established with seedlings grown would therefore represent the Stirling Range populations from seed collected from natural populations which has (Site 1), the Milbrook- Waychnincup populations (Site 2) been stored in the DBCA Threatened Flora Seed Centre and the Vancouver Peninsula population (Site 3). covering the three genetically and biogeographically A desktop GIS-based search was made of conservation distinct regions. Two translocation sites (Sites 1 and 2) reserves in the vicinity of the known B. brownii were established with a proportion of seed collected from populations in each of the three regions to locate suitable now extinct populations. sites. Search criteria included similar soil and vegetation At each site, seedlings were established during winter to the natural populations, secure tenure, absence and planted roughly in rows, amongst the existing of threats and proximity to the known populations. vegetation, with progeny from the same maternal plant Infestation with Phytophthora dieback was the most kept separate. Each plant was permanently tagged for significant challenge as many otherwise suitable sites monitoring purposes and caged to prevent grazing by were infested. An additional factor in site selection was rabbits and kangaroos. An automatic solar-powered the risk of a major disturbance event (such as fire) and irrigation system was established in spring to water plants whether measures could be put in place to ensure the during the first and second summer. As a precautionary risk of an event affecting the translocated populations measure to protect the translocation sites from disease, was low. all equipment used during planting and monitoring As it was not possible to locate a translocation site was maintained under strict disease hygiene, with within areas of suitable habitat in the SRNP which access restricted to dry soil conditions. Vehicles and was not affected by Phytophthora dieback, Site 1 was footwear were cleaned of soil before entering the natural located north of the Porongurup Range in revegetated populations and translocation sites. woodland on private property within 26 km of B. brownii 4 Australasian Plant Conservation | Vol 27 No 1 June – August 2018 Stirling Range n n n n n T1 Millbrook - Waychinnicup T2 n n n n n Albany n 0 10 T3 KILOMETRES Vancouver Peninsula Figure 1. Mean q-matrix membership proportions of Banksia brownii populations (pie charts) when K=3 from a STRUCTURE analysis (see Coates et al. 2015). The size of pie charts is relative to the level of genetic diversity. Extant populations ■. Germinated
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