Review of Species Selected on the Basis of a New Or Increased Export Quota in 2009

Home , Blue coral, Coral bleaching, Euphyllia ancora, Galaxea, Galaxea astreata, Madrepora

Review of species selected on the basis of a new or increased export quota in 2009

(Version edited for public release)

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

May, 2009

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

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CITATION UNEP-WCMC. 2009. Review of species selected on the basis of a new or increased export quota in 2009. UNEP-WCMC, Cambridge.

Table of Contents

1. Introduction ...... 4 2. Update since SRG 47 ...... 4 3. Species reviews ...... 5 SPECIES: Cordylus regius ...... 5 SPECIES: Euphyllia ancora ...... 7 SPECIES: Galaxea astreata ...... 14 SPECIES: Heliopora coerulea ...... 22 SPECIES: Pectinia lactuca ...... 30

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 Animals and Plants Committees. In general, there is no specific requirement in the text of the Convention to establish quotas to limit the trade in CITES-listed species. However, quotas should be established for meat and caviar of Acipenseriformes species from stocks shared between different Range States [Resolution Conf. 12.7 (Rev. CoP14)]. When a country sets its own national export quotas for CITES species, it should inform the Secretariat [see Resolution Conf. 12.3 (Rev. CoP14) ], 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); however, since 2008 sturgeon quotas have related to a quota year (1 March to 28 February). The CITES export quotas for sturgeon were initially published on the CITES website ( www.cites.org ) on 02/03/2009. Quotas for other species were initially published on 04/03/2009 and were updated on 10/03/2009, 03/04/2009, 09/04/2009 and 04/05/2009. Based on the quotas that were available on 11/03/2009, UNEP-WCMC analysed the 2009 CITES export quotas to identify: a) Quotas that were newly established in 2009; b) Quotas that increased or decreased in 2009 compared with 2008 quotas. This analysis was presented at the 47th Meeting of the SRG on 12/03/2009. Five species/country combinations were selected for review where the new or increased quota in 2009 indicated that further discussion 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: • Cordylus regius /Mozambique: New quota of 500 live specimens. Mozambique is not a known range State of this species. • Euphyllia ancora / Indonesia: Quota increased from 28,800 to 32,000 wild-taken pieces. Globally Vulnerable. • Galaxea astreata / Indonesia: Quota increased from 5,040 to 5,432 wild-taken pieces. Globally Vulnerable • Heliopora coerulea / Indonesia: Quota increased from 2,250 to 2,425 wild-taken pieces. Globally Vulnerable. • Pectinia lactuca / Indonesia: Quota increased from 2,250 to 2,500 wild-taken pieces. Globally Vulnerable.

1.1. Trade data Trade data included in this report were downloaded from the UNEP-WCMC CITES Trade Database on 16/04/2009.

2. Update since SRG 47 Since the analysis of CITES export quotas was undertaken in March, 2009, additional CITES export quotas have been published on the CITES website. Of particular note were: - Indonesia established 2009 quotas for a number of coral species around 10% higher than the 2008 quotas. - The 2009 Indonesia quota for Cibotium barometz increased by 100% on the 2008 quota, from 450 kg to 900 kg (dry weight, in the form of ‘hairs’, etc.). - The 2009 Indonesia quota for Gonystylus bancanus increased by 35% on the 2008 quota, from 5,909 m 3 to 8,000 m 3.

3. Species reviews

REVIEW OF SPECIES SELECTED ON THE BASIS OF A NEW OR INCREASED EXPORT QUOTA IN 2009

REPTILIA CORDYLIDAE

SPECIES: Cordylus regius

SYNONYMS: Cordylus warreni regius

COMMON NAMES: Regal Girdled Lizard (English)

RANGE STATES: Zimbabwe

RANGE STATE UNDER REVIEW: Mozambique

IUCN RED LIST: Not evaluated

PREVIOUS EC OPINIONS: No previous opinions formed

TRADE PATTERNS: Cordylus regius from Mozambique was selected for review on the basis of a new quota of 500 live specimens combined with the fact that Mozambique is not a known range State of this species. No trade in Cordylus regius from Mozambique has been reported. CONSERVATION STATUS in range states C. regius was reported to occur in southeast Mutare District, eastern Zimbabwe (Branch, 1998; Broadley, 2006), where it was reported to inhabit rock outcrops in open savannah (Branch, 1998). Welch (1982) also reported the species’ occurrence in southern Zimbabwe. Mozambique: No evidence was found for the occurrence of C. regius in Mozambique. Mozambique is not listed as a range State for C. regius in the CITES standard reference for Cordylus (Broadley, 2006).

C. regius was reported to be closely related to C. mossambicus , which occurs in the Gorongosa Mountains of Mozambique and in the lower slopes of the Chimanimani Mountains in Zimbabwe (Branch, 1998). Breeding males of both species were described as having blackish backs with bright orange to yellow flanks, and females were described as having dark brown backs with C. regius having yellowish brown flanks and C. mossambicus having grey brown flanks (Branch, 1998) – hence their appearance is similar. C. mossambicus was also reported to closely resemble C. regius on Le Monde des Cordylus (2006).

Mozambique has had an annual quota of 500 live C. mossambicus between 2003 and 2008, which increased to 1500 in 2009. Imports of this species to the EU from Mozambique have been suspended since 2006, following a negative opinion formed in 2004. Imports to the EU from Mozambique of two other species of Cordylus , C. tropidosternum and C. vittifer, are also suspended.

REFERENCES: Branch, B. 1998. Field guide to snakes and other reptiles of southern Africa. Struik Publishers Ltd, Cape Town. Broadley, D. G. 2006. CITES standard reference for the species of Cordylus (Cordylidae, Reptilia) compiled by Donald G. Broadley at the request of the CITES Nomenclature Committee. Update 2006 URL: http://www.cites.org/common/docs/Res/12_11/Cordylus_CoP14_update.pdf Le Monde des Cordylus. 2006. Fiche du Cordylus warreni mossambicus URL: http://cordyles.canalblog.com/archives/fiche_warreni_mossambicus_/index.html Accessed: 5-5- 2009. Welch, K. R. G. 1982. Herpetology of Africa: a checklist and bibliography of the orders Amphisbaenia, Sauria, and Serpentes. RE Krieger Pub. Co., Malabar, Florida.

REVIEW OF SPECIES SELECTED ON THE BASIS OF A NEW OR INCREASED EXPORT QUOTA IN 2009

ANTHOZOA CARYOPHYLLIIDAE

SPECIES: Euphyllia ancora

SYNONYMS: -

COMMON NAMES: Anchor Coral (English), Hammer Coral (English)

RANGE STATES: Australia (?), British Indian Ocean Territory, Indonesia, Japan, Malaysia, New Caledonia, Papua New Guinea, Philippines, Solomon Islands, Taiwan, Province of China, Thailand, Viet Nam,

RANGE STATE UNDER REVIEW: Indonesia

IUCN RED LIST: Vulnerable

PREVIOUS EC OPINIONS: A current positive opinion for Indonesia is in place, formed on 15/05/2002. A negative opinion was previously in place for Indonesia, formed on 11/07/2000.

TRADE PATTERNS: Euphyllia ancora from Indonesia was selected for review on the basis of an increased export quota for wild specimens in 2009 combined with its globally Vulnerable status. The published quota of 27,550 live specimens had remained constant from 2003 to 2007 increased in 2008 to 28,880 and further increased to 32,000 in 2009. Trade has been within quota for all years, according to exporters’ data. The apparent quota excess according to importers’ data in 2005, Table 4) was the result of trade on export permits issued in 2004 being imported in 2005. The major importing countries in the EU were France, Germany, Italy, Netherlands, Spain and United Kingdom and most trade was directly from Indonesia. Outside of the EU, the main importer was the United States with lesser quantities imported by Canada, Hong Kong S.A.R. and Japan. Indonesia has not submitted export quotas for maricultured corals to the CITES Secretariat for 2009. Table 1. Direct exports of Euphyllia ancora from Indonesia to EU 27, 2002-2007. All trade was in live wild specimens.

Importer Purpose Reported by 2002 2003 2004 2005 2006 2007 Total

Austria T Importer 10 84 94

Exporter 10 10 28 119 167

Belgium T Importer 23 20 201 244

Exporter 34 20 201 255

Importer Purpose Reported by 2002 2003 2004 2005 2006 2007 Total

Cyprus T Importer 5 5

Exporter

Czech Republic T Importer 27 40 53 70 52 130 372

Exporter 60 70 30 58 105 139 462

Denmark T Importer 86 62 46 88 65 347

Exporter 25 86 78 66 93 50 398

Estonia T Importer 9 9

Exporter 11 11

Finland T Importer 63 6 10 79

Exporter 13 10 10 33

France T Importer 558 930 958 1086 998 1122 5652

Exporter 185 1276 1087 850 960 1059 5417

Germany Q Importer

Exporter 30 30

T Importer 383 1325 1484 1267 1070 2164 7693

Exporter 735 1522 1383 1197 1032 2175 8044

Greece T Importer 10 10

Exporter 59 10 10 79

Hungary T Importer 10 81 135 36 71 333

Exporter 46 22 91 29 53 68 309

Italy T Importer 427 927 1390 1144 1293 1040 6221

Exporter 644 1592 1245 1203 1597 1276 7557

Latvia T Importer

Exporter 60 60

Lithuania T Importer 16 30 70 116

Exporter 10 32 30 70 142

Netherlands Q Importer

Exporter 81 81

T Importer 540 572 1304 1181 800 1279 5676

Exporter 621 587 954 1209 959 1257 5587

Poland T Importer 21 97 154 55 64 391

Exporter 40 26 85 81 55 52 339

Portugal T Importer 70 70

Exporter 12 19 5 5 92 97 230

Romania T Importer 9 9

Exporter 5 10 9 24

Slovakia T Importer 30 30 Exporter 10 40 30 80

Spain T Importer 13 215 215 261 241 250 1195

Exporter 21 269 155 253 254 279 1231

Importer Purpose Reported by 2002 2003 2004 2005 2006 2007 Total

Sweden T Importer 25 50 70 145

Exporter 30 80 65 175

United Kingdom T Importer 710 1043 1537 1633 1663 2151 8737

Exporter 1172 1749 1911 1911 1905 2199 10847

Importer 2721 5192 7232 7018 6485 8780 37428 Totals Exporter 3584 7361 7159 7035 7284 9135 41558

Table 2. Indirect exports of Euphyllia ancora originating in Indonesia to EU 27, 2002-2007. All trade was in live wild specimens for commercial purposes.

Exporter Importer Reported by 2005 2006 2007 Total

Malaysia Germany Importer

Exporter 130 130

Luxembourg Importer

Exporter 4 4

United Kingdom Importer

Exporter 127 123 250

Singapore Belgium Importer 4 4

Exporter 4 4

Switzerland Germany Importer

Exporter 10 10

United States Austria Importer 55 55

Exporter

Importer 55 4 59 Totals Exporter 137 261 398

Table 3. Direct exports of Euphyllia ancora from Indonesia to countries other than EU-27, 2002-2007. All trade was in live wild specimens for commercial purposes. Importer Reported by 2002 2003 2004 2005 2006 2007 Total

Brazil Importer 54 54

Exporter 120 10 59 17 97 303

Canada Importer 343 405 572 488 1808

Exporter 976 835 663 893 1043 1274 5684

China Importer 5 5

Exporter 44 15 100 60 19 5 243

Croatia Importer

Exporter 30 30

Hong Kong Importer 540 539 700 523 418 422 3142

Exporter 272 768 561 266 477 465 2809

Israel Importer

Exporter 50 10 70 1 15 146

Japan Importer

Importer Reported by 2002 2003 2004 2005 2006 2007 Total

Exporter 923 514 1092 775 616 636 4556

Jordan Importer

Exporter 15 15

Kuwait Importer

Exporter 86 15 10 45 156

Lebanon Importer

Exporter 16 10 26

Macao Importer 22 22

Exporter 15 15

Malaysia Importer

Exporter 200 363 409 173 1145

Mexico Importer 10 10 20

Exporter 20 20

New Zealand Importer

Exporter 17 23 20 5 50 20 135

Norway Importer 6 15 16 37

Exporter 20 45 18 23 44 150

Peru Importer

Exporter 6 13 19

Republic of Korea Importer 171 16 58 5 88 338

Exporter 210 120 101 22 109 116 678

Russian Federation Importer

Exporter 70 38 55 66 1 230

South Africa Importer 15 73 125 213

Exporter 62 5 25 60 146 84 382

Switzerland Importer 50 74 40 164

Exporter 40 40 78 61 92 56 367

Taiwan, Prov. of China Importer

Exporter 106 20 20 77 12 247 482

Tanzania, United Rep. of Importer

Exporter 30 30

Turkey Importer 40 40

Exporter 49 40 89

Ukraine Importer

Exporter 10 10 20

United Arab Emirates Importer 4 4

Exporter 14 15 29

United States Importer 9665 12741 16314 21283 16180 16539 92722

Exporter 18002 17583 13428 15454 16173 14932 95572

Importer Reported by 2002 2003 2004 2005 2006 2007 Total

Venezuela Importer

Exporter 8 8

Importer 10719 13296 17552 22468 17223 17311 98569 Totals Exporter 20978 19978 16471 18179 19427 18306 113339

Table 4. CITES Export quotas for Euphyllia ancora from Indonesia and associated global exports, reported by importer and exporter. All quotas refer to live wild specimens. 2000 2001 2002 2003 2004 2005 2006 2007 2008 2009

Quota 36000 40000 25000 27550 27550 27550 27550 27550 28800 32000

Reported by importer 3316 8940 13440 18488 24784 29486 23708 26091

Reported by exporter 35883 38248 24562 27339 23630 25103 26711 27441

CONSERVATION STATUS in range states The range of Euphyllia ancora comprises the central and eastern Indian Ocean from the Maldives to Myanmar, eastern Australia, the South China Sea, the waters around Indonesia and the western Pacific from Japan to the Great Barrier Reef (Veron, 2000). Its distribution is widespread but patchy (Turak et al. , 2008). The species occurs in shallow environments exposed to moderate wave action, with abundance described as “ seldom common, but may be a dominant species on protected horizontal substrates and on rocky outcrops in high latitude locations ” (Veron, 2000). Turak et al . (2008) described E. ancora as a common species, even forming carpets in some areas of occurrence. There is no species specific population information available for E. ancora (Turak et al., 2008). However, declines are inferred based upon the known reduction of habitat quality resulting from estimates of destroyed coral reef and coral reef at a critical stage of degradation within the species range (Turak et al. , 2008). Coral decline is a general global phenomenon, and Wilkinson (2004) estimated that 24% of coral reef globally is under imminent risk of collapse through human pressures. The rate of coral decline and reef habitat quality in the Indo-Pacific has been significant (Bruno & Selig, 2007). Corals of the genus Euphyllia are frequently colourful and large polyped, making them attractive in the live aquarium trade (Green & Shirley, 1999). E. ancora is heavily harvested for trade purposes (Turak et al. 2008). Other non-extractive threats to the species include both climate change leading to increased sea temperatures and coral bleaching (stress-induced expulsion of symbiotic algae) and coral disease for which E. ancora is particularly susceptible (Wilkinson, 2004 cited in Turak et al . 2008). However, Rachello-Doman & Cleary (2007) classify Euphyllia spp. in a group of massive, submassive and massive- platy corals which are “stress tolerators”, which are able to occur in areas of high sedimentation or eutrophication. Additional localised events that can threaten coral reefs communities include pollution, invasive species and human development activities; however the severity of these combined threats to the global population of E. ancora is unknown (Turak et al., 2008). Green and Shirley (1999) observed that Euphyllia spp. are the fastest growing of the main Scleractinian coral species in international trade, with minimum area growth rates of 96.5cm 2 per year. However, despite comparatively fast growth rates, the susceptibility of E. ancora to known threats increases the likelihood of the species being lost within a generation from reefs at a critical stage and accordingly, a population reduction of 40% over three generation lengths is inferred by the IUCN, meeting the threshold for the Vulnerable category (Turak et al. , 2008). The species could be confused with E. divisa and E. paraancora (Veron, 2000). Indonesia: Euphyllia ancora is found in locations scattered across the whole of Indonesia including Sumatra, Java, Kalimantan, Sulawesi, the Moluccas and West Papua in waters that are relatively calm (Suharsono, 2008). In a survey of 33 sites in three Indonesian regions of Ambon (Moluccas), South Sulawesi and the Java Sea, Euphyllia ancora was found to occur in two sites in Ambon, at the reef wall at

Tanjung Setan at a depth of 10 meters on the edge of the deep water Saram Strait, and at the Wayame fringing protected reef at depths of 3m and 10m (Edinger et al ., 2000). In a rapid ecological assessment of the Raja Ampat Islands in the province of Papua, East Indonesia, which cover an area of four million hectares, E. ancora was found to occur at 17 of 51 dive survey sites off islands including Salawati, Bantanta, Misool, Kofiau, Weigeo and Uranie (Turak & Souhoka, 2003). The dominant species in each of several community types (protected communities in bays, single depth communities and communities around bays with strong headlands) were determined by relative abundance or number of individuals at each site classified categorically; E. ancora was not reported as a dominant species in any of the community types within the Raja Ampat archipelago (Turak & Souhoka, 2003). Overall coral reef communities in the Raja Ampat area were considered to be in very good health during the 2002 surveys and six established protected areas were noted as established within the archipelago which may include E. ancora ; however enforcement of the site designation within Raja Ampat was noted at that time as inefficient (Turak & Souhoka, 2003). In a similar assessment of 45 sites in 2001, E. ancora was found to occur in the Raja Ampat islands (Veron, 2002), with the species confirmed at ten sites (Fenner, 2002a). During rapid ecological assessments, Euphyllia ancora was not found in shallow or deep reef surveys of the Banda islands in the Maluku region of Indonesia, which mostly comprised narrow fringing reefs without any intertidal reef flat (Turuk & Wakeford, 2002). In a similar rapid assessment study of the Togean and Benggai islands of Sulawesi, Fenner (2002b) confirmed the occurrence of E. ancora in six of 47 sites sampled. Two sites were fringing reefs on the periphery of islands, two were on offshore reefs and two were atoll reefs, which typically include a shallow reef crest (Fenner, 2002b). In the National Marine Park of Bunaken in North Sulawesi, a dense population of E. ancora was found to completely cover a sloped area to a depth of 40 meters (Tazioloi et al ., 2007). E. ancora was recorded in a survey of 27 coral reef sites surveyed in the Wakatobi National Marine Park situated between the Banda and Flores seas in southwest Sulawesi, Indonesia which covers 1.39 million ha during a rapid ecological assessment (Turak, 2003). The species was found in eight sites, including Pasar Wajo (Buton), Karang Kapota Inner Lagoon, Kambode SW (Kapota Island), SE Wangi Atoll (N tip), Koromaha East Lagoon Bommie , Ndaa Enclosed Lagoon/Reef flat, Karang Kaledupa SE Lagoon, and Tanjung Kondowa (Pasar Wajo, Buton). The same study found that E. ancora was not a dominant species in any of five community types, which were determined by depth (either shallow or deep water), varying coral species richness and reef exposure. Coral damage was seen at most sites but at relatively low levels, however the Wakatobi area is relatively protected from coral bleaching by upwellings of cool waters from the south (Turak, 2003). Coral disease prevalence in Wakatobi Marine Park was recorded to be low (Haapkyla et al ., 2007). UNESCO surveyed coral assemblages in 28 patch reefs associated with islands throughout the Palau Seribu (Thousand Island) reef complex and National Park (which includes Jakarta Bay) in north-west Java in 1985, and data were analysed by Cleary et al . (2006). In a study which aimed to compare species diversity across a disturbance gradient, Cleary et al ., (2006) found the genus Euphyllia to be a significant indicator genus (or the degree to which a genus is unique to a particular habitat) for the zone outside of the major influence of Jakarta Bay with some localised fishing disturbance and pollution in the dry season, although no individual species of Euphyllia were specifically identified as occurring within the national park. Similar to the situation for the global population, there are no estimates available for the size of the Indonesian population of E. ancora . Indonesia is at the centre of a global coral diversity hotspot within South East Asia. Anthropogenic stress combined with global change threats places coral reefs in the Indo-Pacific region at high risk of collapse (Turak et al., 2008). Whilst the status of coral reefs in general in South East Asia continues to show an overall decline in reef condition, it is notable that Indonesia showed some slight improvements in reef condition 1999-2004 (Wilkinson, 2004). Dirhamsyah (2006) suggested that the legal framework of sixteen laws on coastal and coral reef resources management in Indonesia is too complex and inappropriate, which in general has led to poor implementation and degradation of coral resources.

REFERENCES: Bruno, J.F. & Selig, E.R. 2007. Regional decline of coral cover in the Indo-Pacific: timing, extent and subregional comparisons. PLoS ONE : 8, 7-11. Cleary, D.F.R., Suharsono, & Hoeksema, B.W. 2006. Coral diversity across a disturbance gradient in the Pulau Seribu reef complex off Jakarta, Indonesia. Biodiversity and Conservation 15: 3653–3674. Dirhamsyah, D. 2006. Indonesian legislative framework for coastal resources management: A critical review and recommendation. Ocean & Coastal Management 49; 68-92. Edinger, E.N., Kolasa, J. & Risk, M.J. 2000. Biogeographical variation in coral species diversity on coral reefs in three regions of Indonesia. Diversity and Distributions 6: 133-127. Fenner, D. 2002a. Reef corals of the Raja Amput Islands, Papua Province, Indonesia – Comparison of Survey Sites. In: A Marine Rapid Assessment of the Raja Amput Islands, Papau Province, Indonesia . Eds. McKenna, S.A. Allen, G.R. & Suryadi, S. RAP Bulletin of Biological Assessment 22: 191. Fenner, D. 2002b. Reef corals of the Togean and Banggai Islands,Sulawesi, Indonesia. In: A Marine Rapid Assessment of the Togean and Banggai Islands, Sulawesi, Indonesia . Eds. Allen, G.R. & McKenna, S.A. Conservation International. Green, E., & Shirley, F. 1999. The Global Trade in Corals. World Conservation Monitoring Centre. World Conservation Press. Haapkyla, J., Seymour, A.S., Trebilco, J. & Smith, D. 2007. Coral disease prevalence and coral health in the Wakatobi Marine Park, south-east Sulawesi, Indonesia. Journal of the Marine Biological Association of the United Kingdom 87: 403-414. Rachello-Domen, P.G. & Cleary, D.F.R. 2007. Relating coral species traits to environmental conditions in the Jakarta Bay/Pulau Seribu reef system, Indonesia. Estuarine, Coastal and Shelf Science 73: 816- 826 Suharsono. 2008. Jenis-jenis karang de Indonesia. Indonesian Institute of Sciences. Jakarta. Tazioli, S., Bo, M., Boyer, M., Rotinsulu, H. & Bavestrello, G. 2007. Ecological Observations of Some Common Antipatharian Corals in the Marine Park of Bunaken (North Sulawesi, Indonesia). Zoological Studies 46(2): 227-241 Turak, E. 2003. Coral diversity and distribution. In: Rapid Ecological Assessment Wakatobi National Park . Eds. Pet-Soede, L. & Erdmann, M. Marine Program, WWF Indonesia. Turak, E., Sheppard, C., & Wood, E. 2008. IUCN Red List of Threatened Species. Accessed 11 May 2009. Turak, E. & Souhoka, J. 2003. Coral Diversity and the Status of Coral Reefs in the Raja Ampat Islands. In: Report on a rapid ecological assessment of the Raja Ampat Islands, Papua, Eastern Indonesia held October 30 – November 22, 2002. The Nature Conservancy. Turak, E. & Wakeford. M. 2002. Banda Islands Rapid Ecological Assessment, May 2002: Assessment of Coral Biodiversity and Coral Reef Health. Australian Institute of Marine Science. Veron, J. E. N. 2000. Corals of the world. 3 vols. Australian Institute of Marine Science and CRR Qld Pty Ltd. Veron, J.E.N 2002. Reef corals of the Raja Amput Islands, Papua Province, Indonesia – Overview of Scleractinia. In: A Marine Rapid Assessment of the Raja Amput Islands, Papau Province, Indonesia . Eds. McKenna, S.A. Allen, G.R. & Suryadi, S. Conservation International. Wilkinson, C. 2004. Status of Coral Reefs of the World. Australian Institute of Marine Science.

REVIEW OF SPECIES SELECTED ON THE BASIS OF A NEW OR INCREASED EXPORT QUOTA IN 2009

ANTHOZOA OCULINIDAE

SPECIES: Galaxea astreata

SYNONYMS: Anthophyllum clavus, Caryophyllia astreata, Galaxea clavus, Galaxea lamarcki, Galaxea laticostata, Galaxea negrensis, Galaxea susanae

COMMON NAMES:

RANGE STATES: American Samoa, Australia, Bangladesh, British Indian Ocean Territory, China, Djibouti, Egypt, Fiji, Guam, Hong Kong (?), India, Indonesia, Japan, Kenya, Madagascar, Malaysia, Maldives, Mauritius, Mozambique, Myanmar, New Caledonia, Oman, Palau, Papua New Guinea, Philippines, Saudi Arabia, Seychelles, Singapore, Solomon Islands, Sri Lanka, Taiwan, Province of China, Thailand, Tonga, United Republic of Tanzania, Vanuatu, Viet Nam,

RANGE STATE UNDER REVIEW: Indonesia

IUCN RED LIST: Vulnerable

PREVIOUS EC OPINIONS: No previous opinions formed

TRADE PATTERNS: Galaxea astreata from Indonesia was selected for review on the basis of an increased export quota for 2009 combined with its globally Vulnerable status. An export quota of 4,650 live specimens had remained the same from 2003 to 2007 but increased to 5,040 in 2008 and further increased to 5,432 in 2009. In addition, quotas for products derived from mariculture were set for 2004 and 2007. None of the quotas appear to have been exceeded (Tables 8 & 9). The major importing countries in the EU were France, Germany, Italy, Netherlands, Spain and United Kingdom and most trade was directly from Indonesia. Outside of the EU, the main importer by far is the United States with lesser quantities exported to Canada, Hong Kong and Japan. Indonesia has not submitted export quotas for maricultured corals to the CITES Secretariat for 2009. Table 5. Direct exports of Galaxea astreata from Indonesia to EU 27, 2002-2007. All trade was in live specimens for commercial purposes and units were blank. Importer Source Reported by 2002 2003 2004 2005 2006 2007 Total

Austria W Importer 19 26 4 22 71

Importer Source Reported by 2002 2003 2004 2005 2006 2007 Total

Exporter 50 30 4 15 32 131

Belgium W Importer 8 8

Exporter 10 10

Cyprus W Importer

Exporter 8 8

Czech Republic F Importer

Exporter 20 10 30

W Importer 15 12 5 14 46

Exporter 42 5 5 4 56

Denmark F Importer

Exporter 120 120

W Importer 8 12 15 10 45

Exporter 68 16 10 5 10 109

Finland W Importer 3 5 5 5 18

Exporter 3 5 10 18

France F Importer

Exporter 25 20 45

W Importer 245 137 89 235 226 229 1161

Exporter 287 220 202 267 235 142 1353

Germany F Importer

Exporter 60 275 335

W Importer 474 273 368 407 516 548 2586

Exporter 480 364 427 404 526 622 2823

Greece F Importer

Exporter 146 146

W Importer 10 10

Exporter 10 10 10 18 48

Hungary W Importer 16 24 10 50

Exporter 5 37 20 14 5 81

Italy F Importer

Exporter 68 68

W Importer 194 100 145 47 181 115 782

Exporter 225 161 163 112 228 224 1113

Lithuania W Importer 2 7 9

Exporter 7 7

Netherlands F Importer

Exporter 55 55

W Importer 44 54 35 81 107 272 593

Exporter 69 64 47 140 139 158 617

Poland F Importer

Exporter 30 10 40

Importer Source Reported by 2002 2003 2004 2005 2006 2007 Total

W Importer 15 10 50 34 25 134

Exporter 30 11 70 12 13 15 151

Portugal W Importer 5 4 9

Exporter 10 1 15 5 11 42

Romania W Importer 5 5

Exporter 5 5

Slovakia W Importer 5 5

Exporter 5 5 10

Spain F Importer

Exporter 18 18

W Importer 34 71 19 45 22 74 265

Exporter 55 95 12 48 47 87 344

Sweden F Importer

Exporter 5 5

W Importer 12 18 15 23 58 126

Exporter 42 66 49 27 70 254

United Kingdom F Importer

Exporter 30 105 135

W Importer 35 137 166 388 123 254 1103

Exporter 68 282 122 456 135 211 1274

Importer 1078 853 928 1256 1278 1633 7026 Totals Exporter 1371 1365 1156 1556 1559 2444 9451

Table 6. Indirect exports of Galaxea astreata originating in Indonesia to EU 27, 2002-2007. All trade was in live wild specimens for commercial purposes and units were blank.

Exporter Importer Reported by 2002 2003 2004 2005 2006 2007 Total

Fiji France Importer 40 40

Exporter

Germany Importer 2 2

Exporter

United Kingdom Importer 1 10 11

Exporter 6 6

Malaysia Denmark Importer 8 8

Exporter

Germany Importer

Exporter 11 11

Italy Importer

Exporter 3 3

United Kingdom Importer

Exporter 114 283 397

Totals Importer 40 1 12 8 61

Exporter Importer Reported by 2002 2003 2004 2005 2006 2007 Total

Exporter 6 117 294 417

Table 7. Direct exports of Galaxea astreata from Indonesia to countries other than EU-27, 2002-2007. All trade was in live specimens for commercial purposes and units were blank.

Importer Source Reported by 2002 2003 2004 2005 2006 2007 Total

Brazil W Importer

Exporter 6 54 6 3 69

Canada F Importer

Exporter 40 360 400

W Importer 32 81 94 65 272

Exporter 162 167 181 169 128 154 961

China F Importer

Exporter 60 60

W Importer

Exporter 40 25 14 10 89

Hong Kong F Importer

Exporter 5 5

W Importer 5 82 19 106

Exporter 23 83 11 41 158

Israel F Importer

Exporter 74 74

W Importer

Exporter 20 4 24

Japan F Importer

Exporter 15 40 568 623

W Importer

Exporter 383 182 256 245 324 330 1720

Kuwait W Importer

Exporter 17 91 66 174

Malaysia W Importer

Exporter 82 31 67 86 56 322

New Zealand W Importer

Exporter 8 4 7 13 20 52

Norway W Importer 10 10

Exporter 8 24 32

Republic of Korea W Importer 26 20 195 35 21 94 391

Exporter 46 108 85 57 68 54 418

Russian Federation W Importer

Exporter 83 26 15 43 56 223

Singapore F Importer

Exporter 217 217

Importer Source Reported by 2002 2003 2004 2005 2006 2007 Total

W Importer 105 105

Exporter 2 2

South Africa W Importer 85 29 24 138

Exporter 18 28 69 16 46 48 225

Switzerland F Importer

Exporter 130 130

W Importer 63 20 14 97

Exporter 20 48 25 31 44 30 198

Taiwan, Prov. of China W Importer

Exporter 178 40 49 46 101 75 489

Ukraine F Importer

Exporter 19 19

W Importer 4 4

Exporter 4 2 6

United States F Importer

Exporter 18 1295 1313

W Importer 1386 1313 1934 1764 1602 1932 9931

Exporter 3084 2257 2226 2165 2143 2012 13887

Venezuela W Importer

Exporter 1 1

Importer 1449 1333 2440 1917 1731 2184 11054 Totals Exporter 3988 3165 2996 2841 3193 5708 21891

Table 8. CITES Export quotas for Galaxea astreata from Indonesia and associated global exports, reported by importer and exporter. All quotas refer to live wild specimens.

1999 2000 2001 2002 2003 2004 2005 2006 2007 2008 2009

Quota 6300 5400 6000 5500 46 50 4650 4650 4650 4650 5040 5432

Reported by importer 571 1382 2237 2527 2186 3368 3173 3009 3817

Reported by exporter 5660 5086 5688 5359 4530 4137 4397 4489 4592

Table 9. CITES Export quotas for Galaxea astreata from Indonesia and associated global exports, reported by importer and exporter. All quotas refer to specimens from mariculture.

2004 2005 2006 2007

Quota 200 - - 3973

Reported by importer 0 0 0 0

Reported by exporter 15 0 263 3560

CONSERVATION STATUS in range states Galaxea astreata has a widespread distribution from the East African coast including Madagascar to the Red Sea and Gulf of Aden, the East and West Indian Ocean including Sri Lanka and the Maldives, Japan and the South China Sea, the waters around Indonesia and the western and eastern coasts of Australia, to the Pacific Islands (Veron, 2000). The species occurs in reef environments protected from strong wave action, and is described as common throughout its range (Veron, 2000; Hoeksema et al ., 2008). No species specific population information was identified for G. astreata. However, global declines were inferred based upon the known reduction of habitat quality resulting from estimates of destroyed coral reef within the species range, and a population reduction of 35% over three generation lengths is estimated by the IUCN, meeting the threshold for the Vulnerable category (Hoeksema et al ., 2008). The species is targeted by collectors for the aquarium trade and other non-extractive threats to all coral species include climate change leading to increased sea temperatures and coral bleaching (stress- induced expulsion of symbiotic algae) and coral disease (Hoeksema et al ., 2008). Additional localised events that can threaten coral reef communities include pollution, invasive species and human development activities; however the severity of these combined threats to the global population of G. astreata is unknown (Hoeksema et al ., 2008). Coral decline is a general global phenomenon, and Wilkinson (2004) estimated that 24% of coral reef globally is under imminent risk of collapse through human pressures. The rate of coral decline and reef habitat quality in the Indo-Pacific has been significant (Bruno & Selig, 2007). The species is, however, more resilient to reef threats than other coral species (Wilkinson, 2004 cited in Hoeksema et al ., 2008). In Australia’s Great Barrier Reef, Galaxea spp. were relatively unaffected by bleaching compared with other taxa following a large-scale bleaching event in 1998 (Marshall & Baird, 2000). Rachello-Doman & Cleary (2007) classified Galaxea spp. in a group of massive, submassive and massive-platy corals which are “stress tolerators”, which are able to occur in areas of high sedimentation or eutrophication. Indonesia: Galaxea astreata is found in locations scattered across the whole of Indonesia from north- west Sumatra, Java and the Moluccas, Sulawesi, the Banda Islands and West Papua (Suharsono, 2008). In a survey of 33 sites in three Indonesian regions of Ambon (Moluccas), South Sulewesi and the Java Sea, Galaxea astreata was found to occur at three sites in Ambon, at the reef wall at Tanjung Setan at a depth of 3 meters on the edge of the deep water Saram Strait, at the Wayame fringing protected reef and at the Wailiha fringing and exposed reef, both at depths of 3m, and of the Southern coast of Sulawesi, at the Kapoposan wall reef at a depth of 10m (Edinger et al ., 2000). In a rapid ecological assessment of the Raja Ampat Islands in the province of Papua, East Indonesia, which cover an area of four million hectares, G. astreata was found to have a large geographic spread across the Raja Ampat archipelago, occurring at 36 of 51 dive survey sites (Turak & Souhoka, 2003). The species was found at survey sites at each of the islands of Salawati, Bantanta, Misool, Kofiau, Weigeo, Wayag, Quoy, Uranie, and Weigao and generally in more than one location off these islands (Turak & Souhoka, 2003). G. astreata was not reported as a dominant species (determined by relative abundance or number of individuals) in any of the community types sampled (protected communities in bays, single depth communities and communities around bays with strong headlands) within the Raja Ampat archipelago (Turak & Souhoka, 2003). Overall coral reef communities in the Raja Ampat area were considered to be in very good health during the 2002 surveys and six established protected areas were noted as established within the archipelago which may include G. astreata ; however enforcement of the site designation within Raja Ampat was noted at that time as inefficient (Turak & Souhoka, 2003). In a similar assessment of the Raja Ampat islands in 2001, G. astreata was found to be widespread in occurrence (Veron, 2002), with the species confirmed at 21 of 45 sites (Fenner, 2002a). During rapid ecological assessments in the Banda islands in the Maluku region of Indonesia in 2002, G. astreata was found to occur in five of 18 survey sites of shallow and deep reefs which mostly comprised narrow fringing reefs without any intertidal reef flat (Turuk & Wakeford, 2002). It was recorded to occur near the islands of Palau Api, Gunung Api and at two sites near Bandar Besar (Atap Tingii and Selamo village), but it was not found to be one of the most abundant corals at any of the sampled sites, irrespective of coral community type (Turuk & Wakeford, 2002).

In a similar rapid assessment study of the Togean and Benggai islands of Sulawesi, Fenner (2002b) confirmed the occurrence of G. astreata at six sites in each of the Togean and Benggai islands of a total of 47 sites sampled. Four sites were offshore reefs, three were fringing reefs typically on the periphery of islands, three sites were exposed reefs, and one occurrence record was on a barrier reef (Fenner, 2002b). G. ancora was recorded in a survey of 27 coral reef sites surveyed in the Wakatobi National Marine Park situated between the Banda and Flores seas in southwest Sulawesi, Indonesia which covers 1.39 million ha during a rapid ecological assessment in 2003 (Turak, 2003). The species was found in three sites including Karang Kapota Inner Lagoon, Kambode SW (Kapota Island) and North Lintea Selatan (facing Strait). The same study found that G. ancora was not a dominant species in any of five community types, which were determined by shallow or deep water depths, varying coral species richness and reef exposure. Coral damage was seen at most sites but at relatively low levels, however the Wakatobi area is relatively protected from coral bleaching by upwellings of cool waters from the south (Turak, 2003). Coral disease prevalence in Wakatobi Marine Park is also recorded to be low (Haapkyla et al ., 2007). UNESCO surveyed coral assemblages in 28 patch reefs associated with islands throughout the Palau Seribu (Thousand Island) reef complex and National Park in north-west Java (which includes Jakarta Bay) in 1985, and data were analysed by Cleary et al . (2006) to compare species diversity across a disturbance gradient. G. astreata was confirmed to occur in the Palau Seribu complex; both the genus Galaxea and the species G. astreata were found to be a significant indicator genus (or the degree to which a genus or species is unique to a particular habitat) for the zone outside of the major influence of Jakarta Bay with some localised fishing disturbance and pollution in the dry season (Cleary et al ., 2006). In surveys of the Palau Seribu complex in 1995, Galaxea astreata was most abundant in offshore sites characterised by a large cover of dead corals (Cleary et al ., 2008) which may indicate the species ability to cope with some disturbance. Similar to the situation for the global population, no population estimates were identified for the Indonesian population of G. astreata . Anthropogenic stress combined with global change threats places coral reefs in the Indo-Pacific region at high risk of collapse (Hoeksema et al ., 2008). Whilst the status of coral reefs in general in South East Asia continues to show an overall decline in reef condition, it is notable that Indonesia has shown some slight improvements in reef condition 1999-2004 (Wilkinson, 2004). Dirhamsyah (2006) suggests that the legal framework of sixteen laws on coastal and coral reef resources management in Indonesia is too complex and inappropriate, which in general has led to poor implementation and degradation of coral resources.

Haapkyla, J., Seymour, A.S., Trebilco, J. & Smith, D. 2007. Coral disease prevalence and coral health in the Wakatobi Marine Park, south-east Sulawesi, Indonesia. Journal of the Marine Biological Association of the United Kingdom 87: 403-414. Hoeksema, B., Rogers, A. & Quibilan, M. 2008. IUCN Red List of Threatened Species. Accessed 11 May 2009. Green, E., & Shirley, F. 1999. The Global Trade in Corals. World Conservation Monitoring Centre. World Conservation Press. Marshall, P.A. & Baird, A.H. 2000. Bleaching of corals on the Great Barrier Reef: differential susceptibilities among taxa. Coral Reefs 19: 155-163. Rachello-Domen, P.G. & Cleary, D.F.R. 2007. Relating coral species traits to environmental conditions in the Jakarta Bay/Pulau Seribu reef system, Indonesia. Estuarine, Coastal and Shelf Science 73: 816- 826. Suharsono. 2008. Jenis-jenis karang de Indonesia. Indonesian Institute of Sciences. Jakarta. Tazioli, S., Bo, M., Boyer, M., Rotinsulu, H. & Bavestrello, G. 2007. Ecological Observations of Some Common Antipatharian Corals in the Marine Park of Bunaken (North Sulawesi, Indonesia). Zoological Studies 46(2): 227-241 Turak, E. 2003. Coral diversity and distribution. In: Rapid Ecological Assessment Wakatobi National Park . Eds. Pet-Soede, L.& Erdmann, M. Marine Program, WWF Indonesia. Turak, E. & Souhoka, J. 2003. Coral Diversity and the Status of Coral Reefs in the Raja Ampat Islands. In: Report on a rapid ecological assessment of the Raja Ampat Islands, Papua, Eastern Indonesia held October 30 – November 22, 2002. The Nature Conservancy. Turak, E. & Wakeford. M. 2002. Banda Islands Rapid Ecological Assessment, May 2002: Assessment of Coral Biodiversity and Coral Reef Health. Australian Institute of Marine Science. Veron, J. E. N. 2000. Corals of the world. 3 vols. Australian Institute of Marine Science and CRR Qld Pty Ltd. Veron, J. E. N. 2002. Reef corals of the Raja Amput Islands, Papua Province, Indonesia – Overview of Scleractinia. In: A Marine Rapid Assessment of the Raja Amput Islands, Papau Province, Indonesia. Eds. McKenna, S.A. Allen, G.R. & Suryadi, S. Conservation International. Wilkinson, C. 2004. Status of coral reefs of the world. Australian Institute of Marine Science.

REVIEW OF SPECIES SELECTED ON THE BASIS OF A NEW OR INCREASED EXPORT QUOTA IN 2009

ANTHOZOA HELIOPORIDAE

SPECIES: Heliopora coerulea

SYNONYMS: Heliopora compressa, Madrepora coerulea

COMMON NAMES: Blue Coral (English)

RANGE STATES: American Samoa, Australia, British Indian Ocean Territory, Cocos (Keeling) Islands, Fiji, Guam, India, Indonesia, Japan, Kiribati, Malaysia, Maldives, Marshall Islands, Mauritius, Micronesia (Federated States of), Nauru, New Caledonia, Northern Mariana Islands, Palau, Papua New Guinea, Philippines, Seychelles, Singapore, Solomon Islands, Taiwan, Province of China, Tuvalu, Vanuatu, Viet Nam,

RANGE STATE UNDER REVIEW: Indonesia

IUCN RED LIST: Vulnerable

PREVIOUS EC OPINIONS: A positive opinion for all countries was formed on 22/07/1997. A positive opinion for Viet Nam was formed on 09/03/2006. A 4.6(b) import suspension is in place for wild specimens from the Solomon Islands (formed 03/09/2008) following a negative opinion formed on 12/06/2006.

TRADE PATTERNS: Heliopora coerulea from Indonesia was selected for review on the basis of an increased export quota for 2009 combined with its globally Vulnerable status. The quota for live specimens was 950 in 2003, but decreased to 400 in 2004. No export quota was set for 2005 and 2006 but a quota of 950 was established for 2007. In 2008, this was increased to 2250 and further increased to 2425 in 2009. The quota for 2004 was apparently exceeded according to both importer and exporter data (Table 12). The major importing countries in the EU were France, Germany and United Kingdom and there was no indirect trade. Outside of the EU, the main importer is the United States with lesser quantities going to Japan and the Republic of Korea. Indonesia has not submitted export quotas for maricultured corals to the CITES Secretariat for 2009.

Table 10. Direct exports of Heliopora coerulea from Indonesia to EU 27, 2002-2007. All trade was in live specimens for commercial purposes and units were blank. Importer Source Reported by 2002 2003 2004 2005 2006 2007 Total

Austria W Importer 19 5 21 2 13 60

Exporter 56 25 1 2 13 97

Czech Republic W Importer 3 2 1 6

Exporter 3 7 10

Denmark F Importer

Exporter 25 40 65

W Importer 2 10 29 40 81

Exporter 2 10 4 16

Finland W Importer 3 5 8

Exporter 8 8

France F Importer

Exporter 10 95 30 135

W Importer 326 42 33 77 66 86 630

Exporter 157 74 49 51 23 33 387

Germany F Importer

Exporter 120 195 30 345

W Importer 249 106 187 62 229 146 979

Exporter 339 70 122 108 230 126 995

Greece F Importer

Exporter 30 55 85

W Importer 30 30

Exporter 5 5

Hungary W Importer 3 3

Exporter 5 5

Italy W Importer 8 13 15 36

Exporter 5 8 13 25 51

Latvia W Importer

Exporter 2 2

Lithuania W Importer 1 1

Exporter 1 1

Netherlands F Importer

Exporter 30 90 120

W Importer 30 30

Exporter 13 13

Poland W Importer 40 5 41 3 89

Exporter 40 14 37 91

Portugal W Importer 1 1

Exporter 2 2

Importer Source Reported by 2002 2003 2004 2005 2006 2007 Total

Spain W Importer 13 1 14

Exporter 9 11 4 2 4 30

Sweden W Importer 39 1 10 4 54

Exporter 40 5 11 7 63

United Kingdom F Importer

Exporter 40 65 105

W Importer 16 66 44 80 28 77 311

Exporter 40 86 51 82 10 77 346

F Importer

Totals Exporter 200 500 155 855

W Importer 689 246 376 237 402 383 2333

Exporter 689 287 291 276 280 299 2122

There were no indirect exports of Heliopora coerulea originating in Indonesia to EU 27, 2002-2007. Table 11. Direct exports of Heliopora coerulea from Indonesia to countries other than EU-27, 2002-2007. All trade was in live specimens for commercial purposes and units were blank. Importer Source Reported by 2002 2003 2004 2005 2006 2007 Total

Brazil W Importer

Exporter 6 37 10 2 8 63

Brunei Dar. F Importer

Exporter 5 5

Canada F Importer

Exporter 10 20 70 100

W Importer 14 18 8 40

Exporter 10 35 11 17 23 96

China W Importer

Exporter 20 20

Hong Kong F Importer

Exporter 20 45 30 95

W Importer 10 20 15 45

Exporter 46 5 10 61

Israel W Importer

Exporter 12 1 14 27

Japan F Importer

Exporter 10 440 450

W Importer

Exporter 149 122 145 227 160 221 1024

Kuwait F Importer

Exporter 35 35

W Importer

Exporter 1 6 9 12 28

Importer Source Reported by 2002 2003 2004 2005 2006 2007 Total

Macao W Importer 6 6

Exporter 6 6

Malaysia F Importer

Exporter 20 20

W Importer

Exporter 2 23 15 25 20 43 128

Mexico W Importer 8 8

Exporter 17 17

New Zealand W Importer

Exporter 5 9 14

Norway W Importer

Exporter 5 5

Republic of Korea W Importer 10 68 22 14 45 159

Exporter 10 59 43 17 59 27 215

Russian Federation W Importer

Exporter 5 14 11 21 29 26 106

Singapore W Importer

Exporter 9 9

South Africa W Importer 20 10 30

Exporter 90 28 10 25 14 6 173

Switzerland F Importer

Exporter 49 20 25 94

W Importer 26 17 5 9 73 130

Exporter 45 22 1 33 3 12 116

Taiwan, Prov. of China F Importer

Exporter 150 15 165

W Importer

Exporter 40 51 82 75 85 32 365

Thailand W Importer

Exporter 2 4 6

Ukraine F Importer

Exporter 10 10

W Importer 19 19

Exporter

United States F Importer

Exporter 135 491 340 966

W Importer 34 40 168 68 384 135 829

Exporter 290 271 186 194 253 232 1426

Importer Source Reported by 2002 2003 2004 2005 2006 2007 Total

F Importer

Totals Exporter 400 1300 1070 25 2795 400 1300

W Importer 777 309 675 373 896 573 3603

Exporter 1428 931 858 917 950 947 6031

Table 12. CITES Export quotas for Heliopora coerulea from Indonesia and associated global exports, reported by importer and exporter. All quotas refer to live wild specimens.

1999 2000 2001 2002 2003 2004 2005 2006 2007 2008 2009

Quota 1350 1350 1500 1500 950 400 - - 950 2250 2500

Reported by importer 65 145 353 777 309 675 373 896 573

Reported by exporter 1147 1142 1412 1428 931 858 917 950 947

The quota for 2004 was exceeded according to both importer and exporter data. CONSERVATION STATUS in range states Heliopora coerulea has a widespread distribution from the East African coast including Madagascar to the Red Sea and Gulf of Aden, the East and West Indian Ocean including Sri Lanka and the Maldives, Japan and the South China Sea, the waters around Indonesia and the western and eastern coasts of Australia, to the Pacific Islands (Veron, 2000). It commonly occurs on intertidal reef flats and can form large colonies (Veron, 2000). H. coerulea normally grows on ridges near to deep ravines exposed at low tides, and is sometimes a dominant species (Suharsono, 2008). However, it has also been described as uncommon in most of its range (Zann & Bolton, 1985) and locally rare (Obura et al ., 2008). In studies in the Pacific, H. coerulea was found to be most abundant in sites in the equatorial Central Pacific zone (Zann & Bolton, 1985). H. coerulea is restricted to extremely shallow depths (generally less than 2m), thus is susceptible to coral bleaching (stress-induced expulsion of symbiotic algae), harvesting and other localised events (Obura et al ., 2008). Coral decline is a general global phenomenon, and Wilkinson (2004) estimated that 24% of coral reef globally is under imminent risk of collapse through human pressures. The rate of coral decline and reef habitat quality in the Indo-Pacific has been significant (Bruno & Selig, 2007). There is no species specific population information available for H. coerulea. However, declines are inferred based upon the known reduction of habitat quality resulting from estimates of destroyed coral reef and coral reef at a critical stage of degradation within the species range, and a population reduction of 37% over three generation lengths is estimated by the IUCN, meeting the threshold for the Vulnerable category (Obura et al ., 2008). The species is targeted by collectors for the live aquarium trade but the preferred market for the species is dead coral for the curio and jewellery trade (Bruckner, 2001). Other non-extractive threats to coral species include climate change leading to increased sea temperatures and coral bleaching and disease (Obura et al ., 2008). Additional localised events that can threaten coral reefs communities include pollution, invasive species and human development activities; however the severity of these combined threats to the global population of H. coerulea is unknown (Obura et al ., 2008). Heliopora spp. are considered to be “ruderals” which are capable of rapid growth but are also relatively fragile (Edinger & Risk, 2000). H. coerulea does not usually survive much more than a year within aquaria (Green & Shirley, 1999). Indonesia: In a rapid ecological assessment of the Raja Ampat Islands of the province of Papua, East Indonesia, which covers an area of four million hectares, H. coerulea was found to occur at

21 of 51 dive survey sites (Turak & Souhoka, 2003). The dominant species in each of several community types (protected communities in bays, single depth communities and communities around bays with strong headlands) were determined by relative abundance or number of individuals at each site classified categorically; H. coerulea was reported as a dominant species within the Raja Ampat archipelago in single depth communities found far in a narrow inlet (Turak & Souhoka, 2003). In dive surveys to assess reef damage following a tsunami of 26 December 2004 which hit the west coast of Sumatra, large stands of healthy H. coerulea were recorded off the north coast of Aceh Province (Sumatra) at 3m water depth in 2005, however, in one site surveyed in the northern islands near Pulau Weh, large colonies of H. coerulea had been overturned and shattered into pieces. It was estimated that recovery of the affected Sumatran reefs would be complete within a decade (Hagen et al ., 2007). During rapid ecological assessments in 2002, H. coerulea was found in surveys of the Banda islands of the Maluku region of Indonesia, which mostly comprise narrow fringing reefs without any intertidal reef flat (Turuk & Wakeford, 2002). H. coerulea was one of the most abundant non-Scleractinian corals to occur in shallow communities less than 10m depth, and was found to be common on the exposed reef flat northeast of Hatta Island (Turuk & Wakeford, 2002). In a rapid assessment study of the Togean and Benggai islands of Sulawesi, Fenner (2002b) confirmed the occurrence of H. coerulea in 18 of 47 sites sampled, as well as the occurrence of Heliopora dendritica at an additional eight sites. However, it is considered by Veron (2000) that Heliopora coerulea is the sole member of the Order Helioporacea, and CITES notification 2003/20 accordingly reflects the genus as mono-specific. A wide range of reef types were represented by the combined Heliopora records, including sheltered fringing reefs typically on the periphery of islands, exposed reefs, offshore reefs which typically arise from deep water, atoll reefs and barrier reefs (Fenner, 2002b). Heliopora coerulea was recorded in 16 sites of 27 coral reef sites surveyed in the Wakatobi National Marine Park situated between the Banda and Flores seas in southwest Sulawesi, Indonesia, which covers 1.39 million ha during a rapid ecological assessment in 2003 (Turak, 2003). It was a dominant species in shallow exposed reefs at depths of 8m or less with medium gradients, and most commonly found around the island of Wangi and the eastern atolls of the park (Turak, 2003). Coral damage was seen at most sites but at relatively low levels, and the Wakatobi area is relatively protected from coral bleaching by upwellings of cool waters from the south (Turak, 2003). Coral disease prevalence in Wakatobi Marine Park was recorded to be low (Haapkyla et al ., 2007). H. coerulea was not recorded in a survey of 33 sites in three Indonesian regions of Ambon (Moluccas), South Sulewesi and the Java Sea (Edinger et al ., 2000). UNESCO surveyed coral assemblages in 28 patch reefs associated with islands throughout the Palau Seribu (Thousand Island) reef complex and National Park (which includes Jakarta Bay) in north-west Java in 1985, and data were analysed by Cleary et al . (2006). The genus Heliopora was not identified as a significant species across sites with varying disturbance levels (Cleary et al ., 2006). Similar to the situation for the global population, no estimates were identified for the size of the Indonesian population of H. coerulea . Indonesia is at the centre of a global coral diversity hotspot in South East Asia. Anthropogenic stress combined with global change threats places coral reefs in the Indo-Pacific region at high risk of collapse (Obura et al ., 2008). Whilst the status of coral reefs in general in South East Asia continues to show an overall decline in reef condition, it is notable that Indonesia has shown some slight improvements in reef condition from 1999-2004 (Wilkinson, 2004). Bruckner (2001) observed that coral specimens taken for the curio trade are often substantially larger in size than those taken for the live ornamental trade, but the trade in curio corals was noted to be suspended at that time in Indonesia. Dirhamsyah (2006) suggests that the legal framework of sixteen laws on coastal and coral reef resources management in Indonesia is too

complex and inappropriate, which in general has led to poor implementation and degradation of coral resources. REFERENCES: Bruno, J. F. & Selig, E. R. 2007. Regional decline of coral cover in the Indo-Pacific: Timing, extent and subregional comparisons. PLoS ONE : 8, 7-11. Cleary, D. F. R., Suharsono, & Hoeksema, B.W. 2006. Coral diversity across a disturbance gradient in the Pulau Seribu reef complex off Jakarta, Indonesia. Biodiversity and Conservation 15: 3653–3674. Dirhamsyah, D. 2006. Indonesian legislative framework for coastal resources management: A critical review and recommendation. Ocean & Coastal Management 49; 68-92. Edinger, E.N., Kolasa, J. & Risk, M.J. 2000. Biogeographical variation in coral species diversity on coral reefs in three regions of Indonesia. Diversity and Distributions 6: 133-127. Edinger, E,N & Risk, M.J. 2000. Reef classification by coral morphology predicts coral reef conservation value. Biological Conservation 92: 1-13. Fenner, D. 2002. Reef corals of the Raja Amput Islands, Papua Province, Indonesia – Comparison of Survey Sites. In: A Marine Rapid Assessment of the Raja Amput Islands, Papau Province, Indonesia . Eds. McKenna, S.A. Allen, G.R. & Suryadi, S. RAP Bulletin of Biological Assessment 22: 191. Fenner, D. 2002b. Reef corals of the Togean and Banggai Islands,Sulawesi, Indonesia. In: A Marine Rapid Assessment of the Togean and Banggai Islands, Sulawesi, Indonesia . Eds. Allen, G.R. & McKenna, S.A. Conservation International. Haapkyla, J., Seymour, A.S., Trebilco, J. & Smith, D. 2007. Coral disease prevalence and coral health in the Wakatobi Marine Park, south-east Sulawesi, Indonesia. Journal of the Marine Biological Association of the United Kingdom 87: 403-414. Hagen, A.B., Foster, R., Perera, N., Gunawan, C.A., Silaban, I., Yaha, Y., Manuputty, Y., Hazam, I., & Hodgson, G. 2007. Tsunami impacts in Aceh province and north Sumatra, Indonesia. Atoll Research Bulletin 544: 37-54 Obura, D., Fenner, D., Hoeksema, B., Devantier, L. & Sheppard, C. 2008. IUCN Red List of Threatened Species. Accessed 11 May 2009. Green, E., & Shirley, F. 1999. The Global Trade in Corals. World Conservation Monitoring Centre. World Conservation Press. Marshall, P.A. & Baird, A. H. 2000. Bleaching of corals on the Great Barrier Reef: differential susceptibilities among taxa. Coral Reefs 19: 155-163. Rachello-Domen, P.G. & Cleary, D.F.R. 2007. Relating coral species traits to environmental conditions in the Jakarta Bay/Pulau Seribu reef system, Indonesia. Estuarine, Coastal and Shelf Science 73: 816-826 Suharsono. 2008. Jenis-jenis karang de Indonesia. Indonesian Institute of Sciences. Jakarta. Tazioli, S., Bo, M., Boyer, M., Rotinsulu, H. & Bavestrello, G. 2007. Ecological Observations of Some Common Antipatharian Corals in the Marine Park of Bunaken (North Sulawesi, Indonesia). Zoological Studies 46(2): 227-241 Turak, E. 2003. Coral diversity and distribution. In: Rapid Ecological Assessment Wakatobi National Park . Eds. Pet-Soede, L.& Erdmann, M. Marine Program, WWF Indonesia. Turak, E. & Souhoka, J. 2003. Coral Diversity and the Status of Coral Reefs in the Raja Ampat Islands. In: Report on a rapid ecological assessment of the Raja Ampat Islands, Papua, Eastern Indonesia held October 30 – November 22, 2002. The Nature Conservancy. Turak, E. & Wakeford. M. 2002. Banda Islands Rapid Ecological Assessment, May 2002: Assessment of Coral Biodiversity and Coral Reef Health. Australian Institute of Marine Science. Veron, J. E. N. 2000. Corals of the world. 3 vols. Australian Institute of Marine Science and CRR Qld Pty Ltd. Veron, J. E. N 2002. Reef corals of the Raja Amput Islands, Papua Province, Indonesia – Overview of Scleractinia. In: A Marine Rapid Assessment of the Raja Amput Islands, Papau Province, Indonesia . Eds. McKenna, S.A. Allen, G.R. & Suryadi, S. Conservation International.

Wilkinson, C. 2004. Status of Coral Reefs of the World. Australian Institute of Marine Science. Zann, L. P. and Bolton, L. 1985. The distribution, abundance and ecology of the blue coral Heliopora caerulea (Pallas) in the Pacific. Coral Reefs 4: 125-134.

REVIEW OF SPECIES SELECTED ON THE BASIS OF A NEW OR INCREASED EXPORT QUOTA IN 2009

ANTHOZOA PECTINIIDAE

SPECIES: Pectinia lactuca

SYNONYMS: Madrepora lactuca, Tridacophyllia lactuca

COMMON NAMES: Carnation Coral (English), Frilly Lettuce Coral (English)

RANGE STATES: Australia, China (?), Cocos (Keeling) Islands, Fiji, India, Indonesia, Japan, Kenya, Madagascar, Malaysia, Maldives, Marshall Islands, Mauritius, Myanmar, New Caledonia, Palau, Papua New Guinea, Philippines, Réunion, Seychelles, Singapore, Solomon Islands, Taiwan, Province of China, Thailand, Vanuatu, Viet Nam,

RANGE STATE UNDER REVIEW: Indonesia

IUCN RED LIST: Vulnerable

PREVIOUS EC OPINIONS: A positive opinion for all countries was formed on 22/07/1997. TRADE PATTERNS: Pectinia lactuca from Indonesia was selected for review on the basis of an increased export quota for 2009 combined with its globally Vulnerable status. A quota of 2350 live wild specimens was published for 2003 to 2007, which decreased in 2008 to 2250 and then increased to 2500 in 2009. A quota for specimens derived from mariculture was set for 2004 and 2005, but in 2007 a zero quota for mariculture products was set. Exports of 40 specimens were reported by Indonesia in 2007, apparently exceeding the zero quota (Table 16). The major importing countries in the EU were France, Germany and United Kingdom and all trade was directly from Indonesia. Outside of the EU, the main importer by far was the United States with lesser quantities going to Japan, the Republic of Korea and Taiwan, Province of China. Indonesia has not submitted export quotas for maricultured corals to the CITES Secretariat for 2009. Table 13. Direct exports of Pectinia lactuca from Indonesia to EU-27, 2002-2007. All trade was in live specimens for commercial purposes and units were blank.

Importer Source Reported by 2002 2003 2004 2005 2006 2007 Total

Belgium W Importer 14 27 41

Importer Source Reported by 2002 2003 2004 2005 2006 2007 Total

Exporter 10 7 30 47

Cyprus W Importer 3 3

Exporter 3 3

Czech Republic W Importer 3 1 6 10

Exporter 5 3 1 12 21

Denmark W Importer 11 21 5 2 19 58

Exporter 21 19 5 15 9 69

France F Importer

Exporter 30 30

W Importer 60 464 377 238 231 187 1557

Exporter 37 545 392 205 243 179 1601

Germany W Importer 66 108 252 224 272 258 1180

Exporter 164 210 252 291 241 278 1436

Hungary W Importer 11 11

Exporter 30 1 31

Italy W Importer 5 21 16 14 56

Exporter 15 4 24 24 29 96

Latvia W Importer

Exporter 14 14

Lithuania W Importer 15 15

Exporter 2 17 19

Netherlands F Importer

Exporter 10 10

W Importer 33 172 36 58 20 22 341

Exporter 40 158 79 42 35 53 407

Poland F Importer

Exporter 20 20

W Importer 5 3 18 32 58

Exporter 1 5 19 21 9 55

Portugal W Importer 2 2

Exporter 27 5 2 13 47

Romania W Importer

Exporter 3 3

Spain W Importer 1 26 35 32 19 38 151

Exporter 5 29 29 27 43 19 152

Sweden W Importer 10 2 23 35

Exporter 10 2 23 35

United Kingdom W Importer 89 163 89 185 526

Exporter 56 89 163 94 195 597

Importer 160 796 832 762 700 794 4044 Totals Exporter 247 1121 906 801 721 897 4693

There were no indirect exports of Pectinia lactuca originating in Indonesia to EU-27, 2002-2007.

Table 14. Direct exports of Pectinia lactuca from Indonesia to countries other than EU-27, 2002-2007. All trade was in live specimens for commercial purposes and units were blank.

Importer Source Reported by 2002 2003 2004 2005 2006 2007 Total

Brazil W Importer

Exporter 28 36 47 14 8 133

Canada W Importer 3 6 71 24 104

Exporter 37 59 26 89 39 82 332

China W Importer

Exporter 10 10

Hong Kong W Importer 11 31 42

Exporter 15 24 3 40 11 93

Israel W Importer

Exporter 5 8 5 9 27

Japan F Importer

Exporter 80 20 100

W Importer

Exporter 104 109 133 267 297 237 1147

Kuwait W Importer

Exporter 1 26 4 17 21 69

Macao W Importer

Exporter 19 19

Malaysia W Importer

Exporter 2 33 29 24 41 20 149

New Zealand W Importer

Exporter 6 8 5 8 27

Norway W Importer 2 2

Exporter 3 5 8

Republic of Korea W Importer 45 1 13 50 109

Exporter 28 84 14 19 80 24 249

Russian Federation W Importer

Exporter 2 10 4 32 45 93

Singapore W Importer

Exporter 14 14

South Africa W Importer 55 31 32 118

Exporter 15 35 39 51 12 152

Switzerland F Importer

Exporter 11 11

W Importer 27 43 13 83

Exporter 23 29 15 18 5 1 91

Importer Source Reported by 2002 2003 2004 2005 2006 2007 Total

Taiwan, Prov. of China F Importer

Exporter 50 50

W Importer

Exporter 34 79 112 132 116 37 510

Turkey W Importer

Exporter 20 20

United States F Importer

Exporter 5 66 71

W Importer 84 99 253 503 320 242 1501

Exporter 260 685 607 872 767 932 4123

Importer 87 99 386 618 414 355 1959 Subtotals Exporter 549 1185 1063 1700 1515 1486 7498

Table 15. CITES Export quotas for Pectinia lactuca from Indonesia and associated global exports, reported by importer and exporter. All quotas refer to live wild specimens.

1999 2000 2001 2002 2003 2004 2005 2006 2007 2008 2009

Quota 900 900 1000 800 2350 2350 2350 2350 2350 2250 2500

Reported by importer 127 264 388 247 895 1218 1380 1114 1149

Reported by exporter 805 898 984 796 2306 1964 2274 2216 2343

Table 16. CITES Export quotas for Pectinia lactuca from Indonesia and associated global exports, reported by importer and exporter. All quotas refer to pieces – mariculture products from the 2003/2004/2005 product plan.

2004 2005 2006 2007

Quota 2000 1420 - 0

Reported by importer 0 0 0 0

Reported by exporter 6 227 20 40

CONSERVATION STATUS in range states Pectinia lactuca has a widespread distribution from the East African coast including Madagascar to the Red Sea and Gulf of Aden, the East and West Indian Ocean including Sri Lanka and the Maldives, Japan and the South China Sea, the waters around Indonesia and the western and eastern coasts of Australia, to the Pacific Islands (Veron, 2000). It occurs in most reef environments especially lower reef slopes and turbid water habitats and was described as a “common” species (Veron, 2000). Colonies reportedly reach one metre or more in diameter (Wood 1983 cited in Sheppard et al ., 2008). In the South China Sea it has been found to occur at depths of 12-15 metres but rarely from 9-11 m, however in other locations it occurs at shallower depths from 3m (Sheppard et al. , 2008). There is no species specific population information available for P. lactuca. However, declines are inferred based upon the known reduction of habitat quality resulting from estimates of destroyed coral reef and coral reef at a critical stage of degradation within the species range (Sheppard et al. , 2008). Coral decline is a general global phenomenon, and Wilkinson (2004) estimated that 24% of coral reef globally is under imminent risk of collapse through human pressures. The rate of coral decline and reef habitat quality in the Indo-Pacific has been significant (Bruno & Selig, 2007).

The genus Pectinia is highly susceptible to coral bleaching (Baird & Marshall, 2000). Additional localised events that can threaten coral reef communities include coral disease, pollution, invasive species and human development activities; however the severity of these combined threats to the global population of P. lactuca is unknown (Sheppard et al. , 2008). The susceptibility of P. lactuca to known threats such as coral bleaching, disease and trade increases the likelihood of the species being lost within a generation from reefs at a critical stage and accordingly, a population reduction of 38% over three generation lengths is inferred by the IUCN, meeting the threshold for the Vulnerable category (Sheppard et al. , 2008). Indonesia: Pectinia lactuca is found in locations scattered across the whole of Indonesia from north-west Sumatra, Java and the Moluccas, Kalimantan, Sulawesi, the Banda Islands and West Papua (Suharsono, 2008). In a survey of 33 sites in three Indonesian regions of Ambon (Moluccas), South Sulewesi and the Java Sea, Pectinia lactuca was found to occur in two sites in Ambon, at the reef wall at Tanjung Setan at a depth of 10 meters on the edge of the deep water Saram Strait, and at the Wayame fringing protected reef at a depth of 10m (Edinger et al ., 2000). In a rapid ecological assessment of the Raja Ampat Islands in the province of Papua, East Indonesia, which cover an area of four million hectares, P. lactuca was found to occur over a large geographic area at 35 of 51 dive survey sites off the islands of Salawati, Bantanta, Misool, Kofiau, Weigeo, Sayang, Wayag, Quoy, Uranie, Kawe, and Waigeo (Turak & Souhoka, 2003). The dominant species in each of several community types (protected communities in bays, single depth communities and communities around bays with strong headlands) were determined by relative abundance or number of individuals at each site classified categorically; P. lactuca was reported as a dominant species within the Raja Ampat archipelago in single depth communities found far in a narrow inlet, and in mixed community types, and was also found as one of the most common species in communities with high soft coral cover and areas with high species diversity and coral cover in both shallow (<8m) and deep waters (>10m), (Turak & Souhoka, 2003). Overall coral reef communities in the Raja Ampat area were considered to be in very good health during the 2002 surveys and six established protected areas were noted as established within the archipelago which are likely to include P. lactuca ; however, enforcement of the site designation within Raja Ampat was noted at that time as inefficient (Turak & Souhoka, 2003). In a similar assessment of 45 sites in 2001, P. lactuca was found to be widespread in the Raja Ampat islands (Veron, 2002), with the species confirmed at 29 sites (Fenner, 2002a). During rapid ecological assessments in 2002, Pectinia lactuca was found at every one of the 18 survey sites of the six major islands of the Banda group of islands of the Maluku region of Indonesia, which mostly comprise narrow fringing reefs without any intertidal reef flat (Turuk & Wakeford, 2002). The surveys included shallow water coral communities (8-10m) and deep reef at a depth of 12-30m; P. lactuca was one of the most abundant corals in deep water community types with steep slopes (Turuk & Wakeford, 2002). In a similar rapid assessment study of the Togean and Benggai islands of Sulawesi, Fenner (2002b) confirmed the occurrence of P. lactuca at 17 sites in Togean islands and 17 sites of the Benggai islands of a total of 47 sites sampled. A wide range of reef types were represented where the species occurred, including sheltered fringing reefs typically on the periphery of islands, exposed reefs, offshore reefs which typically arise from deep water, atoll reefs and barrier reefs (Fenner, 2002b). P. lactuca was recorded in 21 of 27 coral reef sites surveyed in the Wakatobi National Marine Park situated between the Banda and Flores seas in southwest Sulawesi, Indonesia which covers 1.39 million ha during a rapid ecological assessment in 2003 (Turak, 2003). It was found to have a wide geographic spread across this area and was recorded in all of the islands surveyed in at least one site, including Buton, Karang-Kapota, Wangi-Wangi, Kaledupa, Tomia, Binongka, Ndaa, Cowocowo, Koromaha, and Tokabao (Turak, 2003). The same study found that P. lactuca was not a dominant species in any of five community types, which were determined by depth (either shallow or deep water), varying coral species richness and reef

exposure. Coral damage was seen at most sites but at relatively low levels, however the Wakatobi area is relatively protected from coral bleaching by upwellings of cool waters from the south (Turak, 2003). Coral disease prevalence in Wakatobi Marine Park is recorded to be low (Haapkyla et al ., 2007). UNESCO surveyed coral assemblages in 28 patch reefs associated with islands throughout the Palau Seribu (Thousand Island) reef complex and National Park (which includes Jakarta Bay) in north-west Java in 1985, and data were analysed by Cleary et al . (2006). The genus Pectinia was not identified as a significant species across sites with varying disturbance levels (Cleary et al ., 2006). Similar to the situation for the global population, there are no estimates available for the size of the Indonesian population of P. lactuca . Indonesia is at the centre of a global coral diversity hotspot in South East Asia. Anthropogenic stress combined with global change threats places coral reefs in the Indo-Pacific region at high risk of collapse (Sheppard et al. , 2008). Whilst the status of coral reefs in general in South East Asia continues to show an overall decline in reef condition, it is notable that Indonesia has shown some slight improvements in reef condition from 1999-2004 (Wilkinson, 2004). Dirhamsyah (2006) suggests that the legal framework of sixteen laws on coastal and coral reef resources management in Indonesia is too complex and inappropriate, which in general has led to poor implementation and degradation of coral resources.

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