|Scientific Name:||Holothuria scabra|
|Species Authority:||Jaeger, 1833|
Holothuria scabra and H. scabra var. versicolor (now H. lessoni) have recently been properly identified as distinctive species (Uthicke et al. 2005).
|Red List Category & Criteria:||Endangered A2bd ver 3.1|
|Assessor(s):||Hamel, J.-F., Mercier, A., Conand, C., Purcell, S., Toral-Granda, T.-G. & Gamboa, R.|
|Reviewer(s):||Polidoro, B., Carpenter, K.E., Knapp, L. & Harwell, H.|
This species is commercially exploited throughout its range for its high value as beche-de-mer to supply the Asian consumers around the world. Based on a number of quantitative and qualitative studies, populations are estimated to have declined by more than 90% in at least 50% of its range, and are considered overexploited in at least 30% of its range, although exact declines are difficult to estimate. The status of populations in China are not known, and populations near mainland Australia are targeted but not considered to be overexploited. Declines and overexploitation have occurred primarily since the 1960s, and although generation length is not known, echinoderms are not considered to go through senescence and therefore one generation length may be greater than several decades. As this species is estimated to have experienced at least a 50% decline over the past 30-50 years, it is therefore listed as Endangered. If fishing pressure was significantly decreased, this species may recover relatively quickly due to its reproductive capacity.
|Range Description:||This species is widespread throughout the Indo-Pacific between latitudes 30°N and 30°S (Hamel et al. 2001), from South Africa to the Red Sea, India, China and Japan to Australia, and to Micronesia in the northeast and Tonga in the southeast. In Madagascar, this species is observed in the west coast from the south of Toliara to Nosy-be (Rasolofonirina pers. comm. 2010).|
Native:Australia; Bangladesh; British Indian Ocean Territory; Brunei Darussalam; Cambodia; China; Comoros; Cook Islands; Djibouti; Egypt; Eritrea; Fiji; India (Andaman Is.); Indonesia; Israel; Japan; Jordan; Kenya; Kiribati; Madagascar; Malaysia; Maldives; Mauritius; Mayotte; Micronesia, Federated States of ; Mozambique; Myanmar; Nauru; New Caledonia; Oman; Palau; Papua New Guinea; Philippines; Réunion; Samoa; Saudi Arabia; Seychelles; Singapore; Solomon Islands; Somalia; South Africa; Sri Lanka; Sudan; Taiwan, Province of China; Tanzania, United Republic of; Thailand; Tonga; Tuvalu; Vanuatu; Viet Nam; Wallis and Futuna; Yemen
|FAO Marine Fishing Areas:|
|Range Map:||Click here to open the map viewer and explore range.|
Genetic studies on this species show distinct populations within Australia (the Northern Territory, the Torres Strait, the Solomon Islands, the Great Barrier Reef), the Solomon Islands, and New Caledonia with little geneflow (Kinch et al. 2008). Genetic studies involving this species have showed a very restricted gene flow indicating a limited recruitment from within regions (Uthicke and Benzie 2001, Skewes et al. 2004).
This species has been significantly depleted in at least 50% of its range (e.g. in East Africa, Madagascar, India, Viet Nam, Papua New Guinea, Solomon Islands) It is considered overexploited in at least another 25% of its range (e.g. Philippines and Indonesia), and the status of populations that have been heavily targeted in China are not known (Chen 2004, Li 2004). In New Caledonia, India and Malaysia catches have been depleted (Hamel et al. 2001), In the Torres Strait, the fishery for this species was closed in the mid 1990s, and the current biomass today is still estimated at less than 8 percent of the virgin biomass (Skewes et al. 2000). This species may also be overexploited in Vanuatu as the fishery has been closed since 2008. In Australia, this species is targeted in the Northern Territory, but is not considered to be overexploited, except possibly in the Torres Strait.
Depletion refers to commercially unviable, and estimated to represent an approximately 90% loss or greater over the past 25-50 years (since the 1960s). In areas where it is considered overexploited, populations are difficult to estimate based on regional and local fishing effort, but harvests have declined and based on traditional fisheries definitions, overexploited is estimated to be 30% above maximum sustainable yield. This species has been reported to be extirpated from a few locations in recent years (in Egypt see Hasan 2005; parts of Indonesia, Thailand, Viet Nam and Malaysia see Choo 2008; Papua New Guinea Milne Bay see Skewes et al. 2002; and some parts of Solomon Islands see Friedman et al. 2010).
Regional and Country Specific Information:
In the Solomon Islands, this species is considered rare. In Samoa, the little information available on sea cucumber densities showed the absence of this species. In Palau, recorded densities of this species in 2003 were 40 ind/ha. In Vanuatu, there were 43 ind/ha in 1987, however recent surveys show lower densities in certain sites. In Fiji, there were 625 ind/ha in 1993, while in 2003 there were only 160 ind/ha in areas close to Suva (Kinch et al. 2008). Also in Fiji, catches for this species peaked at 700 t in 1988, and stocks are now considered depleted (Bruckner et al. 2003).
In New Caledonia, information suggests some overharvesting. In New Caledonia, populations of a few commercial species appear depleted, namely Holothuria fuscogilva, Holothuria lessoni and Actinopyga lecanora. Several other species are perhaps not critically low but are relatively sparse, namely Actinpyga mauritiana, A. miliaris and this species (Purcell et al. 2009). Furthermore, although few of this species are found in field surveys, they are still one of the most common species collected by fishers (Purcell et al. 2009). In New Caledonia, exports were over 125 t in 1990 and 1991 with declines to less than 81 t/yr from 1992 to 1994 (A. miliaris harvest ~75% of exports; this species harvest ~ 25% of exports). Exports continued to decline from 79.8 t in 1994 to 39.1 t in 1998 (Bruckner et al. 2003).
Recent information from Papua New Guinea indicates that this species has been overexploited. In New Ireland Province, the fishery for this species targets all sizes. In the Western Province of Papua New Guinea, this species formed 100% of the sea cucumber catch in 1990 and 1991, and dropped only because of depleted stocks (Lokani pers. obs.). Catches in Papua New Guinea dropped from 192,647 kg/year in 1991 to 39,302 kg/year in 1993.
Many tropical countries in the Indo-Pacific are targeting sea cucumbers with this species being the main overfished species (Choo 2008). In Indonesia (Sulawesi), this species is considered overfished and in other locations it is a rare species. In Malaysia, it is now rare and fishing pressure is focusing on other lower value species. In Thailand, its population has also become depleted. In Viet Nam, this species is fast approaching local extinction. In Philippines, monthly average landing of this species have been about 20 kg, well below the 109 kg average in 2002 (Choo 2008).
In India, Holothuria scabra, H. spinifera and Bohadschia marmorata have been collected over the last 1000 years. Fishermen began collecting other species in 1990 in response to high export value and population declines. Actinpyga echinites and A. miliaris populations were overexploited in some areas as early as 2 years later (Bruckner et al. 2003). Particularly in the Gulf of Manner and Pal Bay, CPUE and size of specimens has dramatically declined (Bruckner et al. 2003).
In Seychelles, it used to be collected in large numbers, but landings have decreased to very low levels. It is considered overexploited (Aumeeruddy and Conand 2008). In Tanzania, this species used to dominate the catches (Mgaya and Mmbaga 2007). In Egypt, it is almost completely lost (Lawrence et al. 2004).In Madagascar, declining exports, quality and size of sea cucumbers, including this species, indicate that resources are overexploited (1998) (Bruckner et al. 2003). In Mozambique, high fluctuation in exports of this species, Holothuria nobilis, H. fuscogilva, H. atra, Actinpyga echinites and A. mauritiana may be due to irregular reporting or to overexploitation. Catch here was reported at 500 t in 1990, 700 t in 1993, 6 t in 1995, and 54 t in 1996. In Inhambane Province, holothurian fisheries are closed until stocks rebuild (Bruckner et al. 2003). Kalaeb et al. (2008) used transect data to calculate a population density of 7.5 individuals/ha of this species in Eritrea. In East Africa, fisheries for this species may now have trouble finding brood stocks (Conand pers. comm. 2010).
|Current Population Trend:||Decreasing|
|Habitat and Ecology:|
This species is distributed mainly in low energy environments behind fringing reefs or within protected bays and shores. Individuals prefer ordinary coastal areas to coral reefs, particularly intertidal seagrass beds close to mangroves, however they are also found along inner reef flats and lagoons. This species is attracted to muddy sand or mud habitats (Rasolofonirina pers. comm. 2010, Skewes et al. 2004). Juveniles of this species settle in shallow seagrass beds and some may make it to deeper waters (Mercier et al. 1999). This species has been found to preferentially settle on seagrass such as Thallassia hemprichi (Hamel et al. 2001). Recent studies on released juveniles have shown that mangrove/seagrass areas were the most suitable habitat for settling juveniles, due mainly to low predation rates (Dance et al. 2003, Skewes et al. 2004). This species is also known to burrow, possibly leading to biased transect data.
In the Western Central Pacific, this species can be found in inner reef flats of fringing reefs and lagoon islets between 0 and 15 m (Kinch et al. 2008). In Viet Nam, it is found in sandy estuaries or lagoons between 2 and 25 m (Choo 2008). In the Africa and Indian Ocean region, this species can be found in the back reef over muddy sand between 0 and 5 m, in the vicinity of mangroves; both adults and juveniles burrow in the sand (Conand 2008). In Madagascar, it can be found in the inner slope and seagrass beds, with highest densities in the latter (Conand 2008). This species has narrow habitat preferences that restrict it's range within the Torres Straight and the surrounding areas of Australia (Skewes et al. 2004).
In the Western Central Pacific, reproductive biology studies have been conducted by several authors, yielding the following information on reproductive periods: Great Barrier Reef (Australia) between November and January, Great Barrier Reef (Australia) November and December, Northern Territory (Australia) between December and February; New Caledonia December to January and August to September; PNG in November and December; Solomon Islands from September to December (Kinch et al. 2008). In India, only a careful microscopic revision of the gametes allows identification of a specimen as male or female (James 2004). In Asian countries near the Equator, this species spawns throughout the year. However, in Indonesia, it had two peak spawning periods, whilst in the Philippines, the main spawning event is from May to June and October to November (Choo 2008). In Australia, this species seems to follow a pattern of spawning in warmer months, but also undergoes a smaller, secondary peak of spawning later in the year (Skewes et al. 2004).
Larvae of this species are planctonic, small juveniles under 10 mm in length that are epibiontic (live on seagrasses) and juveniles and adults are endobiontic. This species grows relatively fast when young, reaching size at first maturity at ca. 180 g in a year (Conand 1989, Purcell 2010). Shelley (1985) estimated that it grows 14 g/month. In the Philippines, size at first maturity is 120 g (Gamboa pers. comm. 2010). In captivity, this species has reached settling stage after 13-16 days as planktonic larvae (Skewes et al. 2004). This species is reported to mature and to grow to 15 cm in one to two years (Skewes et al. 2000). This species recruits well under proper conditions.
In general, generation length is unknown for these species. Body size is not a good indicator of age or longevity. There is some indication, however, that many echinoderms do not go through senescence, but simply regenerate. Therefore generation length cannot be estimated, but is assumed to be greater than several decades (20-40 years) in a natural, undisturbed environment.
|Use and Trade:||
This species has been targeted in fisheries throughout its range for hundreds of years, with periods of high and low abundance. However, fishing pressure has dramatically increased in the past 25 to 50 years, since the 1960s, and is expected to continue, even as stocks are depleted. When this occurs, other species are often targeted in their place.
In the Western Pacific Region, this species is commercially exploited in FSM, Kiribati, Wallis and Futuna, PNG, Solomon Islands, Vanuatu, New Caledonia, Fiji, Torres Strait, Great Barrier Reef, Moreton Bay, Northern Australia and Western Australia (Australia) where it is consumed either whole or their intestines and/or gonads are consumed as delicacies or as protein in traditional diets; local consumption is of greater importance in times of hardship (i.e. following cyclones). There is a subsistence fishery in Palau, Wallis and Futuna, PNG and Fiji. In Palau, the gonads and/or intestines of this species are consumed. In PNG, this species is consumed, often grilled, in the Western Central Province and in the Milne Bay province. In 1989, this species accounted for 70% of the total catches for export; however recent activity has shifted to low value species due to its decline. In Fiji, it is also consumed locally in coconut sauce. In New Caledonia, this species is among the most dominant species in the catch however export statistics show declines in catches of this species and increase of others (Kinch et al. 2008).
In Asia, this species is harvested in China, Japan, Malaysia, Thailand, Viet Nam, Indonesia and Philippines. In Thailand, it was originally consumed locally but then in 1970s an export fishery started. In Viet Nam, it is also part of an export fishery (Choo 2008). In Philippines, it is the second most valuable species (after Holothuria fuscogilva) (Choo 2008).
In the Africa and Indian Ocean region, this species is fished in Madagascar and Mozambique where it is one of the most valuable species. It is also fished in Eritrea, India, Oman, Seychelles (Conand 2008), Tanzania (Mgaya and Mmbaga 2007), Egypt (Lawrence et al. 2004), and Mozambique (Bruckner 2006). In India it used to be one of the most important species for the last 1000 years, until a fishing ban as of 2001 closed the fishery (Bruckner 2006).
The sandfish Holothuria scabra has been identified as one of the most promising sea cucumber species for aquaculture (Toral-Granda 2007). In Vanuatu, a sea ranching venture with this species was initiated by an Australian company using juveniles produced in the Australian-based hatchery. A private Australian company has been successful in mass producing this species in a hatchery in Queensland. Thousands of juveniles have been released in designated aquaculture areas over the last few years (Kinch et al. 2008). This species has been bred on an experimental scale in India, Indonesia, Solomon Islands, New Caledonia, Viet Nam and the Maldives with reproductive, settling and feeding cycle completed (Choo 2008). In China, it is a candidate for sea cucumber farming due to its high commercial value (Chen 2004).
|Major Threat(s):||Commercial harvest is of high concern for this highly valued species (Toral-Granda 2006, 2007). This species is one of the most valuable species of holothurian and it is intensively exploited in many tropical countries for trade in the Asian markets (Rasolofonirina pers. comm. 2010). Despite being a high value species, this species showed an increase in catches after the decline in catch of Actinopyga miliaris as seen in Fiji (Kinch et al. 2008). This species has been heavily exploited in many parts of its range, and is also a bycatch of prawn nets in Madagascar (Toral-Granda 2007). Although few individuals are found in field surveys, they are still one of the most targeted species by fishers (Purcell et al. 2009).|
For stocks in Papua New Guinea, Kinch et al. (2008) note “Arguably, the declines in abundances of Holothuria scabra and H. whitmaei could qualify them for CITES listing”. At the CITES sea cucumber workshop in Malaysia in 2004, this species was identified as a species of highest concern due to its overexploitation (Toral-Granda 2007).
This species is regulated with a minimum size of 22 cm TL live and 10 cm TL dry in Papua New Guinea, 20 cm TL live and 10 cm TL in New Caledonia, 18 cm TL in Torres Strait, 17 cm TL in Moreton Bay, and 16 cm TL in Great Barrier Reef, Northern Territory and Western Australia (Australia) (Kinch et al. 2008). The Moreton Bay fishery (Australia) for this species is managed through permits as a developmental fishery. In Australia, a ban was put in place between 1996 and 2000, but no significant recovery was observed (Purcell 2010). In the Solomon Islands, release of cultured juveniles is sometimes used for restoring and enhancing natural stocks of this species (Battaglene 1999). In the Philippines the exporters observe a size limit 6.35 cm (dry length). However, bans are often not permanent. This species has been banned in Fiji, India, and Papua New Guinea, and the fishery has been closed in Vanuatu since 2008. Sea cucumber collection has been banned in the Andaman and Nicobar Islands (Bruckner et al. 2003). In Inhambane Province, holothurian fisheries have been closed until stocks rebuild (Bruckner et al. 2003). The effectiveness of the ban on this species' population is yet to be determined.
Aumeeruddy, R. and Conand, C. 2008. Seychelles: a hotspot of sea cucumber fisheries in Africa and Indian ocean. In: Toral-Granda V., Lovatelli A., Vasconcellos M. (ed.), Sea cucumbers. A global review on fishery and trade.. FAO Fisheries Technical Paper No. 516, Rome.
Battaglene, S.C. 1999. Culture of tropical sea cucumbers for stock restoration and enhancement. ICLARM (International Center for Living Aquatic Resources Management) Quarterly 22(4): 4-11.
Bruckner, A.W. 2006. Management and conservation strategies and practices for sea cucumbers. In: A.W. Bruckner (ed.), Proceedings of the CITES workshop on the conservation of sea cucumbers in the families Holothuriidae and Stichopodidae.. NOAA Technical Memorandum NMFS-OPR-34, USA.
Bruckner, A.W., Johnson, K.A. and Field, J.D. 2003. Conservation strategies for sea cucumbers: Can a CITES Appendix II listing promote sustainable international trade? SPC Beche-de-mer Information Bulletin 18: 24-33.
Chen, C.-H. 2004. Checklist of the fishes of Penghu.
Choo, P.S. 2008. Population status, fisheries and trade of sea cucumbers in Asia. In: M.V. Toral-Granda, A. Lovatelli, M. Vasconcellos. (ed.), Sea cucumbers. A global review on fisheries and trade.. FAO, Rome.
Conand, C. 2008. Population status, fisheries and trade of sea cucumbers in Africa and the Indian Ocean. In: M.V. Toral-Granada, A. Lovatelli, M. Vasconcellos. (ed.), Sea cucumbers. A global review on fisheries and trade.. FAO, Rome.
Conand, C.P. 1998. Holothurians (sea cucumbers, Class Holothuroidea). In: K.E. Carpenter and V.H. Niem (eds), FAO Species Identification Guide for Fishery Purposes, pp. 1157-1190. Rome.
Dance, S.K., Lane, I. and Bell, J.D. 2003. Variation in short-term survival of cultured sandfish (Holothuria scabra) released in mangrove–seagrass and coral reef flat habitats in Solomon Islands. Aquaculture 220(1-4): 495-505.
Hamel, J.-F., Conand, C., Pawson, D.L. and Mercier, A. 2001. The sea cucumber Holothuria scabra (Holothuroidea: Echinodermata): Its biology and exploitation as Beche-de-mer. Advances in Marine Biology 41: 129-223.
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James, D.B. 2004. Captive Breeding of the Sea Cucumber Holothuria scabra, from India. In: C. Conand, S. Purcell, S. Uthicke, J.-F. Hamel and A. Mercier (eds), Advances in sea cucumber aquaculture and management, pp. 385-395. FAO, Rome.
Kalaeb, T., Ghirmay, D., Semere, Y. and Yohannes, F. 2008. Status and preliminary assessment of the sea cucumber fishery in Eritrea. SPC Beche de Mer Information Bulletin #27.
Kinch, J., Purcell, S., Uthicke, S. and Friedman, K. 2008. Population status, fisheries and trade of sea cucumbers in the Western Central Pacific. In: V. Toral-Granda and A. Lovatelli and M. Vasconcellos. (eds), Sea cucumbers. A global review of fisheries and trade. Fisheries and Aquaculture Technical Paper. No. 516, pp. 7-55. FAO, Rome.
Lawrence, J.M., Sonnenholzner, J. 2004. Distribution and abundance of asteroids, echinoids and holothuroids in the Galapagos. In: Heinzeller and Nebelsick (eds), 11th International Conference Echinoderms, pp. 239-244. Munich.
Li, X. 2004. Fishery and resource management of tropical sea cucumbers in the islands of the South China Sea. In: A. Lovatelli, C. Conand, S. Purcell, S. Uthicke, J.F. Hamel, A. Mercier. (ed.), Advances in sea cucumber aquaculture and management.. FAO, Rome.
Lokani, P., Polon, P. and Lari, R. 1996. Management of beche-de-mer fisheries in the Western Province of Papua New Guinea. SPC Beche-de-mer Information Bulletin. James Cook University and National Fisheries Authority, Konedobu, Papua New Guinea, Townsville, Australia.
Mgaya, Y.D. and Mmbaga, T.K. 2007. Chapter 6: Sea cucumbers in Tanzania. In: C. Conand and N.A. Muthiga (eds), Commercial sea cucumbers: a review for the Western Indian Ocean, WIOMSA Book Series.
Purcell, S.W. 2010. Managing sea-cucumber fisheries with an ecosystem approach. In: A. Lovatelli, M. Vasconcellos, Y.Yimin. (ed.). FAO Fisheries and Aquaculture Techinical Paper No. 520., Rome.
Purcell, S.W., Gossuin, H. and Agudo, N.N. 2009. Status and management of the sea cucumber fishery of la Grande Terre, New Caledonia. The WorldFish Center, Penang, Malaysia.
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Toral-Granda, V.M. 2006. Fact sheets and identification guide for commercial Sea cucumber species.
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Uthicke, S. and Benzie, J. 2001. Effect of bêche-de-mer fishing on densities and size structure of Holothuria nobilis (Echinodermata: Holothuroidea) populations on the Great Barrier Reef. Coral Reefs 19(3): 271-276.
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|Citation:||Hamel, J.-F., Mercier, A., Conand, C., Purcell, S., Toral-Granda, T.-G. & Gamboa, R. 2013. Holothuria scabra. The IUCN Red List of Threatened Species 2013: e.T180257A1606648.Downloaded on 25 June 2017.|
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