|Scientific Name:||Naso unicornis|
|Species Authority:||(Forsskål, 1775)|
Acanthurus unicornis (Forsskål, 1775)
Chaetodon unicornis Forsskål, 1775
|Taxonomic Notes:||Naso unicornis is widespread throughout the Indo-Pacific region, genetic studies conducted by Horne et al. (2008) did not find any evidence of geographic population structure even at the largest spatial scales.|
|Red List Category & Criteria:||Least Concern ver 3.1|
|Assessor(s):||McIlwain, J., Choat, J.H., Abesamis, R., Clements, K.D., Myers, R., Nanola, C., Rocha, L.A., Russell, B. & Stockwell, B.|
|Reviewer(s):||Edgar, G. & Kulbicki, M.|
Naso unicornis is widespread in the Indo-Pacific. It is common and can achieve high abundances in parts of its range. It is a targeted fish species in most of its distribution. There have been signs of catch declines - however, with no corresponding effort data population declines cannot be easily quantified. There is no clear trend of population declines. It is found in a number of well-managed protected areas and has shown positive responses to protection. It is therefore listed as Least Concern. We recommend continued monitoring of the harvest levels and population status of this species.
|Range Description:||Naso unicornis is found from the Red Sea and East Africa to the Hawaiian Islands and Pitcairn Islands, northwards to southern Japan, southwards to New South Wales, Lore Howe Island, and Norfolk Island. It is also reported from Western Australia. It was recently recorded from Easter Island.|
Native:American Samoa (American Samoa); Australia; British Indian Ocean Territory; Brunei Darussalam; Cambodia; Chile (Easter Is.); China; Christmas Island; Cocos (Keeling) Islands; Comoros; Cook Islands; Disputed Territory (Paracel Is., Spratly Is.); Djibouti; Egypt; Eritrea; Fiji; French Polynesia; French Southern Territories (Mozambique Channel Is.); Guam; India (Andaman Is., Nicobar Is.); Indonesia; Israel; Japan; Jordan; Kenya; Kiribati (Gilbert Is., Kiribati Line Is., Phoenix Is.); Madagascar; Malaysia; Maldives; Marshall Islands; Mauritius; Mayotte; Micronesia, Federated States of ; Mozambique; Myanmar; Nauru; New Caledonia; New Zealand; Niue; Norfolk Island; Northern Mariana Islands; Oman; Palau; Papua New Guinea; Philippines; Pitcairn; Réunion; Samoa; Saudi Arabia; Seychelles; Singapore; Solomon Islands; Somalia; South Africa; Sri Lanka; Sudan; Taiwan, Province of China; Tanzania, United Republic of; Thailand; Timor-Leste; Tokelau; Tonga; Tuvalu; United States (Hawaiian Is.); United States Minor Outlying Islands (Howland-Baker Is., Johnston I., Midway Is., US Line Is., Wake Is.); Vanuatu; Viet Nam; Wallis and Futuna; Yemen
|FAO Marine Fishing Areas:||
Indian Ocean – western; Indian Ocean – eastern; Pacific – northwest; Pacific – southwest; Pacific – western central; Pacific – southeast; Pacific – eastern central
|Lower depth limit (metres):||80|
|Range Map:||Click here to open the map viewer and explore range.|
FAO capture production for Naso unicornis from Saudi Arabia recorded 126 tonnes in 2000 to 191 tonnes in 2001, catch decreased from 2002-2004 with 133, 145 and 113 tonnes respectively; it has increased since then with 195 tonnes recorded in 2007. There are no capture production records prior to 2000. Density of N. unicornis was 3-10 times greater after marine reserves around five islands in New Caledonia were protected from fishing for 4 yrs (Wantiez et al. 1997). In the central Philippines, there were two orders of magnitude difference in mean biomass between fished areas and marine reserves (0.5 to 11 years protection) (Stockwell et al. 2009).
In Saipan, this species was the most abundant fish in the surveys with landings accounting for 14% of the total fish landings, and 50% of the acanthurids landings (P. Houk unpublished data). Census data from seven sites around Saipan using timed visual surveys on SCUBA revealed N. unicornis was extremely rare at 0.05% of the total acanthurid abundance. A similar result was found on Guam, where this species made up 17% of the acanthurid fishery but was rarely recorded during visual surveys. In these and other locations where spearfishing is the primary fishing method, daytime visual surveys using fixed length transects might be inappropriate.
In the Federal States of Micronesia, particularly Yap, N. unicornis accounts for approximately 12% of the total catch landed from the sheltered coastal reefs and lagoons at two sites Yyin and Riiken (Kronen et al. 2006). On Pohnpei, this species is the second most abundant acanthurid in the fishery (26% of all acanthurids) (Rhodes et al. 2008). Analysis of longterm fishery data (1984-2007) from Guam reveal no decline in mean individual weight for this species (Division of Aquatic and Wildlife Resources unpub. data). An average of 7,700 kg/year is landed in Hawaii (Division of Aquatic Resources unpub. data). This species is collected as an aquarium fish in West Hawaii. The total number of individuals caught from FY 2005-2009 was 24 with a total value of $68 (Walsh et al. 2010).
This species was recorded as occasional in terms of relative abundance in Palawan Province, Philippines and the northern Bismarck Sea, Papua New Guinea (Werner and Allen 2000, Palawan Council for Sustainable Develeopment, Allen 2009). It is moderately common in Milne Bay Province, Papua New Guinea and in Raja Ampat, Indonesia (Allen 2003, 2003b). In Moorea, French Polynesia, SPOT satellite images allowed estimation of the surface area of fringing reef (1,076 ha), barrier reef (3,788 ha) and outer slop (493 ha). A total of 21,346 individuals were recorded in this area in fish visual surveys conducted from 1990-1993 (Lecchini et al. 2006).
In the Nabq Managed Resource Protected Area, South Sinai, Egyptian Red Sea, mean abundance of this species was higher in the fished areas than in the no-take zones across 3 and 10 m depths. This can be attributed to a result of reduced predation or competition (Ashworth and Ormond 2005). In a stock assessment conducted at the northern province of New Caledonia by Letourneur et al. (2000), density and biomass was higher in the north zone and on barrier reefs (17.5 g m-2 and 129 ×10-4 individuals m-2) compared to other areas surveyed and other reef types.
|Current Population Trend:||Unknown|
|Habitat and Ecology:||
Naso unicornis is found in inshore coral reefs but will enter shallow water (Randall 2001a). It feeds on macroscopic algae, mainly larger brown algae (Turbinaria and Dictyota) (Choat et al. 2002, 2004). It undergoes ontogenetic habitat shifts from shallow, sheltered areas of the reef to deeper, more exposed habitats (Meyer and Holland 2005), juveniles move from shallow reef flats to the reef crest at approximately 12 cm (J. McIlwain pers. obv.). It typically occurs in small groups, migrates around the outer reef edge, and spawns around both new and full moons (Johannes 1981, Arai and Sato 2007).
Home range estimates of N. unicornis from a study on Guam ranged from 51 m2 to 100,045 m2 (mean = 30,227 m2) almost ten times that for the same species in Hawaii (mean = 3,172 m2) (Meyer et al. 2000, Marshall unpub thesis). These differences may reflect differences in methods with the former employing a remote array deployed over five months and the latter a hand-held hydrophone used to track individual fish for a maximum of 21 days. There was a strong ontogenetic shift in both home range size and habitat preference at both locations. On Guam, large individuals (26 cm) use not only the shallow reef flats but range over deeper, more exposed habitat on the reef slope
The sexes are separate and there is evidence of sexual dimorphism in the caudal knives which are relatively larger in males (J.H. Choat pers. comm. 2010). Size at first reproduction (L50) for females collected from the fishery in Guam (2008-2009) was 328 mm (J. McIlwain unpub.data). In Hawaii the L50 for reproductive females collected only in June was 378 mm (Eble et al. unpub report). The smallest females with vitellogenic or hydrated oocytes were 286 mm and 342 mm respectively. The L50 for males from Hawaii was 286 mm, and the smallest male with sperm present was 266 mm. For the Hawaiian fishery, two thirds of females enter the fishery before maturation (Eble et al. 2009). In Guam, mature or spent females were only recorded from August to October during 2008. This species exhibits high recruitment rates (J. McIlwain unpub. data).
In Hawaii, mean age from a sample of 197 fish was 12.8 yrs (range of 1-58 yrs). They found no evidence of sexual dimorphism in size or differences in growth among locations. Males reached age at first maturity at 4.5 yrs, 7.5 years for females at 37.8 cm (TL) (J. Eble unpub. report). In the Great Barrier Reef females reach first maturity at four years 30-35 cm (TL) (J.H. Choat pers comm. 2010).
It was observed to form spawning aggregations on the Great Barrier Reef (Johannes 1981, Squire and Samoilys unpub.). The large pelagic larvae persist in the pelagic environment for approximately 90 days (B.Victor pers comm. in Horne et al. 2008).
The number of sagital increments in a study done by Choat and Axe (1996) suggest that members of the genus Naso attain the same maximum ages as the other Acanthurids, in excess of 20 years for this species. Maximum age was 30 years in the Great Barrier Reef (Choat and Robertson 2002a), 58 years in Hawaii (Eble 2009).
A study by Meyer and Holland (2005) revealed the first nocturnal movements in surgeonfishes. Naso unicornis moved up to 170 m on nights where moonlight was completely absent. The study also showed that this species was site-attached to home ranges situated within the boundaries of the study area and their movements were aligned with topographical features.
|Use and Trade:||Naso unicornis is an important food fish and is targeted by fishers. In Atafu, large netting drives with seines are occasionally employed as a community fishing actvity involving over 100 people. This species is one of the main species captured by this netting method (Ono and Addison 2009). It is also an occasional component of the aquarium trade (Global Marine Aquarium Database accessed 19 March 2010).|
Naso unicornis is a targeted food fish. There have been significant reductions in biomass in parts of its range.
Surgeonfishes show varying degrees of habitat preference and utilization of coral reef habitats, with some species spending the majority of their life stages on coral reef while others primarily utilize seagrass beds, mangroves, algal beds, and /or rocky reefs. The majority of surgeonfishes are exclusively found on coral reef habitat, and of these, approximately 80% are experiencing a greater than 30% loss of coral reef area and degradation of coral reef habitat quality across their distributions. However, more research is needed to understand the long-term effects of coral reef habitat loss and degradation on these species' populations. Widespread coral reef loss and declining habitat conditions are particularly worrying for species that recruit into areas with live coral cover, especially as studies have shown that protection of pristine habitats facilitate the persistence of adult populations in species that have spatially separated adult and juvenile habitats (Comeros-Raynal et al. 2012).
|Conservation Actions:||There are no species-specific conservation measures in place for this species. However, its distribution overlaps several marine protected areas within its range. In Queensland, Australia, there is a recreational catch limit of five per species and a minimum size limit of 25 cm (Department of Primary Industries accessed 8 April 2010).|
Allen, G.R. 2003. Appendix 5. List of the reef fishes of Milne Bay Province, Papua New Guinea. In: G.R. Allen, J. P. Kinch, S.A. McKenna, and P. Seeto (eds), A Rapid Marine Biodiversity Assessment of Milne Bay Province, Papua New Guinea–Survey II (2000), pp. 172. Conservation International, Washington, DC, USA.
Allen, G.R. 2003b. Appendix 1. List of the Reef Fishes of the Raja Ampat Islands. In: R. Donnelly, D. Neville and P.J. Mous (eds), Report on a rapid ecological assessment of the Raja Ampat Islands, Papua, Eastern Indonesia, held October 30 – November 22, 2002. The Nature Conservancy - Southeast Asia Center for Marine Protected Areas, Sanur, Bali.
Allen, G.R. 2009. Coral Reef Fish Diversity. In: R. Hamilton, A. Green and J. Almany (eds), Rapid Ecological Assessment: Northern Bismarck Sea, Papua New Guinea. Technical Report of survey conducted August 13 to September 7, 2006, The Nature Conservancy.
Arai, H. and Sato, T. 2007. Prominent ornaments and rapid color change: use of horns as a social and reporductive signal in unicornfish (Acanthuridae: Naso). Ichthyological Research 54: 49-54.
Ashworth, J.S. and Ormond, R.F.G. 2005. Effects of fishing pressure and trophic group on abundance and spillover across boundaries of a no-take zone. Biological Conservation 121: 333-344.
Choat, J.H. and Robertson, D.R. 2002a. Age-based studies on coral reef fishes. In: P.F. Sale (ed.), Coral reef fishes: dynamics and diversity in a complex ecosystem, pp. 57-80. Academic Press, Burlington, San Diego and London.
Choat, J.H., Clements, K.D. and Robbins, W.D. 2002b. The trophic status of herbivorous fishes on coral reefs. 1. Dietary analyses. Marine Biology 140: 613-623.
Choat, J.H., Robbins, W.D. and Clements, K.D. 2004. The trophic status of herbivorous fishes on coral reefs. Marine Biology 145: 445-454.
Comeros-Raynal, M.T., Choat, J.H., Polidoro, B.A., Clements, K.D., Abesamis, R., Craig, M.T., Lazuardi, M.E., McIlwain, J., Muljadi, A., Myers, R.F., Nañola Jr., C.L., Pardede, S., Rocha, L.A., Russell, B., Sanciangco, J.C., Stockwell, B., Harwell, H. and Carpenter, K.E. 2012. The likelihood of extinction of iconic and dominant components of coral reefs: the parrotfishes and surgeonfishes. PLoS ONE http://dx.plos.org/10.1371/journal.pone.0039825.
Department of Primary Industries - Queensland Government. 2010. Surgeonfishes. Available at: http://www.dpi.qld.gov.au/28_8861.htm. (Accessed: 8 April).
Eble, J. 2009. How old is that fish? Journal of Micronesian Fishing Fall 2009(3): 5.
Eble, J.A., Langston, R. and Bowen, B.W. 2009. Growth and reproduction of Hawaiian Kala, Naso unicornis. Final Report prepared for Fisheries Local Action Strategy. Division of Aquatic Resources, Honolulu.
Global Marine Aquarium Database. 2010. Species Trade Details. Available at: http://www.unep-wcmc.org/GMAD/species.cfm. (Accessed: March 19).
Horne, J.B., L. van Herwerden, J.H. Choat and D.R. Robertson. 2008. High population connectivity across the Indo-Pacific: Congruent lack of phylogeographic structure in three reef fish congeners. Molecular Phylogenetics and Evolution 49: 629-638.
IUCN. 2012. IUCN Red List of Threatened Species (ver. 2012.2). Available at: http://www.iucnredlist.org. (Accessed: 17 October 2012).
Johannes, R.E. 1981. Words of the lagoon: fishing and marine lore in the Palau district of Micronesia. University of California Press, Berkley.
Kronen, M., Friedman, K., Boblin, P., Chapman, L., Vunisea, A., Lasi, F., Awira, R., Pakoa, K., Magron, F., Tardy, E. and Pinca. S. 2006. Federated States of Micronesia Country Report: Profiles and results from survey work at Yyin and Riiken (Yap) and Piis-Panewu and Romanum (Chuuk). ReeFisheries Observatory. Series 2 – Fisheries. Pacific Regional Oceanic and Coastal Fisheries Development Programme (PROCFish/C/CoFish) / Secretariat of the Pacific Community, Noumea, New Caledonia.
Kulbicki, M., Labrosse, P. and Letourneur, Y. 2000.. Fish stock assessment of the northern New Caledonian lagoons: 2 – Stocks of lagoon bottom and reef-associated fishes. Aquatic and Living Resources 13(2): 77-90.
Lecchini, D., Polti, S., Nakamura, Y., Mosconi, P., Tsuchiya, M., Remoissenet, G. and Planes, S. 2006. New perspectives on aquarium fish trade. Fisheries Science 72: 40-47.
Letourneur, Y., M. Kulbicki and P. Labrosse. 2000. Fish stock assessment of the northern New Caledonian lagoons: 1- Structure and stocks of coral reef fish communities. Aquat. Living Resour. 13(2): 65-76.
Meyer, C.G. and Holland, K.N. 2005. Movement patterns, home range size and habitat utilization of the bluspine unicornfish, Naso unicornis (Acanthuridae) in a Hawaiian marine reserve. Environmental Biology of Fishes 73: 201-210.
Ono, Rintaro and Addison, D.J. 2009. Ethnoecology and Tokelauan fishing lore from Atafu Atoll, Tokelau. SPC Traditional Marine Resource Management and Knowledge Information Bulletin 26: 3-22.
Randall, J.E. 2001a. Surgeonfishes of the world. Mutual Publishing and Bishop Museum Press, Hawai'i, Honolulu, Hawaii.
Reeson, P.H. 1983. The biology, ecology and bionomics of the surgeonfishes, Acanthuridae. In: J.L. Munro (ed.), Caribbean coral reef fishery resources, pp. 178-190.
Rhodes, K.L.,Tupper, M.H. and Wichilmel, C.B. 2008. Characterization and management of the commercial sector of the Pohnpei coral reef fishery, Micronesia. Coral Reefs 27: 443–454.
Walsh, W., Cotton, S., Carman, B., Livnat, L., Osada, K., Barnett, C., Tissot, B., Stevenson, T., Wiggins, C., Tarnas, D., Bourdon, K. and Peck, S. 2010. Report on the Findings and Recommendations of Effectiveness of the West Hawaii Regional Fishery Management Area. Department of Land and Natural Resources State of Hawaii, State of Hawaii.
Wantiez, L., Thollot, P. and Kulbicki, M. 1997. Effects of marine reserves on coral reef fish communities from five islands in New Caledonia. Coral Reefs 16(4): 215-224.
Werner, T.B. and Allen, G.R. 2000. A rapid marine biodiversity assessment of the Calamianes Islands, Palawan province, Philippines. RAP Bulletin of Biological Assessment 17. Conservation International, Washington, USA.
|Citation:||McIlwain, J., Choat, J.H., Abesamis, R., Clements, K.D., Myers, R., Nanola, C., Rocha, L.A., Russell, B. & Stockwell, B. 2012. Naso unicornis. The IUCN Red List of Threatened Species 2012: e.T177970A1506556. . Downloaded on 25 June 2016.|
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