|Scientific Name:||Panulirus marginatus|
|Species Authority:||(Quoy & Gaimard, 1825)|
Palinurus marginatus Quoy & Gaimard, 1825
|Red List Category & Criteria:||Data Deficient ver 3.1|
|Assessor/s:||Butler, M., Cockcroft, A. & MacDiarmid, A.|
|Reviewer/s:||Collen, B., Livingstone, S. & Richman, N.|
|Contributor/s:||Batchelor, A., De Silva, R., Dyer, E., Kasthala, G., Lutz, M.L., McGuinness, S., Milligan, H.T., Soulsby, A.-M. & Whitton, F.|
Panulirus marginatus has been assessed as Data Deficient. This species has, in the past, experienced threat from over-harvesting throughout its range, where declines of over 80% in catch per unit effort data have been recorded (mid 1970s to 1999) from the NWHI fishery. This would have made the species eligible for Endangered classification (A1abd). However, since 2000 harvesting of this species has ceased as the fishery was closed and a marine protected area designated, with ongoing management and monitoring by the National Marine Fisheries Service, Honolulu Laboratory. Currently there are no accurate abundance data for this species and therefore the population trend since 2000 is unknown. Once this data is available a more accurate assessment of this species can be carried out, which may result in a Least Concern classification.
|Range Description:||This species is only known from Hawaii, including the Northwest Hawaiian Islands (Holthuis 1991).|
Native:United States (Hawaiian Is.)
|FAO Marine Fishing Areas:||
Pacific – eastern central
|Range Map:||Click here to open the map viewer and explore range.|
In the past there were striking contrasts in abundance between different Hawaiian islands; e.g., Maro Reef adjusted landings were more than 300 times those from Lisianski Island, despite both being of similar size and depth and only 330 km apart (Parrish and Polovina 1994). This suggests a highly heterogeneous population structure for this species, determined partly by habitat topography. Generally catches were lowest on banks with summits deeper than 30 m (Parrish and Polovina 1994).
Fivefold declines in CPUE were observed at Necker Bank through the late 1980s and 1990s, both for commercial catch-per-trap haul and in research landings of all size groups (including juveniles) (DeMartini et al. 2003). This occurred simultaneously with increasing size-specific fecundity, a compensatory response consistent with decreases in median body size at sexual maturity (DeMartini et al. 2003). The result of this was that egg production was dominated by smaller females, partly due to the poor representation of large females in the population (DeMartini et al. 2003).
As landings of all species were showing declines, in 2000 the NWHI fishery was closed as a precautionary measure due to increasing uncertainty of the population models used to assess stock status. Later on that year the Northwestern Hawaiian Islands Coral Reef Ecosystem Reserve was established which may prohibit commercial lobster fishing in the NWHI indefinitely (DiNardo and Moffitt 2007). For catch data from the NWHI fishery whilst it was in operation see DiNardo and Moffitt (2007).
CPUE data for this species from 1983 (mature lobster landings/trap hauls; data from DiNardo and Marshall 2001):
1983 - 2.47; 1984 - 1.83; 1985 - 0.96; 1986 - 0.65; 1987 - 0.49; 1988 - 1.06; 1989 - 0.88; 1990 - 0.50; 1991 - 0.44; 1992 - 0.36; 1993 - closed; 1994 - 0.51; 1995 - 0.55 (experimental fishery); 1996 - 1.07; 1997 - 0.79; 1998 - 0.40; 1999 - 0.31; 2000 - fishery closed.
This suggests an approximately 87 % decline in CPUE between 1983 and 1999 across the NWHI fishery. Surveys at
|Habitat and Ecology:||
"Shallow water" under rocks and crevices on rocky bottoms, according to Holthuis (1991), although it has been recorded as deep as 143 m. This species is nocturnal. Although longevity and age at maturity are not known for this species, inference from similar species (e.g., the Caribbean Spiny Lobster Panulirus argus) suggests a longevity of up to 20 years and sexual maturity at around four years.
Changes in recruitment levels for this species are related to Pacific sea levels four years earlier (Polovina and Mitchum 1992).
|Major Threat(s):||The NWHI fishery has been closed since 2000 and a protected area now covers this species' distribution, therefore there are no current threats impacting this species. Previous declines in catch per unit effort (CPUE) of over 80 % have been recorded for this species between 1983 and 1999 (DiNardo and Marshall 2001), which had knock-on effects in relation to fecundity (DeMartini et al. 2003), but there is no information to indicate this has had a long-term impact on the species.|
The fishery for this species was closed in 2000, upon the creation of the Northwest Hawaiian Islands Coral Reef Ecosystem Reserve. Were it to re-open in the future - which is conditional on the recovery of lobster populations - several management practices should be put in place. The first of these is a minimum size limit, as past "retain all" policies, introduced in 1996 to reduce discard, were detrimental to populations of this species. DeMartini et al. (2003) recommend a larger limit than the previous 50 mm used until 1996, in order to protect smaller females which are now the primary egg-producers. This may help to counter recruitment overfishing (DeMartini et al. 2003).
Necker Island is an important focus for stock recovery efforts, as it is thought to be an important source of larvae for the rest of the fishery. This tallies with a novel metapopulation-based approach to the fishery (DiNardo and Marshall 2001), based on the premise that "overfishing or depletion of local populations could
result in catastrophic impacts to the population as a whole (e.g. a reduction in average recruitment or recruitment failure), particularly when a large number of local populations or the most productive populations are overfished". This calls for the collection of higher-quality population data, which is being addressed by the National Marine Fisheries Service, Honolulu Laboratory (NMFS-HL) in the form of a research and monitoring plan.
DeMartini, E.E., DiNardo, G.T. and Williams, H.A. 2003. Temporal changes in population density, fecundity, and egg size of the Hawaiian spiny lobster (Panulirus marginatus) at Necker Bank, Northwestern Hawaiian Islands. Fishery Bulletin 101: 22-31.
DiNardo, G.T. and Marshall, R. 2001. Status of lobster stocks in the Northwestern Hawaiian Islands, 1998 - 2000. Southwest Fisheries Science Center Administrative Report H-01-04, Honolulu, Hawaii.
DiNardo, G.T. and Moffitt, R.B. 2007. The Northwestern Hawaiian Islands Lobster Fishery: A Targeted Slipper Lobster Fishery. In: Lavalli, K.L. and Spanier, E (eds), The Biology and Fisheries of the Slipper Lobster, pp. 243-262. CRC Press, Taylor and Francis Group, Florida.
Holthuis, L.B. 1991. Marine lobsters of the world. An annotated and illustrated catalogue of species of interest to fisheries known to date. FAO species catalogue 13(125). FAO, Rome.
IUCN. 2011. IUCN Red List of Threatened Species (ver. 2011.1). Available at: http://www.iucnredlist.org. (Accessed: 16 June 2011).
Parrish, F.A. and Polovina, J.J. 1994. Habitat Thresholds and Bottlenecks in Production of the Spiny Lobster (Panulirus Marginatus) in the Northwestern Hawaiian Islands. Bulletin of Marine Science 54(1): 151-163.
Polovina, J.J. 1989. Density dependence in spiny lobster, Panulirus marginatus, in the Northwestern Hawaiian Islands. Canadian Journal of Fisheries and Aquatic Sciences 46: 660-665.
Polovina, J.J. and Mitchum, G.T. 1992. Variability in spiny lobster Panulirus marginatus recruitment and sea level in the northwestern Hawaiian Islands. Fishery Bulletin 90(3): 483-493.
|Citation:||Butler, M., Cockcroft, A. & MacDiarmid, A. 2011. Panulirus marginatus. In: IUCN 2013. IUCN Red List of Threatened Species. Version 2013.2. <www.iucnredlist.org>. Downloaded on 18 April 2014.|
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