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SHORT COMMUNICATION Response of Seedling Communities to Mammalian Pest Eradication on Ulva Island, Rakiura National Park, New Zealand

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SHORT COMMUNICATION Response of Seedling Communities to Mammalian Pest Eradication on Ulva Island, Rakiura National Park, New Zealand CLAYTONAvailable on-line ET AL.: at: http://www.newzealandecology.org/nzje/ SEEDLING REGENERATION AFTER PEST ERADICATION 103 SHORT COMMUNICATION Response of seedling communities to mammalian pest eradication on Ulva Island, Rakiura National Park, New Zealand Richard I. Clayton1,2*, Deborah J. Wilson3, Katharine J. M. Dickinson1 and Carol J. West4 1Botany Department, University of Otago, PO Box 56, Dunedin 9054, New Zealand 2Manaaki Whenua Landcare Research, PO Box 40, Lincoln 7640, New Zealand 3Manaaki Whenua Landcare Research, Private Bag 1930, Dunedin 9054, New Zealand 4Department of Conservation, PO Box 10420, Wellington 6143, New Zealand *Author for correspondence (Email: [email protected]) Published on-line: 4 February 2008 ___________________________________________________________________________________________________________________________________ Abstract: Norway rats (Rattus norvegicus) were eradicated from Ulva Island, Rakiura National Park, in 1996. The aim of our work was to determine if seedlings and saplings increased in density and/or species richness following this eradication. In 2003, we took advantage of eight permanent plots (5 × 5 m) that had been established on Ulva Island in 1991, by counting seedlings and saplings of woody species, including tree ferns. Over this period, total numbers of woody seedlings (< 30 cm tall), and saplings (30 cm – 2 m tall) did not increase significantly (P > 0.05). However, seedlings of two species, Dicksonia squarrosa and Pittosporum colensoi, and saplings of one species, Coprosma colensoi, did increase in numbers significantly. Little change in the species richness of seedlings or saplings was recorded. The removal of Norway rats may have been partly responsible for the recorded increases in density, though the eradication of white-tailed deer (Odocoileus virginianus borealis) from Ulva Island approximately two decades _______________________________________________________________________________________________________________________________prior to this work is an important confounding factor. ____ Keywords: forest regeneration; herbivory; Odocoileus virginianus borealis; Rattus norvegicus; seedling establishment; seedling recruitment; seed predation; Stewart Island Introduction 2003). This work has been done to provide refugia for native birds, invertebrates, and herpetofauna, at the same Invasive species are an increasing problem worldwide, time as allowing plant communities to recover from the with oceanic islands suggested by some to be more influence of introduced browsing mammals (see Atkinson vulnerable than continental regions (Veitch & Clout 2002). 1973). Although the conservation benefits from these Establishing the effects of such invasions is often hindered programmes are often very clear for fauna (e.g. Veitch by unavailability of pre-invasion data. Eradication methods & Clout 2002), fewer studies have measured changes to used for invasive mammalian species on oceanic and plant communities on islands following eradication of offshore islands are increasing in sophistication as well as introduced animals, particularly rats (Rattus spp.). As well size of area being successfully tackled (Towns & Broome as eating a variety of seeds and fruits, rats eat seedlings, 2003). Following eradication the ecosystem will recover fleshy roots, leaf laminae and petioles, flowers, apical buds to some degree, but it is questionable as to how similar and bark (Campbell 1978). Also, by consuming native that state will be to the pre-invasion situation (Caughley herbivores such as invertebrates, reptiles and birds, rats 1989). Nevertheless, post-removal measurements of key may indirectly affect vegetation structure and composition elements of the ecosystem are crucial to understanding the by modifying plant–herbivore interactions (Clout & Hay recovery trajectory of a particular habitat especially when 1989; King 2005). considering reintroductions of native species. Several studies do show changes in seedling New Zealand is regarded by many as a world communities after eradication of introduced mammals on leader in eradication technologies and the New Zealand islands. Five years after Norway rats (Rattus norvegicus) Department of Conservation (DOC) has completed a were removed from Breaksea Island in Fiordland, Ralph series of eradication programmes on islands around Allen and colleagues (1994) found an increase in numbers New Zealand over the last c. 40 years (Towns & Broome of seedlings (< 30 cm tall) of 10 out of 24 common woody New Zealand Journal of Ecology (2008) 32(1): 103-107 ©New Zealand Ecological Society 104 NEW ZEALAND JOURNAL OF ECOLOGY, VOL. 32, NO. 1, 2008 plant species. Following the eradication of brushtail Woody plants that were rooted in the plots and had true possums (Trichosurus vulpecula), Norway rats (Rattus leaves (i.e. non-cotyledonous seedlings) were counted in norvegicus) and Pacific rats (R. exulans) from Kapiti Island, two height categories: < 30 cm tall (seedlings) and 30 cm seedlings of four out of the five plant species expected – 2 m tall (saplings). The tree ferns Dicksonia squarrosa to increase in density (based on known palatability) did and Cyathea smithii were counted in the same fashion so over a 4-year period (Campbell 2002). However, (as ‘seedlings’ and ‘saplings’), with height recorded to Campbell (2002) concluded that pest eradication could the base of the crown. not be separated from other factors contributing to the Numbers of seedlings and saplings of all species apparent recovery of seedlings of many species. (combined and separate) were compared before and after Ulva Island is the largest (226 ha) of the approximately rat eradication (i.e. 1991 and 2003 data) with two-tailed, 20 islands in Paterson Inlet, Stewart Island (46º55´ S, paired t-tests, with a significance level of 0.05. Species 168º08´ E). The island was declared a reserve for the richness in the seedling and sapling height classes, defined preservation of nature, game and flora in 1899 and is as the number of species present per plot, was compared now managed as an ‘open sanctuary’ and part of Rakiura before and after rat eradication in the same way. National Park (DOC 2004). The two remaining species of exotic vertebrates (i.e. white-tailed deer, Odocoileus virginianus borealis and Norway rats) were eradicated Results from Ulva Island in 1976 and 1996 respectively. Rance (1991 – DOC Invercargill unpubl. report) established eight Seedlings permanent vegetation plots on Ulva Island in 1991 in order When counts of seedlings (< 30 cm) of all woody and tree to study vegetation changes after rat eradication. Changes fern species were combined, there were on average 9.1 in seedling communities were minimal in the subsequent seedlings m–² in 1991 and 11.0 seedlings m–² in 2003 (Table few years (Rance 1994 – DOC Invercargill unpubl. report). 1). This increase was not statistically significant (t7 = 0.94, We revisited these plots in 2003 to determine whether the P = 0.38). However, increases in numbers of seedlings density of seedlings on Ulva Island had changed since plots were statistically significant in two species, Dicksonia were established there 12 years previously. We expected squarrosa (t7 = 2.56, P = 0.038) and Pittosporum colensoi that the density of seedlings of some plant species known (t7 = 4.58, P = 0.003). The number of Myrsine divaricata to be palatable to rats would have increased. seedlings decreased significantly (t7 = 2.7, P = 0.03). Two species not present in 1991 appeared in 2003 (Coprosma grandifolia and Metrosideros umbellata). Neither was Methods present in large numbers, although 18 small seedlings of Study site C. grandifolia were found on one plot. An average of 14.6 woody and tree fern species per Meurk and Wilson (1989) described the vegetation of Ulva plot was recorded in the seedling height class in 1991 Island and identified two major forest types (nomenclature and 15.5 species per plot in 2003. This difference was not follows Allan Herbarium (2000)): (1) rimu–rātā–kāmahi statistically significant t( = 2.0, P = 0.087). forest (Dacrydium cupressinum, Metrosideros umbellata 7 and Weinmannia racemosa) covering the majority of Saplings the island (86%); and (2) coastal ‘muttonbird scrub’– leatherwood–inaka low forest (Brachyglottis rotundifolia, When all species of saplings (30 cm – 2 m tall) were combined, there were on average 1.29 saplings m–² Olearia colensoi and Dracophyllum longifolium) – dominating most of the remaining area (12%). present in 1991 and 1.96 saplings m ² in 2003 (t7 = 2.32, P = 0.058) (Table 1). Of 18 species of saplings that were Field data collection present in both 1991 and 2003, only Coprosma colensoi increased significantly in density during this period (P × Eight plots (5 5 m) were established at random points < 0.01). Pseudopanax colensoi was present in 2003 but along a public track network at the western end of Ulva not in 1991, while Pittosporum colensoi had disappeared Island (Rance 1991 unpubl.). These plots were all placed between the years. in the rimu–rātā–kāmahi forest; the coastal vegetation type An average of 7.8 species per plot were present in was excluded as it had little plant species diversity and the the sapling height class in 1991 and this number did not major plant species present there were not expected to be change significantly in 2003 with 8.1 species per plot (t7 influenced by rats. Vegetation on the plots was measured in = 0.48, P = 0.32). 1991 and the seedling tiers (< 30
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