Review of selected on the basis of a new or increased export quota in 2011

(Version edited for public release)

SRG 57

Prepared for the

European Commission Directorate General E - Environment ENV.E.2. – Development and Environment

by the

United Nations Environment Programme World Conservation Monitoring Centre

September, 2011

UNEP World Conservation Monitoring PREPARED FOR Centre 219 Huntingdon Road The European Commission, Brussels, Belgium Cambridge

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CITATION UNEP-WCMC. 2011. Review of species selected on the basis of a new or increased export quota in 2011. SRG 57. UNEP-WCMC, Cambridge.

Table of Contents

1. Introduction ...... 4

2. Update since Analysis of 2011 CITES export quotas ...... 4

3. Species reviews...... 5

SPECIES: Cercopithecus dryas...... 5 SPECIES: tataricus...... 9 SPECIES: Hippocampus comes ...... 13 SPECIES: Hippocampus kelloggi ...... 18

3

1. Introduction Export quotas are usually established by each Party to CITES unilaterally, but they can also be set by the Conference of the Parties or result from recommendations of the and Plants Committees. For Acipenseriformes species, quotas should be established for meat and caviar from stocks shared between different Range States [Resolution Conf. 12.7 (Rev. CoP14)]. However, in general, there is no specific requirement in the text of the Convention to establish quotas to limit the trade in CITES-listed species. Nevertheless, the use of export quotas was recognised as being such an effective management tool that Parties adopted Resolution Conf. 14.7 (Rev. Cop15) on the Management of nationally established export quotas. When a country sets its own national export quotas for CITES species, it should inform the Secretariat (Resolution Conf. 12.3 [Rev. CoP15]), which in turn informs the Parties. Early in each year, the Secretariat publishes a Notification to the Parties containing a list of export quotas of which it has been informed. Quotas generally relate to a calendar year (1 January to 31 December)1; however, since 2008 sturgeon quotas have related to a quota year (1 March to 29 February). The 2011 CITES export quotas for Anguilla anguilla were published on the CITES website (www.cites.org) on 12/01/2011 and for Swietenia macrophylla from Peru on 28/01/2011. Quotas for other species were initially published on 01/03/2011, and were updated on 07/03/2011, 24/03/2011, 07/04/2011, 12/05/2011 and 18/05/2011. Based on the quotas that were available on 19/05/2011, UNEP-WCMC analysed the 2011 CITES export quotas to identify: a) Quotas that were newly established in 2011; b) Quotas that increased or decreased in 2011 compared with 2010 quotas (or compared with 2009 quotas if no quota was published in 2010). This analysis was discussed at SRG56 on 20/06/2011. Four species/country combinations were selected for review where the new or increased quota in 2011 indicated that further consideration might be necessary to determine whether the trade would have a harmful effect on the conservation status of the species or on the extent of the territory occupied by the relevant population of the species. These were:  Cercopithecus dryas/Democratic Republic of Congo: New quota of 10 live specimens. Globally Critically Endangered.  Eryx tataricus/: Increased quota from 300 live specimens in 2010 to 600 live specimens in 2011.  Hippocampus comes/Vietnam: New quota of 12 000 live specimens. Globally Vulnerable  Hippocampus kelloggi/Vietnam: New quota of 7000 live specimens. Data Deficient.

1.1. Trade data Trade data included in this report were downloaded from the UNEP-WCMC CITES Trade Database on 16/08/2011.

2. Update since Analysis of 2011 CITES export quotas Since the analysis of CITES export quotas was undertaken in May 2011, additional CITES export quotas were published on the CITES website on 22/06/2011, although none of them were of particular note.

1 In addition, quotas for Anguilla anguilla in 2011 were valid from 3rd December 2010 until the end of 2011, and quotas for Swietenia macrophylla from Peru were valid from 23rd July 2010 until 22nd July 2011.

4 Cercopithecus dryas

3. Species reviews REVIEW OF SPECIES SELECTED ON THE BASIS OF THE 2011 QUOTA ANALYSIS

MAMMALIA CERCOPITHECIDAE

SPECIES: Cercopithecus dryas

SYNONYMS: Cercopithecus salongo

COMMON NAMES: Dryasmeerkat (Dutch), Dryas Guenon (English), Dryas Monkey (English), Cercopithèque dryas (French), Mono dryas (Spanish), dryasmarkatta (Swedish)

RANGE STATES: Democratic Republic of the Congo

RANGE STATE UNDER REVIEW: Democratic Republic of the Congo

IUCN RED LIST: Critically Endangered

PREVIOUS EC OPINIONS: Previous Article 4.6(b) import suspension for wild specimens from the Democratic Republic of the Congo first imposed on 22/12/1997 and removed on 26/11/2010.

TRADE PATTERNS: Cercopithecus dryas from the Democratic Republic of the Congo (hereafter referred to as DRC) was selected on the basis of a new quota of 10 wild specimens and also on the basis of its Critically Endangered status and being endemic to DRC. DRC was subject to a European Commission decision to suspend imports of wild-sourced C. dryas 1997-2010. The only reported trade to the EU-27 2000-2009 consisted of one body exported by Cameroon which was reported as seized or confiscated by the United Kingdom in 2002. There were no reported direct exports of the species from DRC to countries other than the EU-27 2000-2009. TAXONOMIC NOTE: Lernoud (1988) reported that at the time of writing so little was known of C. dryas and C. salongo that it was impossible to have a clear idea of their true taxonomic status. The synonym C. salongo is considered an age-variant of the species (Colyn et al., 1991; cited by Wilson and Reeder, 2005), although this was disputed (Sarmiento, 2000). Problems with the appeared to have arisen by C. dryas having been described on the basis of a photograph and C. salongo on the basis of a skin, and individuals of comparable age not having been studied (Sarmiento, 2000).

5 Cercopithecus dryas

CONSERVATION STATUS in range states Democratic Republic of the Congo: Cercopithecus dryas is a guenon species known only from a few localities in the Democratic Republic of Congo (Groves, 2005). It is one of the smallest-sized guenons, mainly inhabiting secondary forest, while a small number inhabit swamp forest (Kuroda et al., 1985). Although Hart et al. (2008) reported that there was no reliable information on the status of the populations, they considered that the population probably did not exceed a few hundred individuals and there could be fewer than 200 individuals left in the wild (M. Hurley, pers. comm. cited by Hart et al., 2008). Hart et al. (2008) reported that no individuals were held in captivity. Very little appears to be known about the species. In 1988 it was reported that C. dryas was known only from a single individual (skin and skull) and the picture of the captive and that although the collecting locality was said to be Lomela, where it came from was unknown (Colyn, 1988). Colyn (1988) was unable to find another specimen in the upper Lopori basin. More recently, it was reported that only two examples of the species were known (Seyler et al., 2010). A field study was performed for the species, which took place in the Bisandu forest of the Kokolopori Bonobo reserve during the period from April 2005 to January 2007 (Lokasola, 2008). Previous to this study, the range of the species was uncertain as specimens were known only from bushmeat markets. Lokasola (2008) reported that C. dryas was observed at four different Kokolopori sites, where group sizes were found to range from 15 to 31 individuals. Cercopithecus dryas had also been reported from Lomela and Wamba, although these ranges were based on one specimen from each location found at bushmeat markets, and the “Wamba” specimen was later established to have been killed in Kokolopori (Lokasola, 2008). However, the presence of C. dryas was confirmed on the left bank of the Congo, where it was reportedly known only from Wamba and Lomela (Colyn, 1991; Murhabale, 2011). Kuroda et al (1985 cited by Colyn, 1988) also reported having seen specimens of C. dryas (reported as C. salongo) in the Wamba area, where although its population density was low, it was apparently not rare. Notably, a survey in December 1997 and January 1998 did not reveal any evidence for the species in the nearby northern section of the Salonga National Park, nor did local hunters employed as guides recognize a picture of the species (Van Krunkelsven et al., 2000). Similarly, a survey of Salonga National Park indicated that C. dryas seemed to occur near the park but not within it (Oates and IUCN/SSC Primate Specialist Group, 1996). Conversely, it was included on a list of mammals of the Salonga National Park (Paniscus, n.d.) Hart et al. (2008) reported that the population trend for the species was unknown; however it was considered that effective management of the Kokolopori reserve was key to the survival of the species (Hart et al., 2008). Hunting and habitat loss to agriculture were considered to be the main threats to the species (Hart et al., 2008). Bushmeat hunting was reported to be a common component of household revenue in the Congo basin, with the Democratic Republic of Congo having high estimated levels of consumption relative to neighbouring countries, and primates known to be consumed in the country (Wilkie and Carpenter, 1999). Survey teams for the Bonobo Conservation Initiative (BCI) discovered apparently permanent hunting camps in the Kokolopori; the BCI considered that the leaders of the Kokolopori reserve would ultimately be able to exercise authority to ban hunting of endangered species, although this was anticipated to be a difficult task (Bonobo Conservation Initiative, 2002). High levels of hunting (though C. dryas was not specified) were identified during a survey in Wamba (Oates and IUCN/SSC Primate Specialist Group, 1996). Wright and Jernvall (1999) warned that species found only in one country were particularly vulnerable to political instability, including warfare, which would compromise otherwise successful conservation actions. Chapman et al. (2006) considered C. dryas to be among those vulnerable species. Researchers were forced to abandon a survey in Wamba for two years due to political instability (Oates and IUCN/SSC Primate Specialist Group, 1996). Salonga National Park was included on the list of World Heritage Sites in Danger in 1999, where it has remained until the present (WHC, 2011).

6 Cercopithecus dryas

C. salongo and C. dryas (although the latter was reported with a question mark) were included on a list of wild animals hunted by the Ngandu principally for food and medicine, being locally known as ekele and tolu (Takeda, 1996). DRC is Party to the African Convention on the Conservation of Nature and Natural Resources (ACCNNR, 1968). Cercopithecus was listed in Annexe 4 of the 2004 Democratic Republic of Congo implementation of the hunting regulations (DRC, 2004) and as such C. dryas is not protected and may be hunted by holders of a hunting permit. REFERENCES: ACCNNR 1968. African Convention on the Conservation of Nature and Natural Resources. Algiers, Organisation of African Unity. Bonobo Conservation Initiative. 2002. Bushmeat URL: http://www.bonobo.org Accessed: 30-8-2011.

Chapman, C. A., Lawes, M. J., and Eeley, H. A. C. 2006. What hope for African primate diversity? African Journal of Ecology, 44 (2): 116-133.

Colyn, M. 1991. L'importance zoogéographique du bassin du fleuve Zaïre pour la spéciation: le cas des primates simiens. Annalen Zoologische wetenschappen edn. Koninklijk Museum voor Midden-Afrika. 264 pp.

Colyn, M., Gautier-Hion, A., and Thys, A. D. 1991. Cercopithecus dryas Schwarz 1932 and C. salongo Thys van den Audenaerde 1977 are the same species with an age-related coat pattern. Folia primatologica; international journal of primatology, 56 (3): 167.

Colyn, M. M. 1988. Distribution of guenons in the Zaïre-Lualaba-Lomami river system, in Gautier- Hion, A., (ed.), A Primate radiation : evolutionary biology of the African guenons. Cambridge University Press, Cambridge. 104-124.

DRC 2004. Arrêté n° 014/CAB/MIN/ENV/2004 relatif aux mesures d'exécution de la Loi n° 82-002 du 28 mai 1982 portant réglementation de la chasse, col. 24. Journal Officiel de la République du Congo 14Kinshasa, Cabinet du Président de la République.

Groves, C. P. 2005. Order Primates, in Wilson, D. E. & Reeder, D. M., (eds.), Mammal species of the world: a taxonomic reference. Third Ed. John Hopkins University Press, Baltimore. 111-184.

Hart, J., Butynski, T. M., and Hurley, M. 2008. Cercopithecus dryas. In: IUCN 2011. IUCN Red List of Threatened Species. Version 2001.1. URL: www.iucnredlist.org Accessed: 17-8-2011.

Kuroda, S., Kano, T., and Muhindo, K. 1985. Further information on the new monkey species, Cercopithecus salongo Thys van den Audenaerde, 1977. Primates, 26 (3): 325-333.

Lernould, J.-M. 1988. Classification and geographical distribution of guenons: a review, in Gautier- Hion, A., (ed.), A Primate radiation : evolutionary biology of the African guenons. Cambridge University Press, Cambridge. 54-78.

Lokasola, A. 2008. First field study of the Salongo Monkey (Cercopithecus dryas), Kokolopori Bonobo Reserve, DRC, The International Primatological Society.XXII Congress.3-8 August 2008., Edinburgh, p. 144.

Murhabale, B. 2011. Biodiversity of Cercopithecidae primates of the Congo basin: taxonomic status and Ecology of conservation. Congo Network Workshop Kisangani 12-14 May 2011.

Oates, J. F. and IUCN/SSC Primate Specialist Group 1996. African Primates: Status Survey and Conservation Action Plan. IUCN: Gland, Switzerland. 88 pp.

7 Cercopithecus dryas

Paniscus. n.d. Les Mammifères du biotope des bonobos URL: http://www.pan- paniscus.org/biodiversite/mammiferes.php Accessed: 5-9-2011.

Sarmiento, E. 2000. The taxonomic status of Cercopithecus dryas and Cercopithecus salongo. African Primates, 4 (1-2): 65-67.

Seyler, J. R., Thomas, D., Mwanza, N., and Mpoyi, A. 2010. Democratic Republic of Congo: biodiversity and tropical forestry assessment (118/119).Final report. USAID. 175 pp.

Takeda, J. 1996. The Ngandu as Hunters in the Zaire River Basin. African Study Monographs, Supplementary issue (23): 1-61.

Van Krunkelsven, E., Bila Isia, I., and Draulans, D. 2000. A survey of bonobos and other large mammals in the Salonga National Park, Democratic Republic of Congo. Oryx, 34 (3): 180-187.

WHC. 2011. List of World Heritage in danger URL: http://whc.unesco.org/en/danger/ World Heritage Convention. Accessed: 5-9-2011.

Wilkie, D. S. and Carpenter, J. F. 1999. Bushmeat hunting in the Congo Basin: an assessment of impacts and options for mitigation. Biodiversity and Conservation, 8 (7): 927-955.

Wilson, D. E. and Reeder, D. M. 2005. Mammal species of the world - a taxonomic and geographic reference. 3rd edn. The Johns Hopkins University Press, Baltimore.

Wright, P. C. and Jernvall, J. 1999. The future of primate communities: a reflection of the present, in Fleagle, J. G., Janson, C., & Reed, K., (eds.), Primate Communities. Cambridge University Press, Cambridge. 295-309.

8 Eryx tataricus

REVIEW OF SPECIES SELECTED ON THE BASIS OF THE 2011 QUOTA ANALYSIS

REPTILIA

SPECIES: Eryx tataricus

SYNONYMS: Boa tatarica, Eryx speciosus

COMMON NAMES: Grote zandboa (Dutch), Tartary Sand Boa (English), Boa des sables de Tatarie (French), tatarisk sandboa (Swedish)

RANGE STATES: , People’s Republic of , Islamic Republic of , Kazakhstan, Kyrgyzstan, Mongolia, Pakistan, Tajikistan, , Uzbekistan

RANGE STATE UNDER REVIEW: Uzbekistan

IUCN RED LIST: Not evaluated

PREVIOUS EC OPINIONS: Current positive opinion for wild specimens from Uzbekistan first applied on 05/09/2002 and last confirmed on 20/06/2011.

TRADE PATTERNS: Eryx tataricus from Uzbekistan was selected on the basis of an increased quota in 2011 from 300 live individuals in 2010 to 600 in 2011. Uzbekistan was the main global direct exporter of wild-sourced E. tataricus 2000-2009. The majority of global direct exports of the species from all countries 2000-2009 consisted of live, wild-sourced specimens exported for commercial purposes (totalling 590 individuals, of which 50 were imported by the EU-27, according to exporter-reported figures). Annual export quotas for wild-sourced E. tataricus from Uzbekistan have been established since 2000. Trade appears to have remained within quota (Table 1). Direct trade from Uzbekistan to the EU-27 between 2000 and 2009 consisted entirely of live individuals exported for commercial purposes. According to Uzbekistan and its trading partners respectively, a total of 81 and 190 live E. tataricus were exported to the EU-27 2000-2009 (Table 2), of which 50 and 190 specimens, respectively, were wild sourced; the remaining exports reported by Uzbekistan were ranched. The only reported indirect trade to the EU-27 of E. tataricus originating in Uzbekistan 2000-2009 consisted of live, wild-sourced specimens re-exported by the Russian Federation to Germany for commercial purposes, amounting to 60 specimens in 2004 and 40 specimens in 2005 (all reported by Germany).

9 Eryx tataricus

Direct exports of E. tataricus from Uzbekistan to countries other than the EU-27 2000-2009 consisted entirely of live specimens, with the United States of America being the main importer. Wild-sourced individuals made up 100 per cent of exports according to importer-reported data, but only 91 per cent of exports according to exporter-reported data, with the remaining 9 per cent comprising ranched individuals (Table 3). Table 1. CITES export quotas for wild Eryx tataricus from Uzbekistan and global exports, reported by the importers and by the exporter 2000 2001 2002 2003 2004 2005 2006 2007 2008 2009

Quota 50 50 300 300 300 300 300 300 1000 300

Reported by Importers 40 150 70 150 70

Reported by Uzbekistan 50 50 40 150 100 207

Table 2. Direct exports of Eryx tataricus from Uzbekistan to the EU-27, 2000-2009. All trade was for commercial purposes and involved live specimens. Importer Source Reported by 2003 2005 2006 2007 Total

Czech Republic R Importer

Exporter 11 11

Germany R Importer

Exporter 20 20

W Importer 20 50 70 140

Exporter

United Kingdom W Importer 50 50

Exporter 50 50

Table 3. Direct exports of Eryx tataricus from Uzbekistan to countries other than the EU-27, 2000-2009. All trade involved live specimens. Purpose Source Reported by 2000 2001 2002 2003 2004 2005 2006 2009 Total

P W Importer

Exporter 7 7

T R Importer

Exporter 50 2 52

W Importer 40 100 50 100 290

Exporter 50 50 40 100 100 200 540

CONSERVATION STATUS in range state: Eryx tataricus is the second largest species of sand boa, reaching 91 cm (females) and 61 cm (males) (Jones, 2006). It was reported to be rare in captivity, but Jones (2006) considered that due to its “attractiveness and good disposition” it was set to become more popular and readily available in the future. Eryx tataricus speciosus was reportedly sought after by many enthusiasts, and Jones (2006) commented that he had a long waiting list of people wanting the subspecies, even at the relatively high prices dictated by short supply and high demand. Captive breeding of the species was reported to be relatively simple (Jones, 2006).

10 Eryx tataricus

The species was reported to be widely distributed in central and eastern Kazakhstan, Kyrgyzstan, Tajikistan, Uzbekistan, eastern Turkmenistan, the Islamic Republic of Iran, Afghanistan, Pakistan, north- western India, western People’s Republic of China and in Southern Mongolia (Ananjeva et al., 2006). McDiarmid et al. (1999), however, did not list India as a range State. Harrison (2003) noted that determining the natural range of E. tataricus is complicated due to the difficulty some authors have had defining the taxon. Of the three subspecies recognised by McDiarmid (1999) (E. t. tataricus, E. t. speciosus and E. t. vittatus), two were regarded by some authors as distinct species (E. tataricus and E. vittatus) (Tokar, 1989; Ananjeva et al., 2006). Some authors referred the forms from Inner Mongolia and Southern Gobi to E. miliaris (Ananjeva et al., 2006). In addition, Harrison (2003) noted that some authors have had difficulty distinguishing E. tataricus from both E. miliaris and E. jaculus. Eryx tataricus was included in the national Red Data Books/Red lists of Mongolia (Terbish et al., 2006), Kyrgystan (Milko & Panfilov, 2006 cited by Harrison, 2003) and Turkmenistan (1985, 1999 cited by Ananjeva et al., 2006). It was considered to occur sparsely and to be declining in Kyrgyzstan (Milko & Panfilov, 2006 cited by Harrison, 2003). In Mongolia the species was evaluated as Near Threatened (Terbish et al., 2006) due to habitat loss through mining, droughts and drying of water sources (Terbish et al., 2006). Uzbekistan: Amirkhanov (1987) reported the species as occurring in the following protected areas in Uzbekistan: Aral-Paigambar (common), Arnasansky (occurrence unconfirmed) and Nuratinsky (occurrence unconfirmed). McDiarmid et al. (1999) listed Uzbekistan as within the range of the species but provided no further information. Vashetko et al. (2003) reported the occurrence of the species in the Western Tian Shan (north-eastern Uzbekistan), including in the following localities: Chirchik, Karzhantau, Khodjikent, Handaylyk, Kaynar-sai, Aktas, Aksak-Ata, Nurekata, Sanganak and Kamchik- sai. Darevsky and Orlov (1988) reported that the species was uncommon in Uzbekistan. The species is not included in the Red Data Book for Uzbekistan (Azimov, 2003). No evidence was found that the species has any protection status in Uzbekistan. In 2002 when the annual export quota had been increased from 50 to 300 and the annual trade in the previous two years was 50 individuals, a positive opinion was formed. Eryx tataricus from Uzbekistan was reviewed in 2008 for SRG 45 when the annual export quota increased from 300 to 1000. However, the report was not discussed at that meeting or at later meetings. REFERENCES: Amirkhanov, A. M. Ed. 1987. Amphibians and in protected areas. Moscow. (In Russian). Ananjeva, N. B., Orlov, N. L., Khalikov, R. G., Darevsky, I. S., Ryabov, S. A., and Barabanov, A. V. 2006. The reptiles of northern Eurasia: taxonomic diversity, distribution, conservation status. Zoological Institute, Russian Academy of Sciences. Azimov, Zh. A. Ed. 2003. The Red Book of the Republic of Uzbekistan. Uzbekistan Academy of Sciences, Tashkent. (In Russian). Darevsky, I. S. and Orlov, N. L. 1988. Rare and endangered animals - reptiles and amphibians. Vyshaya Shkola, Moscow. (In Russian). Harrison, C. 2003. The Tatar Sand Boa (Eryx tataricus) URL: www.kingsnake.com/sandboa/tataricu.html Accessed: 31-8-2011. Jones, C. 2006. Breeding Eurasian Sand Boas (Eryx jaculus, Eryx miliaris and Eryx tataricus). Reptilia (34): 24-28. McDiarmid, R. W., Campbell, J. A., and T'Shaka, A. T. 1999. species of the world: a taxonomic and geographic reference. Herpetologists' League, Washington, DC.

11 Eryx tataricus

Terbish, Kh., Munkhbayar, Kh., Clark, E. L., Munkhbat, J., Monks, E. M., Munkhbaatar, M., Baillie, J. E. M., Borkin, L., Batsaikhan, N., Samiya, R., and Semenov, D. V. 2006. Mongolian Red List of reptiles and amphibians. Zoological Society of London, London. Tokar, A. A. 1989. The revision of the genus Eryx. Kiev. (In Russian). 55 pp. Vashetko, E. V., Chikin, Y. A., Khodzhaev, A. F., and Nuridzhanov, A. S. 2003. Herpetofauna of the western Tian Shan (Uzbekistan) [In Russian]. Modern Herpetology, 2: 24-38.

12 Hippocampus comes

REVIEW OF SPECIES SELECTED ON THE BASIS OF THE 2011 QUOTA ANALYSIS

ACTINOPTERYGII SYNGNATHIDAE

SPECIES: Hippocampus comes

COMMON NAMES: Tiger-tail Seahorse (English)

RANGE STATES: Indonesia, Malaysia, Philippines, Singapore, Thailand, Viet Nam

RANGE STATE UNDER REVIEW: Viet Nam

IUCN RED LIST: Vulnerable

PREVIOUS EC OPINIONS: Current Article 4.6(b) import suspension for wild specimens from Indonesia first imposed on 01/10/2007 and last confirmed on 07/09/2011. Previous negative opinion for wild specimens from Indonesia formed on 15/11/2005. TRADE PATTERNS: Hippocampus comes from Viet Nam was selected on the basis of a new 2011 quota of 12 000 live individuals, and on the basis of its Vulnerable status globally. Indonesia was the main global direct exporter of wild-sourced H. comes between its listing in 2004 in Appendix II and 2009, with a total of around 7000 and 12 000 wild-sourced live specimens exported from the country during this period, according to importers and the exporter, respectively. Direct trade from Viet Nam to the EU-27 2004-2009 consisted entirely of live, captive-born individuals traded for commercial purposes (Table 1). The majority of trade was to France, with the remainder to the United Kingdom. There was no reported indirect trade to the EU-27 of H. comes originating in Viet Nam. The only reported direct trade from Viet Nam to countries other than the EU-27 was in live individuals exported to the United States of America for commercial purposes (Table 2). Wild-sourced individuals made up 21 per cent of exports according to importer-reported figures, with most of the remainder being captive-born.

13 Hippocampus comes

Table 1. Direct exports of Hippocampus comes from Viet Nam to the EU-27, 2004-2009. All trade involved live, captive-born individuals traded for commercial purposes. Importer Reported by 2007 2008 2009 Total France Importer 3827 3827 Exporter 4350 4350 United Kingdom Importer 200 200 400 Exporter 1000 200 1200

Table 2. Direct exports of Hippocampus comes from Viet Nam to countries other than the EU-27, 2004-2009. All trade involved live individuals exported for commercial purposes. Source Reported by 2007 2008 2009 Total F Importer 152 1235 631 2018 Exporter 1800 2000 3500 7300 I Importer 57 57 Exporter W Importer 466 100 566 Exporter

TAXONOMIC NOTE It was noted that the species may be confused with Hippocampus kuda or H. spinosissimus (Lourie et al., 2004). CONSERVATION STATUS in range states H. comes was reported to occur in Indonesia (south Sumatra, south Kalimantan), Malaysia (Johor, Penang), Singapore, Thailand (west coast), Viet Nam (Khan Hoa) and the Philippines (Lourie et al., 2004; S. Lourie, unpublished data, in Morgan and Lourie, 2006). The habitat of adults was reported to be dominated by stony and hard corals, sponges (Morgan and Lourie, 2006) or seagrass, in beds with coral substrate (Morgan and Vincent, 2007). The habitat of the young was in reef-flat macroalgal beds (S. Morgan, unpublished data, in Morgan and Lourie, 2006). H. comes was found to inhabit shallow waters between the low tide line and depths of up to 10 m, with 20 m being the greatest depth the species had been recorded in (Kuiter, 2000; Lourie et al., 2004).

The maximum recorded adult height was reported to be 18.7 cm (Foster and Vincent, 2004) to 26.4 cm SLc (curved Standard Length) (Meeuwig and Lafrance, 2001; in Morgan and Lourie, 2006). The species was reported to reach maturity at about one year of age (Project Seahorse, 2002), with the height at first maturity 96 mm SLc for half the males, although reproduction in individuals smaller than 105 mm has not been confirmed (Morgan and Lourie, 2006). The frequency of reproduction was thought to be every 14 to 21 days (Morgan and Lourie, 2006), with a year round breeding season (Macansantos, unpubl. data, in Foster and Vincent, 2004). Each brood was found to lead to the release of about 400 young (Perante et al., 2002; Morgan and Lourie, 2006). The rate of reproduction was reported to be size dependant, with 45 per cent of males pregnant at 122 mm SLc (L. Brady, unpublished data, in Morgan and Lourie, 2006) and 90 per cent at >204 mm SLc (Morgan and Lourie, 2006). The life span of H. comes was estimated at between 2.6 to 3.7 years (Morgan and Lourie, 2006), but the rate of natural mortality was considered to be high (Meuwig, unpubl. data, in Foster and Vincent, 2004). However, the life history parameters were considered to be insufficiently known (Vincent et al., 2007).

14 Hippocampus comes

The Philippines, where the species was considered to be widely distributed (Morgan and Lourie, 2006), was reported to be the main range of the species (Project Seahorse, 2002). Greatest abundances were reported to occur in the central Philippines (Perante et al., 2002; A. Maypa, unpublished data., M. Pajaro, pers. comm. in Morgan and Lourie, 2006) However, Morgan and Lourie (2006) considered the abundances outside the Philippines to be unknown. Direct exploitation, by-catch and habitat destruction were considered to be major threats to Hippocampus spp., with 20 million specimens estimated to be traded annually in 1995 (Vincent, 1996) and higher numbers in the early 2000s (Salin et al., 2005; Giles et al., 2006). An estimated 95 per cent of specimens in trade were being used for traditional (Chinese) medicine (Vincent et al., 2011), but Hippocampus species were also found to be a suitable food source for human consumption (Lin et al., 2008). Fewer specimens were reported to be used for the live aquarium trade, however pressures on particular populations or species were considered substantial (Vincent et al., 2011). Foster and Vincent (2004) considered Hippocampus species likely to be vulnerable to fishing mortality, due to biological characteristics such as low fecundity and obligate parental care. These characteristics were thought to explain the markedly declining Hippocampus populations observed by fishermen and traders worldwide (Vincent, 1996). Project Seahorse (2002) considered H. comes may be particularly susceptible to decline. However, Martin-Smith et al. (2004) reported that the species recovered rapidly following the establishment of a no-take Marine Protected Area in Handumon in northern Bohol (Philippines). H. comes was reported to be traded for both Traditional Chinese Medicine (TMC) and for the live aquarium trade, with significant rates of exploitation observed in the central portion of its range (Morgan and Lourie, 2006). However, specimens were also considered threatened through by-catch and habitat degradation (Project Seahorse, 2002). Morgan and Lourie (2006) reported that threats outside the Philippines remained unknown, but suggested that similar pressures may apply elsewhere. Vincent et al. (2007) reported that the Hippocampus fishery in central Philippines appeared severely depleted. H. comes was found to be among the most commonly traded Hippocampus species and such evidence of declines in seahorse availability were considered to be disconcerting (Vincent, 1996) for this species (Project Seahorse, 2002). The species was classified as Vulnerable by the IUCN, on the basis of the substantial trade and by-catch affecting the species, inferred declines of 30-50 per cent and habitat loss (Project Seahorse, 2002). Following recommendations made by the Animals Committee at its 20th meeting, a minimum height limit of 10 cm was introduced for the international trade in wild Hippocampus specimens (CITES Secretariat, 2004). The application of a minimum size limit for wild specimen in international trade was later made voluntary and it was recommended to use other ways to make non-detriment findings (CITES Secretariat, 2005). Koldewey and Martin-Smith (2010) reported that aquaculture was not yet able to produce sufficient Hippocampus specimens to cover market demands. However, Job et al. (2006) considered H. comes to be a suitable species for aquaculture, due to its popularity and its relatively high survival rate (90 per cent) and rapid growth in aquaculture. Viet Nam: The species presence in Viet Nam has been confirmed from Khan Hoa [south central Viet Nam], where the species was considered to be rare (Lourie et al., 1999). Viet Nam, along with India, Indonesia, Philippines and Thailand, was reported to be one of the top five producers of dried Hippocampus spp. in the world (Project Seahorse, unpubl. data, in Giles et al., 2006), with the majority of Hippocampus specimens thought to be sourced from trawl by-catch (Giles et al., 2006). Targeted fisheries were reported to be limited (Giles et al., 2006) and daily catch rates were considered to be low (Giles et al., 2006). Annual by-catch of Hippocampus specimens was estimated at about 2.2 million specimens in the five coastal provinces of Vietnam (Giles et al., 2006) and Vincent (1996) estimated the annual trade of Hippocampus spp. in Viet Nam to amount to five tonnes (dry weight), with data pointing at reductions in size of specimens and population declines. Most specimens were reported to be exported

15 Hippocampus comes into China, “generally through unofficial and unregulated channels” (Giles et al., 2006). However, internal trade in “seahorse tonic” was also reported to exist (CITES Secretariat, 2002). Meeuwig et al. (2006) observed that H. spinosissimus and H. trimaculatus were caught in highest numbers and assumed that H. comes’ being caught in lower numbers was due to differences in habitat (shallower water and/or coral reef habitat). Job (pers. obs., in Job et al., 2006) considered the species highly exploited in Viet Nam. Catches of Hippocampus specimens were reported to have declined, according to fishers and buyers surveyed (Giles et al., 2006), however Vincent (1996) considered the destruction of habitat a possibly larger threat than trade. Viet Nam, where the species was thought to have been bred successfully since 2006, was reported to presently be the only country where the species was being bred in captivity (FAO, 2010). However, concerns were raised over the effects of capture of broodstock on the recruitment population and on the possibility of disease transfer from the juveniles released back to the wild (FAO, 2010). REFERENCES: CITES Secretariat. 2002. Consideration of proposals for amendment of Apendices I and II. Prop. 12.37. URL: http://www.cites.org/eng/cop/12/prop/E12-P37.pdf Accessed 8-2-2008. CITES Secretariat. 2004. Notification to the Parties No. 2004/033. Trade in seahorses. Implementation of Decision 12.54. CITES Secretariat. 2005. Notification to the Parties No. 2005/014. Trade in seahorses. FAO. 2010. Cultured Aquatic Species Information Programme. Hippocampus comes. FAO Fisheries and Aquaculture Department. Text by Ky, T.S. URL: http://www.fao.org/fishery/culturedspecies/Hippocampus_comes/en Accessed: 30-8-2011. Foster, S. J. and Vincent, A. C. J. 2004. Life history and ecology of seahorses: implications for conservation and management. Journal of Fish Biology, 65: 1-61. Giles, B. G., Ky, T. S., Hoang, D. H., and Vincent, A. C. J. 2006. The catch and trade of seahorses in Vietnam. Biodiversity and Conservation, 15 (8): 2497-2513. Job, S., Buu, D., and Vincent, A. 2006. Growth and survival of the tiger tail seahorse, Hippocampus comes. Journal of the World Aquaculture Society, 37 (3): 322-327.

Koldewey, H. J. and Martin-Smith, K. M. 2010. A global review of seahorse aquaculture. Aquaculture, 302 (3-4): 131-152. Kuiter, R. H. 2000. Seahorses, Pipefishes and their Relatives: a comprehensive guide to Sygnathiformes. TMC Publishing, Chorleywood, UK. Lin, Q., Lin, J., Lu, J., and Li, B. 2008. Biochemical composition of six seahorse species, Hippocampus sp., from the Chinese coast. Journal of the World Aquaculture Society, 39 (2): 225-234. Lourie, S. A., Foster, S. J., Cooper, E. W. T., and Vincent, A. C. J. 2004. A guide to the identification of seahorses. Project Seahorse and TRAFFIC North America. Lourie, S. A., Pritchard, J. C., Casey, S. P., Truong, A. K., Hall, H. J., and Vincent, A. C. J. 1999. The taxonomy of Vietnam's exploited seahorses (family Syngnathidae). Biological Journal of the Linnean Society, 66: 231-256. Martin-Smith, K. M., Samoilys, M. A., Meeuwig, J. J., and Vincent, A. C. J. 2004. Collaborative development of management options for an artisanal fishery for seahorses in the central Philippines. Ocean & Coastal Management, 47 (3-4): 165-193. Meeuwig, J. J., Hoang, D. H., Ky, T. S., Job, S. D., and Vincent, A. C. J. 2006. Quantifying non-target seahorse fisheries in central Vietnam. Fisheries Research, 81 (2-3): 149-157.

16 Hippocampus comes

Meeuwig, J. J. and Lafrance, P. 2001. Summary of Hippocampus comes biology. Identifying management guidelines for small-scale fisheries using Hippocampus comes as a case study. White Point, Nova Scotia, McGill University. Morgan, S. and Lourie, S. 2006. Threatened fishes of the world: Hippocampus comes Cantor 1850 (Syngnathidae). Environmental Biology of Fishes, 75 (3): 311. Morgan, S. K. and Vincent, A. C. J. 2007. The ontogeny of habitat associations in the tropical tiger tail seahorse Hippocampus comes Cantor, 1850. Journal of Fish Biology, 71 (3): 701-724. Perante, N. C., Pajaro, M. G., Meeuwig, J. J., and Vincent, A. C. J. 2002. Biology of a seahorse species, Hippocampus comes in the central Philippines. Journal of Fish Biology, 60 (4): 821-837. Project Seahorse. 2002. Hippocampus comes. In: IUCN 2011. IUCN Red List of Threatened Species. Version 2011.1 URL: www.iucnredlist.org Accessed: 30-8-2011. Salin, K. R., Yohannan, T. M., and Mohanakumaran 2005. Fisheries and trade of seahorses, Hippocampus spp., in southern India. Fisheries Management & Ecology, 12 (4): 269. Vincent, A., Foster, S., and Koldewey, H. 2011. Conservation and management of seahorses and other Syngnathidae. Journal of Fish Biology, 78 (6): 1681-1724. Vincent, A. C. J. 1996. The international trade in seahorses. Cambridge, United Kingdom, TRAFFIC International. Vincent, A. C. J., Meeuwig, J. J., Pajaro, M. G., and Perante, N. C. 2007. Characterizing a small-scale, data- poor, artisanal fishery: Seahorses in the central Philippines. Fisheries Research, 86 (2-3): 207-215.

17 Hippocampus kelloggi

REVIEW OF SPECIES SELECTED ON THE BASIS OF THE 2011 QUOTA ANALYSIS

ACTINOPTERYGII SYNGNATHIDAE

SPECIES: Hippocampus kelloggi

SYNONYMS: Hippocampus suezensis

COMMON NAMES: Kellog's zeepaardje (Dutch), Great Seahorse (English), Kellog's Seahorse (English), Offshore Seahorse (English), O-umi-uma (Japanese)

RANGE STATES: Australia, China, India, Indonesia, Japan, Malaysia, Pakistan, Philippines, Taiwan, Province of China, Thailand, United Republic of Tanzania, Viet Nam

RANGE STATE UNDER REVIEW: Viet Nam

IUCN RED LIST: Data Deficient

PREVIOUS EC OPINIONS: Current Article 4.6(b) import suspension for wild specimens from Indonesia first imposed on 03/09/2008 and last confirmed on 07/09/2011. Previous negative opinion for wild specimens from Indonesia formed on 26/09/2006.

TRADE PATTERNS: Hippocampus kelloggi from Viet Nam was selected on the basis of a new 2011 quota of 7000 live wild individuals and on the basis of its globally Data Deficient status. Thailand was the main global direct exporter of H. kelloggi since its listing in CITES Appendix II in 2004 up to 2009. Exports from the country during this period comprised a total of around 11 000 kg of bodies and 300 bodies (reported without units) according to the importers, and 16 000 kg of bodies and 2000 bodies (reported without units) according to Thailand, all of which were wild-sourced. There has been no reported direct or indirect trade in H. kelloggi originating in Viet Nam to the EU-27 since its listing in Appendix II in 2004. Direct exports from Viet Nam to countries other than the EU-27, 2004-2009 consisted of bodies and live individuals traded for commercial purposes, with the United States of America being the main importer

18 Hippocampus kelloggi

(Table 1). Wild-sourced individuals made up 99 per cent of importer-reported trade, the remainder being captive-born, and 100 per cent of exports reported by Viet Nam were wild-sourced. Table 1. Direct exports of Hippocampus kelloggi from Viet Nam to countries other than the EU-27, 2004-2009. All trade was for commercial purposes. Importer Term Source Reported by 20052006 2007 2009 Total Taiwan, Province of China bodies W Importer Exporter 1860 1860 United States of America live F Importer 150 150 Exporter W Importer 9677 3322 200 13199 Exporter 12124 350 12474

TAXONOMIC NOTE Several taxonomic revisions of the genus Hippocampus, including Hippocampus kelloggi, were reported to have taken place (Lourie et al., 1999b) and Lourie et al. (2004) considered the identification of H. kelloggi to be difficult, due to the species’ variable and less distinctive character, as well as morphological similarity to H. algiricus, H. ingens, H. kuda and H. spinosissimus. CONSERVATION STATUS in range states H. kelloggi was reported to occur from the western and eastern Indian Ocean to the north-western and western central Pacific, with occurrence in the south-western Pacific considered uncertain (Project Seahorse, 2002). The species’ range was considered to be relatively wide, with reports from Zanzibar (Tanzania), Pakistan, India, southeast , and north to China and Japan (Project Seahorse, 2002). The species was found to be associated with gorgonian corals and sea whips (Lourie et al., 2004) and reported to occur in areas with soft bottom sea floor (Kuiter, 2000). H. kelloggi was reported to occur in deeper water (Meeuwig et al., 2006), with the maximum reported depth 152 m (Lourie et al., 2004). The maximum recorded adult height was reported to be about 28 cm (Kuiter, 2000), with the height at first maturity being 15 cm (Lourie et al., 1999a; in Foster and Vincent, 2005). The life history of this species was considered to be virtually unknown (Lourie et al., 2004). The species was classified as Data deficient by the IUCN (Project Seahorse, 2002), as although trade levels were considered to be high, the proportion of the population represented in this trade was unknown. However, the species was reported to be rarely caught by targeted fisheries (Lourie unpubl. data, Pajaro unpubl. data, in Project Seahorse, 2002) or in trawls (Pajaro unpubl. data, in Project Seahorse, 2002) and its distribution range was considered to be wide (Project Seahorse, 2002). Direct exploitation, by-catch and habitat destruction were considered to be major threats to Hippocampus spp., with 20 million specimens estimated to be traded annually in 1995 (Vincent, 1996) and higher numbers in the early 2000s (Salin et al., 2005; Giles et al., 2006). An estimated 95 per cent of specimens in trade were reported to be used for Traditional (Chinese) Medicine (Vincent et al., 2011), but Hippocampus species were also found to be a suitable food source for human consumption (Lin et al., 2008). Fewer specimens were reported to be used for the live aquarium trade, however pressures on particular populations or species were considered substantial (Vincent et al., 2011). Foster and Vincent (2004) considered Hippocampus species likely to be vulnerable to fishing mortality, due to biological characteristics such as low fecundity and obligate parental care. These characteristics were thought to explain the markedly declining Hippocampus populations observed by fishermen and traders worldwide (Vincent, 1996). Project Seahorse (2002) considered data on H. kelloggi to be extremely limited, but noted that they were not aware of any information on declines in numbers for the species or any subpopulations.

19 Hippocampus kelloggi

H. kelloggi was reported to be traded for use in traditional medicine, as curios (dried) and live for aquarium and hobbyist use (Lourie et al., 2004). The relatively large size of the species, and the smooth texture and pale complexion of dried specimens, were reported to be the reasons for the high demand (Lourie unpubl. data, Pajaro unpubl. data, in Project Seahorse, 2002). However, the proportion of the population exploited was considered unknown (Project Seahorse, 2002). Following recommendations made by the Animals Committee at its 20th meeting, a minimum height limit of 10 cm was introduced for the international trade in wild Hippocampus specimens (CITES Secretariat, 2004). Foster and Vincent (2005) however pointed out that this restriction would not protect H. kelloggi from overexploitation, as the height at first maturity is well above 10 cm. The application of a minimum size limit for wild specimen in international trade was later made voluntary and it was recommended to use other ways to make non-detriment findings (CITES Secretariat, 2005). Range States were reported to provide varying levels of protection to H. kelloggi (Foster, 2008). Koldewey and Martin-Smith (2010) did not clarify whether this species was being bred in captivity anywhere, however they reported that aquaculture was not yet able to produce sufficient Hippocampus specimens to cover market demands. Viet Nam: The species occurrence was confirmed in the Gulf of Tonkin (Nguyen, 1993; in Nguyen and Do, 1998), Quang Nam-Da Nang, Khanh Hoa and Binh Thuan provinces (Lourie et al., 1999b). H. kelloggi was reported to be included as Vulnerable in the Viet Nam Red Data Book (Ministry of Science, 1992; in Giles et al., 2006), although Lourie et al. (1999b) pointed out that the species appeared to have been misidentified or synonymised as H. trimaculatus. Giles et al. (2006) noted that little was known on the status of Hippocampus populations in Viet Nam, or on the nature and size of the trade. Viet Nam, along with India, Indonesia, Philippines and Thailand, was reported to be one of the top five producers of dried Hippocampus spp. in the world (Project Seahorse, unpubl. data, in Giles et al., 2006), with the majority of Hippocampus specimens thought to be sourced from trawl by-catch (Giles et al., 2006). Targeted fisheries were reported to be limited (Giles et al., 2006) and daily catch rates were considered to be low (Giles et al., 2006). Annual by-catch of Hippocampus specimens was estimated at about 2.2 million specimens in the five coastal provinces of Vietnam (Giles et al., 2006) and Vincent (1996) estimated the annual trade of Hippocampus spp. in Viet Nam to amount to five tonnes (dry weight), with data pointing at reductions in size of specimens and population declines. Most specimens were reported to be exported into China, “generally through unofficial and unregulated channels” (Giles et al., 2006). However, internal trade in “seahorse tonic” was also reported to exist (CITES Secretariat, 2002). Catches of Hippocampus specimens were reported to have declined, according to fishers and buyers surveyed (Giles et al., 2006), however Vincent (1996) considered the destruction of habitat a possibly larger threat than trade. Combined landings of H. kelloggi and H. histrix accounted for less than 1 per cent of the by-catch observed in landings of the Cua Be fishing fleet (small fishing community located on the Central Coast and reported to be a major source for Hippocampus specimens), between 1996 and 2000 (Meeuwig et al., 2006). This was thought to be due to H. kelloggis’ occurrence in deeper water than targeted by the trawling, rather than to be reflecting the species abundance (Meeuwig et al., 2006). Additional information has been sought from the country in the context of the Review of Significant Trade process, and this information will be made available in 2012 at the 26th meeting of the Animals Committee. REFERENCES: CITES Secretariat. 2002. Consideration of proposals for amendment of Apendices I and II. Prop. 12.37. URL: http://www.cites.org/eng/cop/12/prop/E12-P37.pdf Accessed 8-2-2008.

20 Hippocampus kelloggi

CITES Secretariat. 2004. Notification to the Parties No. 2004/033. Trade in seahorses. Implementation of Decision 12.54. CITES Secretariat. 2005. Notification to the Parties No. 2005/014. Trade in Seahorses. Foster, S. 2008. Case Study: Hippocampus spp. Project Seahorse. NDF Workshop Case Studies, WG8 - Fishes, Case Study 4, Mexico 2008. Foster, S. J. and Vincent, A. C. J. 2005. Enhancing sustainability of the international trade in Seahorses with a single minimum size limit. Conservation Biology, 19 (4): 1044. Giles, B. G., Ky, T. S., Hoang, D. H., and Vincent, A. C. J. 2006. The catch and trade of seahorses in Vietnam. Biodiversity and Conservation, 15 (8): 2497-2513. Koldewey, H. J. and Martin-Smith, K. M. 2010. A global review of seahorse aquaculture. Aquaculture, 302 (3-4): 131-152. Kuiter, R. H. 2000. Seahorses, Pipefishes and their Relatives: a comprehensive guide to Sygnathiformes. TMC Publishing, Chorleywood, UK. Lin, Q., Lin, J., Lu, J., and Li, B. 2008. Biochemical composition of six seahorse species, Hippocampus sp., from the Chinese coast. Journal of the World Aquaculture Society, 39 (2): 225-234. Lourie, S. A., Foster, S. J., Cooper, E. W. T., and Vincent, A. C. J. 2004. A guide to the identification of seahorses. Project Seahorse and TRAFFIC North America. Lourie, S. A., Vincent, A. C. J., and Hall, H. J. 1999a. Seahorses: an identification guide to the world's species and their conservation. Project Seahorse, London, UK. Lourie, S. A., Pritchard, J. C., Casey, S. P., Truong, A. K., Hall, H. J., and Vincent, A. C. J. 1999b. The taxonomy of Vietnam's exploited seahorses (family Syngnathidae). Biological Journal of the Linnean Society, 66: 231-256. Meeuwig, J. J., Hoang, D. H., Ky, T. S., Job, S. D., and Vincent, A. C. J. 2006. Quantifying non-target seahorse fisheries in central Vietnam. Fisheries Research, 81 (2-3): 149-157. Ministry of Science, T. a. E. 1992. Red Data Book of Viet Nam. Volume 1. Animals. Science and Technology Publishing House, Hanoi. Nguyen, K. H. 1993. The Marine Fishes of Vietnam. 2(3), 10-14. Ha Noi, Scientific and Technical Public House. Nguyen, V. L. and Do, H. H. 1998. Biological parameters of two exploited seahorse species in a Vietnamese fishery, in Morton, B., (ed.), The Marine Biology of the South China Sea III. Third International Conference on the Marine Biology of the South China Sea. Hong Kong University Press, Hong Kong. 449-464. Project Seahorse. 2002. Hippocampus kelloggi. In: IUCN 2011. IUCN Red List of Threatened Species. Version 2011.1. URL: www.iucnredlist.org Accessed: 23-8-2011. Salin, K. R., Yohannan, T. M., and Mohanakumaran 2005. Fisheries and trade of seahorses, Hippocampus spp., in southern India. Fisheries Management & Ecology, 12 (4): 269. Vincent, A., Foster, S., and Koldewey, H. 2011. Conservation and management of seahorses and other Syngnathidae. Journal of Fish Biology, 78 (6): 1681-1724. Vincent, A. C. J. 1996. The international trade in seahorses. Cambridge, United Kingdom, TRAFFIC International.

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