Review of selected corals from Indonesia

UNEP-WCMC technical report

Review of selected corals from Indonesia

(Version edited for public release)

2 Review of selected corals from Indonesia

Prepared for The European Commission, Directorate General Environment, Directorate E - Global & Regional

Challenges, LIFE ENV.E.2. – Global Sustainability, Trade & Multilateral Agreements, Brussels,

Belgium

Prepared June 2015

Copyright European Commission 2015

Citation UNEP-WCMC. 2015. Review of selected corals from Indonesia. UNEP-WCMC, Cambridge.

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3 Contents

Introduction ....................................................................................................................................... 4

Coral management in Indonesia ...................................................................................................... 5

Catalaphyllia jardinei II/B ................................................................................................................ 10

Euphyllia cristata II/B ....................................................................................................................... 14

Plerogyra sinuosa II/B ....................................................................................................................... 18

Plerogyra turbida II/B ...................................................................................................................... 23

Eguchipsammia fistula II/B ............................................................................................................. 27

Heliofungia actiniformis II/B........................................................................................................... 30

Hydnophora microconos II/B .......................................................................................................... 35

Blastomussa wellsi II/B .................................................................................................................... 39

Scolymia vitiensis II/B ...................................................................................................................... 43

Mycedium elephantotus II/B ........................................................................................................... 47

Trachyphyllia geoffroyi II/B ............................................................................................................. 50

References ............................................................................................................................................. 56

Appendix ................................................................................................................................................ 61

4 Introduction This document provides a review of ten coral taxa that have been subject to long term import suspensions for Indonesia, and one coral species (Mycedium elephantotus) for which a new 2014 quota was published retrospectively in 2015.

In informal discussions in the margins of the 27th Animals Committee Meeting in April 2014,

Indonesia requested clarification on the status of imports of 12 taxa, which are all subject to EU

import suspensions (H. Perier in litt. to UNEP-WCMC, 25/09/2014). Following correspondence on

these long-term suspensions, Indonesia provided further information on the management of the

coral harvest and trade, and the status of these species in Indonesia (Scientific Authority of

Indonesia, 2014). The following taxa were queried by Indonesia, three of which are considered to

be synonyms by CITES; this is discussed in more detail in the individual reviews:

- Cynarina lacrymalis (reviewed for SRG70)

- Catalaphyllia jardinei

- Euphyllia cristata

- Plerogyra sinuosa

- Nemenzophyllia turbida (synonym of Plerogyra turbida)

- Dendrophyllia fistula (synonym of Eguchipsammia fistula)

- Heliofungia actiniformis

- Hydnophora microconos

- Blastomussa wellsi

- Scolymia vitiensis

- Trachyphyllia geoffroyi

- Wellsophyllia radiata (synonym of Trachyphyllia geoffroyi)

It was agreed that a review by the SRG of the import suspensions for these taxa would be useful.

At its 70th meeting, the SRG decided to, in the meantime, replace the suspensions for these

species with negative opinions (SRG70 SoC).

Information from the Scientific Authority of Indonesia was provided to UNEP-WCMC in 2014 and

has been incorporated into these species reviews. Views from coral experts which were sought

during the preparation of document SRG 70/10, including from Lyndon DeVantier (Coral Reef

Research), Asuka Ishizaki (Protected Species Coordinator, Western Pacific Regional Fishery

Management Council) and J. E. N. Veron, have also been incorporated into this report. Veron

highlighted that the website ‘Corals of the World’ would be released at the end of 2014 or soon

after, and that this would provide a key resource for decisions in the context of corals (J. E. N.

Veron in litt. to UNEP-WCMC, 2014). As of 28/05/2015, the website was not released.

Since 2008, Indonesia has reported maricultured corals in trade as source F, in line with EU

reporting, instead of reporting them as source ‘W*’, as it had done previously. It is difficult to

compare the proportions of wild-sourced and maricultured coral imports before that change in

reporting, as EU imports of wild-sourced corals prior to 2008 may be artificially high, due to some

maricultured corals having been misreported as wild-sourced by the EU. Also since 2008,

Indonesia has established Maximum Estimated Production (MEP) for coral mariculture, which

generally indicated the expected production per facility and per taxon for half a year at a time.

Full trade data is available here: https://db.tt/uoID7NN7 (direct trade) and

https://db.tt/3FVbaFNw (indirect trade).

5 Coral management in Indonesia A summary of the status of corals in Indonesia, the main threats affecting them, and the management actions taken is provided below, with particular focus on the management of the harvest and trade of corals in Indonesia (for a full review see UNEP-WCMC, 2014).

Status and trends Indonesia was reported to have experienced a rapid decline of marine resources over the last

three decades, with urgent conservation measures needed (Allen, 2008). The status of reefs (Table

2) was considered to be poorest in western Indonesia in 2000 (Dirhamsyah, 2005) and the

condition of coral reefs was found to have declined over the period 2004-2008 (Wilkinson, 2008),

with many reefs considered severely damaged (Scaps et al., 2007).

Table 2: Some assessments of the status of Indonesian reefs over time

Reef status 2000 20111 2014

Poor 32.3% 30.8% 30%

Fair 35.3% 36.9% 37.7%

Good 25.5% 27.0% 26.8%

Excellent 6.7% 5.6% 5.3%

Reference: (Dirhamsyah, 2005) (COREMAP, 2011; in: Asian Development Bank, 2014)

(Scientific Authority of Indonesia, 2014; in litt. to European Commission)

The Scientific Authority (SA) of Indonesia (2014; in litt. to UNEP-WCMC) believed that the

condition of the reef and live coral cover had improved over the period 1993-2014, particularly

since the establishment of COREMAP (The National Policy, Strategy and Action Plan) in the late

1998s (Suharsono, 2008b). COREMAP management actions were also believed to have

contributed to increases in coral cover in eastern Indonesia over the period 2006-2011 (Giyanto,

2011).

Threats In the mid-2000s, 70% of Indonesian coral reefs were considered to be threatened (Dirhamsyah,

2005) and the Center for Ocean Solutions (2009) later considered the majority of the coral reefs to

be under “moderate to severe risk”.

Destructive fishing practices were considered the main threat to corals (Burke et al., 2011;

Dirhamsyah, 2005; Wilkinson, 2008; Center for Ocean Solutions, 2009; Turak and DeVantier,

2003; Scientific Authority of Indonesia, 2014; in litt. to European Commission), with up to 80% of

coral cover destroyed in some areas by fishing with explosives (Center for Ocean Solutions, 2009).

Further significant threats included offtake for trade and local uses (including construction and

lime production) (Bentley, 1998; Dirhamsyah, 2005; Scaps et al., 2007), pollution (Turak and

DeVantier, 2003; Dirhamsyah, 2005; Scaps et al., 2007), coastal construction and tourism

(Dirhamsyah, 2006; Turak and DeVantier, 2003).

The damage through the harvest of marine organisms for the aquarium trade was considered to be

“relatively slight” compared to other human-induced impacts (Reksodihardjo-Lilley and Lilley, 2007;

Wabnitz et al., 2003). While the illegal trade in corals globally was considered to be substantial

1 Percentage of live coral cover: ‘poor’: 0–24%; ‘fair’: 25–49%; ‘good’: 50-74%; ‘excellent’: 75–100%.

6 (Jones, 2008), the SA of Indonesia (2014; in litt. to UNEP-WCMC) believed that it was "almost

impossible", due to controls in place in Indonesia and importing countries. However, it is worth

noting that importers did report some trade from Indonesia under source code I within their CITES

annual reports 2003-2012.

Damage caused by natural disturbances also threaten coral reefs (Scientific Authority of Indonesia,

2014; in litt. to European Commission; Wilkinson, 2008) and bleaching was considered significant,

with up to 100% of bleaching of susceptible species in some areas (GCRMN, 2010).

Protection and management Regulatory background The regulation of marine resources in Indonesia was considered to be complex, with 17 laws relating

to coastal and marine management, 15 to ocean activities and two to the ratification of international

conventions (Asian Development Bank, 2014). Several laws and regulations are relevant for the

management of coral reefs (Dirhamsyah, 2006).

The regulation of coral harvest falls within the Decree of The Minister of Forestry No. 447/Kpts-

II/2003, regulating inter alia the allocation of quotas, collection sites and roles of stakeholders

(Scientific Authority of Indonesia, 2014; in litt. to European Commission). Only live corals can be

traded in Indonesia; the policy having been introduced to encourage collectors to reduce damage

and mortality of harvested corals (Scientific Authority of Indonesia, 2014; in litt. to European

Commission).

While the governance of coastal and ocean resources was reported to lie with the State, many other

agencies, departments and ministries are also involved (Asian Development Bank, 2014). Overall,

the legal and non-legal instruments were considered of limited effectiveness in managing the

marine and coastal resources and ecosystems (Dirhamsyah, 2005; Asian Development Bank, 2014).

Protected areas The number of Marine Protected Areas (MPAs) that include coral reefs was estimated at 30-50

(Center for Ocean Solutions, 2009), and Wilkinson (2008) estimated that 9% of Indonesian coral

reefs were within MPAs. In 2008, out of 114 actively managed MPAs overall, less than 3% were

considered well-managed (Wilkinson, 2008). NOAA (2012) reported that the majority of

Indonesian MPA’s lacked any management activities, although the Asian Development Bank

(2014) reported much activity to focus on strengthening MPA management, including

encouraging community involvement. In study of Spermonde Archipelago, Glaser et al. (2010)

noted that knowledge of the protected area programme amongst local people was poor.

Coral reef management The National Policy, Strategy and Action Plan, also known as ‘Coral Reef Rehabilitation and

Management Program’ (COREMAP) (Suharsono, 2008b) started in 1998, with its last phase running

until 2018 (Asian Development Bank, 2014). The project aims at sustainable use of the coral reef

ecosystem (Asian Development Bank, 2014) through community awareness and education; control

and surveillance; research and monitoring; community-based management; and institutional

strengthening” (Suharsono, 2008a; Scientific Authority of Indonesia, 2014; in litt. to European

Commission).

Coral harvest Indonesia was reported to have adopted the following principles for coral harvest:

• the establishment of no-take zones (Bruckner, 2001) by prohibiting harvest within

protected areas and tourism sites (Samedi and Liman, 2002);

7 • limiting harvest to assessed sites and allowing recovery of exploited sites (Samedi and

Liman, 2002) through rotational harvest (Bruckner, 2001), with a minimum of 4 years

between harvest cycles (Suharsano and Bruckner, 2008);

• limiting harvest to immature specimens through species-specific size limits (Samedi and

Liman, 2002), with a maximum of 15cm for massive corals and 25cm for branching corals

(Bruckner, 2001; Indonesia CITES Management Authority, 1999; in: Wood, 2001); and

conducting population monitoring (Samedi and Liman, 2002).

The SA of Indonesia (2014; in litt. to UNEP-WCMC) explained that quotas were being set by the

Management Authority (MA), with input from the SA and other stakeholders, including exporters.

Quotas were reported to be established based on the following assumptions: reef accretion rates are

1-1.5 cm per year, coral growth rates are 2.5-30 cm per year, and harvest occurs on approximately

30% of the reefs that are in good to excellent condition (Suharsono, 1999; in: Bruckner and

Borneman, 2006). On that basis, an overall coral harvest of 1 million colonies per year was believed

to represent the take of 0.00035% of the coral reef area assessed as in good to excellent condition

(Suharsano and Bruckner, 2008). Furthermore, Indonesia was reported to categorize coral taxa into

five categories, depending on a) the size of the colonies, b) their relative frequency, c) relative

dominance and d) hard coral cover; the category then stipulates the level of harvest as follows: very

common (harvest allowed), common (cautious harvest), uncommon (limited harvest), rare (strictly

limited harvest) and very rare (harvest prohibited) (Buckner and Suharsono 2008; based on

Suharsono and Giyanto, 2006). Timotius et al. (2009) noted that over the period 1999-2007, the

majority of exported wild-sourced corals were slow-growing, with faster growing corals traded at

much lower levels. Fist sized corals were believed to have taken 6 months to 10 years to grow to that

size (Bruckner, 2000).

Harvest sites were reported to be selected based on the province and coral abundance, with

annual assessments to assist with establishing the quotas (Scientific Authority of Indonesia, 2014;

in litt. to European Commission). The determination of collection sites was however thought to

not consider the species composition of sites (Timotius et al., 2009).

The harvest of live corals takes place in 11 provinces (Scientific Authority of Indonesia, 2014; in litt.

to European Commission): Lampung, West Java, Banten, Bangka-Belitung, Central Java, East Java,

West Nusa Tenggara, East Nusa Tenggara, South Sulawesi, Southeast Sulawesi and Central

Sulawesi (Suharsano and Bruckner, 2008; Figure 1). The SA of Indonesia (2014) reported that “Field

monitoring may be done once a year in the harvest site to obtain further information in order to

help determine the quota. The harvest site is determined based on the province and on coral

abundance. The province-based quota is established to prevent overharvesting at a certain

concentrated sites. The distribution of harvest areas will avoid overexploitation in certain sites.”

The largest collection area was reported to be located within the Spermonde archipelago in south-

west Sulawesi (Bruckner and Borneman, 2006). The total reef area of this archipelago was

estimated at 4290 km2, and in the mid-2000s, coral covers of 15-85% were observed at sites used

by coral collectors (Bruckner and Borneman, 2006). The average size of the corals then was 5-

24cm diameter, with only 1.5% of corals exceeding 100cm, thus making the vast majority of

colonies available for collection in that area (Bruckner and Borneman, 2006). Collection quotas

for some species were considered to have been set too high, allowing the annual removal of 1-96%

of the standing stock of individual species in the Spermonde archipelago; the authors pointed out

that for some taxa there was a considerable disconnect between the harvest level and the taxon’s

abundance. The IUCN recommended for a number of coral species that the effects of coral

harvest for the aquarium trade be assessed in Indonesia, and highlighted the need for adequate

management steps to be put in place to ensure sustainability of offtake (IUCN, 2014).

8 The export quotas were reported to represent 90% of the allowable harvest, allowing for some

losses during the collection process (Suharsano and Bruckner, 2008). However, the quotas were

considered to have little meaning in terms of understanding the full impact of offtake on taxa, as

no records have to be kept of the actual harvest levels and losses of harvested corals through

damage and mortality (Lilley, 2001). Such losses through poor handling during the trade chain

were considered to be frequent in Indonesia, leading to the collection of more stock than ordered

to compensate for these losses (Reksodihardjo-Lilley and Lilley, 2007).

Indonesian coral exporters are required to be part of the Indonesian coral, shell and ornamental

fish association (AKKII) (Scientific Authority of Indonesia, 2014; in litt. to European Commission).

In 2001, AKKII was reported to have 18 licensed exporters, each of them having their own divers

without middlemen and providing training in species identification, collection and handling

(Bruckner, 2001). However, a study of livelihoods of coral fishermen in the Spermonde

Archipelago reported that the implementation of laws and government regulations related to

ornamental coral collection appeared largely dysfunctional (Ferse et al., 2012). It was recognized

that if local communities were unable to extract aquarium resources from the wild, other

unsustainable human impacts on the reef would continue (Rhyne et al., 2014). However, the

authors believed that where sustainability of wild harvests cannot be achieved due to low

governance capacity, mariculture should be encouraged instead (Rhyne et al., 2014).

Mariculture

The Indonesian Government is moving towards mariculture of corals (Scientific Authority of

Indonesia, 2014; in litt. to European Commission), aiming at completely ceasing trade in wild-

sourced corals once sufficient corals can be produced through mariculture (Suharsano and

Bruckner, 2008). In 2007, approximately 25 facilities were reported to be actively exporting

maricultured corals from Indonesia (Timotius et al., 2009), with coral culture taking place both in

land-based facilities and in the sea (Reksodihardjo-Lilley and Lilley, 2007).

Coral mariculture is regulated under the Ministry of Forestry Regulation No. P.19/Menhut-II-2005

on captive management of wild plants and animals and PHKA Regulation No. 09, January 2008 on

Guidelines of Ornamental Coral Transplantation for Commercial Purposes (Timotius et al., 2009).

Regulation No. P.19/Menhut-II-2005 specifies that permits are needed for captive breeding and the

export of captive-bred specimens (unofficial English translation was provided by Indonesia with

their Biennial Report in 2007). The same regulation requires coral traders to return 10% of

propagated corals to their natural habitats - this policy was believed not yet be fully implemented

(Asian Development Bank, 2014). Mariculture operations are subject to biannual inspections, with

poor performance over two assessments resulting in mariculture permits being revoked (Scientific

Authority of Indonesia, 2014; in litt. to European Commission). Operations that successfully

mariculture a new species were reported to be allocated the full export quota for a period of two

years (Scientific Authority of Indonesia, 2014; in litt. to European Commission).

Since 2008, Indonesia has established Maximum Estimated Production (MEP) figures for coral

mariculture, which represent the expected production per facility and per taxon for half a year at a

time. The MEP figures were reported to be calculated on the basis of maximum breeding success

and the number of adult breeding stock, and distributed among companies through the AKKII

(Timotius et al., 2009).

9

Indicates provinces where coral collection takes place (based on Suharsano and Bruckner, 2008).

Figure 1: Indonesia, based on UN map No. 4110 Rev. 4, and provinces as of 25/10/2012.

1: Aceh 16: East Kalimantan/ North Kalimantan 2: Bali 17: Lampung 3: Bangka-Belitung 18: Maluku 4: Banten 19: North Maluku 5: Bengkulu 20: West Nusa Tenggara 6: Gorontalo 21: East Nusa Tenggara 7: Papua/West Papua 22: Riau 8: Jakarta 23: South Sulawesi/West Sumatra 9: Jambi 24: Central Sulawesi 10: West Java 25: Southeast Sulawesi 11: Central Java 26: North Sulawesi 12: East Java 27: West Sumatra 13: West Kalimantan 28: South Sumatra 14: South Kalimantan 29: North Sumatra 15: Central Kalimantan 30: Yogyakarta

10 SCLERACTINIA: CARYOPHYLLIDAE

Catalaphyllia jardinei II/B

Trade patterns Between 2003 and 2014, Indonesia published CITES export quotas every year for wild-sourced

Catalaphyllia jardinei (Table 3). Quotas for wild specimens have generally been declining, with the

lowest quota of 19 000 published in 2013 and 2014. Trade appears to have remained within quota

for most years for wild-sourced corals, except in 2012 and 2013, according to data reported by

Indonesia. Additionally, in 2005 and 2007, Indonesia published CITES export quotas for

maricultured C. jardinei (Table 3). The zero quota in 2007 for maricultured C. jardinei appears to

have been exceeded, according to data reported by the importer (the United States of America); a

permit check appears to suggest that the Indonesian export permit was issued in 2007.

Direct exports of C. jardinei from Indonesia comprised moderate levels of trade to the EU and

very high levels of trade to the rest of the world 2004-2013; trade was mainly in live, wild-sourced

individuals exported for commercial purposes (Table 4, Figure 1). Small amounts of source ‘I’

trade (123 specimens) were also reported by importers in this period. In addition, very small

volumes of wild sourced trade for non-commercial purposes and source ‘U’ trade for commercial

purposes were also reported 2004-2013.

SYNONYMS: Pectinia jardinei

COMMON NAMES: Elegant Coral

RANGE STATES: Australia, Fiji, Indonesia, Japan, Madagascar, Malaysia, Maldives, Papua New Guinea, Philippines, Seychelles, Solomon Islands, Tonga, Viet Nam

UNDER REVIEW: Indonesia

EU DECISIONS: Current negative opinion for wild specimens (excluding maricultured

specimens) from Indonesia formed on 08/12/2014. Previous Article 4.6(b)

import restriction for wild specimens first applied on 19/09/1999 and last

confirmed on 04/09/2014. The suspension has excluded maricultured

specimens since 18/02/2005.

Current positive opinion for wild specimens from Australia formed on

03/12/2010 and confirmed on 02/12/2011.

Current no opinion for Fiji formed on 15/01/2004 replacing negative

opinion formed on 22/05/2003.

Current Article 4.6(b) import restriction for wild specimens from Solomon

Islands first applied on 10/05/2006 and last confirmed on 28/05/2015.

Previous negative opinion formed on 09/10/2003.

Negative opinion for wild specimens from Tonga formed on 22/04/2005

and removed on 12/06/2006.

IUCN: Vulnerable

11 Indirect exports of C. jardinei originating in Indonesia to the EU-28 consisted of very low levels of

live, wild-sourced corals exported for commercial purposes, mainly via the United States of

America (Table 5).

Table 3: CITES export quotas exports for Catalaphyllia jardinei (in number of pieces) from Indonesia and global direct exports, as reported by the countries of import and Indonesia, 2004-2013. Trade data for 2014 are not yet available. ‘Mariculture’ includes source C, F and R (no trade in sources F and R was reported in 2005 and 2007).

2004 2005 2006 2007 2008 2009 2010 2011 2012 2013 2014

WILD

Quota 27500 26500 26500 26500 23850 26500 25000 22500 20000 19000 19000

Live Importer 20339 22031 23877 20990 15940 15075 21715 12971 13273 11785

Exporter 22820 25108 25498 26443 23842 26289 24853 20802 21147 24386

Raw corals Importer 1586 158 54 281 2568 3460 3012 2321 1621 875

Exporter MARICULTURE

Quota

1000

0 Live &

Raw Importer 25 6 15 13 45 21 272

Exporter 721

Source: CITES Trade Database, UNEP-WCMC, Cambridge, UK, downloaded on 24/03/2015

Table 4: Main direct commercial exports of Catalaphyllia jardinei from Indonesia to the EU-28 (EU) and the rest of the world (RoW), 2004-2013. ‘Mariculture’ includes sources C, F and R’.

Importer Term (unit) Source Reported by 2004 2005 2006 2007 2008 2009 2010 2011 2012 2013

EU

live (kg)

W Importer 1000

Exporter

live mariculture Importer 60

Exporter 140

W Importer 30 30 58 15 40 10 15 24

Exporter 142 204 188 231 153 279 203 130 409 109

raw corals

W Importer 10

Exporter

RoW

live (kg)

W Importer 67 7 30

Exporter

live mariculture Importer 25 6 15 13 40 21 200

Exporter 581

W Importer 20309 21996 23819 20975 15900 15075 21705 12971 13258 11761

Exporter 22678 24901 25310 26212 23689 26010 24650 20672 20738 24277

raw corals

mariculture Importer 5 12

Exporter

W Importer 1586 158 54 271 2568 3460 3012 2321 1621 875

Exporter


Table 5: Indirect exports of Catalaphyllia jardinei originating in Indonesia to the EU-28, 2004-2013 (No trade was reported in 2004 or 2010-2013).

Reported by 2005 2006 2007 2008 2009 Total

Importer 45 5 50

Exporter 1 2 8 19 3 33


12

Figure 1: Direct imports of wild-sourced (includes source U and unspecified) raw and live Catalaphyllia jardinei from Indonesia to the EU-28 and the rest of the world (RoW), 2004-2013 for commercial purposes (purpose T and unspecified), as reported by the importers.

Conservation status The genus Catalaphyllia contains only one species: C. jardinei, which is zooxanthellate [symbiotic

with microalgae] (Veron, 2000) and ahermatypic [not a main contributor to the reef matrix]

(Atkinson et al., 2008b). Colonies are either free living or attached (Borneman, 2002) and mature

colonies can reach 100 cm in diameter (Wood, 1983). C. jardinei was reported to occur in shallow,

tropical reef environments (Turak et al., 2008d) and in protected, often turbid water (Veron,

2000). The depth range of the species was reported to be 0-40 m (Turak et al., 2008d). Some

authors considered C. jardinei to be a habitat specialist (Atkinson et al., 2008a; Roelofs and

Silcock, 2008), preferring soft bottom habitats such as seagrass beds, algal flats and sandy or

muddy substrates (Suharsano and Bruckner, 2008; Bruckner and Borneman, 2006) and at areas at

river mouths (Lilley, 2001). Turak et al. (2008d) reported that the species occurred in a variety of

reef biotypes, although being especially common on soft substrates, rather than in areas of dense

coral growth.

C. jardinei is gonochorous (individuals are unisexual) (Wabnitz et al., 2003). The age at sexual

maturity was assumed to be three to eight years (Turak et al., 2008d), based on most reef building

corals having been reported to reach maturity at that age (Wallace, 1999). The average generation

length was assumed to be 10 years (Turak et al., 2008d). C. jardinei was observed to be slow

growing, with linear growth rate estimates of 0.8-15.2 cm per year (Green and Shirley, 1999).

C. jardinei was reported to be widespread in the Indo-West Pacific and oceanic west Pacific

(Turak et al., 2008d).

The species was categorised as Vulnerable by the IUCN (Turak et al., 2008d). Re-assessment in 10

years was considered important, due to predicted threats from climate change and ocean

acidification (Turak et al., 2008d). Veron (2000) reported C. jardinei to be seldom common and

rare in the western Indian Ocean. Turak et al. (2008d) also reported it as rare.

Harvesting for the aquarium trade was reported as a threat to C. jardinei (Turak et al., 2008d). The

species was identified as one of the seven most popular coral species in trade (Wabnitz et al.,

2003) particularly as it is colourful with large polyps (Green and Shirley, 1999). In aquaria,

C. jardinei was considered to “survive robustly” (Green and Shirley, 1999), with low mortality

reported (Wabnitz et al., 2003). It was assessed as having moderate vulnerability to harvesting

(Suharsano and Bruckner, 2008) and it was noted that the species was conspicuous and easily

identified (Turak et al., 2008d).

0

5000

10000

15000

20000

25000

30000

EU28 RoW

EU trade restriction

13 In addition to the global threats to corals posed by climate change, localised threats to coral reef

communities were reported to include pollution, invasive species, changing native species

dynamics, as well as human development activities, however, the combined threats to the global

population of C. jardinei were reported to be unknown (Turak et al., 2008d). C. jardinei was

reported to have low susceptibility to coral bleaching compared with other species (Roelofs and

Silcock, 2008).

Indonesia: The distribution of C. jardinei in Indonesia was mapped by Suharsono (2008a) who

reported it to be scattered throughout Indonesian waters. C. jardinei was reported from Banten

(western Java) (Suharsono, 2008a), Central Java, East Java, West Java, East Nusa Tenggara

(Komodo, Rinca), West Nusa Tenggara (Lombok), Bangka-Belitung Islands (off Sumatra),

Lampung (south Sumatra) (Lilley, 2001), West Sumatra (Suharsono, 2008a), Southeast Sulawesi

(Turak and DeVantier, 2011), South Sulawesi (Spermonde Reefs, Take Bonarate), Central Sulawesi

(Lilley, 2001), and North Sulawesi (Scaps et al., 2007). It was also reported from Bali (Turak and

DeVantier, 2011), Maluku province (Ambon Island) (Lilley, 2001), and West Papua (Suharsono,

2008a). Suharsono (2008a) reported that it was found in the Kendari area where suitable habitat

was abundant (Southeast Sulawesi).

Bentley (1998) reported C. jardinei to be uncommon across Indonesia. It was reported to be the

dominant species on Amulewang Reef (Central Sulawesi) in the Banda Sea on shallow reef flats

among seagrass beds (Lilley, 2001) but was reported as rare in the Spermonde Archipelago (South

Sulawesi) (Yusuf and Rani, 2006 in Yusuf and Jompa, 2012). Donnelly et al. (2003) reported

C. jardinei from two of 51 sites surveyed at Raja Ampat Islands (Papua) in 2002, but McKenna et al.

(2002) had not recorded the species during a survey of 45 sites in the same region. Whilst the

species was observed in the Lembeh strait (North Sulawesi), it was not observed during a survey

of 21 sites in the same area and considered rare (Scaps et al., 2007). It was reported from each of

five sites surveyed in Nusalaut Island (Maluku) (Souhoka, 2009) and from one of 29 dives sites in

Wakatobi (Southeast Sulawesi) (Hoeksema, 2003).

The species was reported to be easily harvested from areas, where it was found to grow partly

embedded in soft substrate (Lilley, 2001). It was mainly collected from deep-water sites where the

species grows as small free-living colonies (Borneman, 2002). A green variety from Lampung

(Sumatra) was reported to be particularly sought after (Lilley, 2001).

Bruckner and Borneman (2006) believed that the harvest quota for C. jardinei did not allow for

sustainable levels of harvest in the Spermonde region (South Sulawesi). This area was reported to

be one of the four main ornamental coral collection sites in Indonesia (Ferse et al., 2012). In an

assessment of coral resources in East Belitung (off Sumatra) presented at a conference, a quota of

1000 colonies was mentioned for the province, but C. jardinei was noted not to have been

recorded during dive surveys (Johan et al., 2014).

C. jardinei was reported to difficult to propagate and captive-propagated specimens were

considered to be extremely uncommon (Wood et al., 2012; Borneman, 2008). Suharsono (2014)

contains images of C. jardinei apparently in mariculture but provides no further information on

locations, quantities or mariculture of the species in Indonesia.

At its 25th meeting, the Animals Committee (AC) included C. jardinei (all range States) in the

Review of Significant Trade process (AC25 Summary Record). Following the consultation process,

Indonesia was not retained in the review (AC26 Summary Record).

14 SCLERACTINIA: Caryophylliidae

Euphyllia cristata II/B

Trade patterns Euphyllia cristata was listed in CITES Appendix II on 18/01/1990 through the listing of the order

Scleractinia. Exports of E. cristata reported by Indonesia have been between 25,000-32,000 live

wild specimens per year during the period 2004-2013 and trade has been within or close to the

quota in most years (Table 6).

The quota for E. cristata has decreased from 30,100 wild pieces in 2004 to 23,000 in 2014.

However, the total reported exports of 29,370 live wild pieces in 2013 appears to have exceeded

the quota of 23,500 pieces for that year by almost 6000 pieces (Table 6). However, this apparent

quota excess may be due to Indonesia reporting on the basis of permits issued rather than actual

trade, and therefore actual trade levels may be less than the volumes reported.

COMMON NAMES: White Grape Coral

RANGE STATES: American Samoa, Australia, Fiji, Indonesia, Japan, New Caledonia, Papua New Guinea, Philippines, Solomon Islands, Taiwan, Province of China, Vanuatu, Viet Nam


EU DECISIONS: Current negative opinion for Euphyllia cristata (excluding maricultured specimens) formed on 08/12/2014 and current no opinion i) for Euphyllia spp. raw corals formed on 07/11/2014. Previous Article 4.6(b) for Indonesia applied on 10/05/2006 (excluding maricultured specimens) and last confirmed on 04/09/2014. Previous positive opinion formed on 22/07/1997 but replaced by a negative opinion on 11/07/2000.

Current positive opinion for Australia and Fiji formed on 22/07/1997 and confirmed on 07/11/2014.

Current no opinion i) for American Samoa formed on 07/11/2014. Previous positive opinion formed on 22/07/1997.

Current no opinion i) for Japan, New Caledonia, Papua New Guinea, Philippines, Solomon Islands, Taiwan, Province of China, Vanuatu and Viet Nam formed on 02/12/2011 and confirmed on 07/11/2014. Previous positive opinion for these countries formed on 22/07/1997.

Current positive opinion for raw corals of Euphyllia spp. from Australia formed on 07/11/2014, and current no opinion i) for raw corals of Euphyllia spp. formed on 07/11/2014 for American Samoa, Australia, British Indian Ocean Territory (United Kingdom), Cocos (Keeling) Islands, Djibouti, Guam, India, Israel, Japan, Madagascar, Malaysia, Maldives, Marshall Islands, Mauritius, Micronesia (Federated States of), Myanmar, New Caledonia, Northern Mariana Islands, Oman, Palau, Papua New Guinea, Philippines, Samoa, Seychelles, Singapore, Solomon Islands, Sri Lanka, Taiwan, Province of China, Thailand, Vanuatu, Viet Nam.

IUCN: VU

15 Indonesia established a quota of 2400 pieces of E. cristata from mariculture in 2005 and a zero

quota for mariculture specimens in 2007. It has not established a quota for mariculture since

then, although some trade in mariculture specimens has been reported with relatively high levels

in 2013 (Table 7). The Scientific Authority of Indonesia (2014) indicated that E. cristata has been

successfully cultured.

Table 6: CITES export quotas for wild-sourced Euphyllia cristata from Indonesia and global direct exports, as reported by the countries of import and Indonesia 2004-2013. Importer reported trade data for 2013 may be incomplete; trade data for 2014 are not yet available.

Year 2004 2005 2006 2007 2008 2009 2010 2011 2012 2013 2014

Quota (wild) 30100 30100 30100 30100 27900 32000 29500 28000 25000 23500 23000

Importer 27378 31432 26698 27246 26767 23279 18013 16648 14832 12341

Exporter 25814 27535 29227 30029 27829 31735 29337 26745 25772 29370

Source: CITES Trade Database, UNEP-WCMC, Cambridge, UK, downloaded on 24/03/2015.

Low level imports of wild specimens into the EU have been reported 2004-2013 by both Indonesia and EU countries, despite the trade suspension being in place (Table 7, Figure 2). Relatively low levels of trade in source ‘I’ specimens were reported by importers during this period (218 specimens). Very small volumes of wild sourced commercial trade in raw corals to the EU were also reported by importers (24 raw corals). Wild sourced trade for non-commercial purposes and commercial trade in sources other than W, C and F was also reported at low levels.

Table 7: Main direct commercial exports of Euphyllia cristata from Indonesia to the EU-28 (EU) and the rest of the world (RoW), 2004-2013. (Source ‘mariculture’ includes trade recorded as source ‘F’ and ‘C’).

Importer Term Source Reported by 2004 2005 2006 2007 2008 2009 2010 2011 2012 2013

EU live mariculture Exporter 50 1248

Importer 39 573

W Exporter 265 618 401 185 185 309 344 245 172 165

Importer 149 92 35 48 41 8 11 38

RoW live mariculture Exporter 150 5396

Importer 34 10 36 20 226 626

W (kg) Exporter

Importer 19 30

W Exporter 25549 26917 28826 29844 27644 31426 28993 26500 25600 29205

Importer 27229 31340 26663 27246 26719 23279 17972 16640 14821 12303

raw corals

W Exporter

Importer 1247 23 146 508 1885 2264 2593 2273 1905 1179


Indirect exports of E. cristata originating in Indonesia to the EU-28 comprised very low levels of

live wild and captive-born corals re-exported for commercial purposes, primarily via the United

States of America (Table 8).

Jones (2008) suggested that the genus Euphyllia was the fourth most confiscated coral genus in

the UK during the period 2000-2007.

16 Table 8: Indirect exports of live Euphyllia cristata originating in Indonesia to the EU-28, 2004-2013. All trade was in live corals for commercial purposes. Source Reported by 2004 2005 2006 2007 2008 2009 2010 2011 2012 2013

F Exporter 10

Importer 14 10

W Exporter 3 5 52 20

Importer 7


Figure 2: Direct imports of wild-sourced (includes source U and unspecified) raw and live Euphyllia cristata from Indonesia to the EU-28 and the rest of the world (RoW), 2004-2013 for commercial purposes (purpose T and unspecified), as reported by the importers.

Conservation status Euphyllia cristata is a reef building coral (Scientific Authority of Indonesia, 2014) found in shallow

reef environments (Veron, 2000), usually existing in small colonies at depths of 1-35 m (Turak et

al., 2014b). The age at maturity was assumed to be three to eight years, based on most reef-

building corals having been reported to reach sexual maturity at that age (Wallace, 1999).

Widespread throughout its range, it was reported to be both rare and moderately common by

Turak et al. (2014b), and uncommon but conspicuous by Veron (2000). The species was

categorised as being globally common in Veron (2014), on the basis of semi-quantitative data on

relative abundance from 2984 individual survey sites in 30 ecoregions across the Indo-west Pacific

from 1994 to 2012. However, the overall assessment of the species by Veron, based on his

extensive experience, was that it was globally uncommon (Veron, 2014). Differences between the

two estimates are likely to be due to the species being relatively abundant in specific ecoregions

which can affect semi-quantitative records (Veron, 2014).

The species was categorised as Vulnerable by the IUCN in 2014 (Turak et al. 2014b). Specific

population trends are unknown, however, there is evidence of declines in the extent and quality

of coral reef habitat which has been used as a proxy for population decline of this species (Turak

et al., 2014b). The estimated habitat degradation and loss of 36% over three generation lengths (30

years) is the best inference of population reduction (Turak et al., 2014b).

Turak et al. (2014b) reported that E. cristata was heavily harvested for the aquarium trade. The

species was reported to be particularly susceptible to bleaching, disease, and other threats (Turak

et al., 2014b). However, other authors considered the genus to have a relatively low susceptibility

to coral bleaching (Wilson et al., 2012; Roelofs and Silcock, 2008). Rachello-Dolmen and Cleary

0

5000

10000

15000

20000

25000

30000

35000

EU28 RoW


17 (2007) considered Euphyllia species to be “stress tolerators”, able to occur in areas of high

sedimentation or eutrophication.

Indonesia: E. cristata was reported have a relatively wide distribution throughout Indonesian

waters (Scientific Authority of Indonesia, 2014; Suharsono, 2008a). It was reported to be found in

shallow waters to depths of more than 20 m; it can be found in clear waters to turbid ones close to

estuaries (Scientific Authority of Indonesia, 2014). The species has been found in Bali and adjacent

regions, including Komodo (East Nusa Tenggara Province), Wakatobi (South Sulawesi), Derewan

(East Kalimantan) and Bunaken National Park (North Sulawesi) (Turak and deVantier, 2011).

Lilley (2001) referred to four areas in which the species was known to occur: Komodo and Rinca,

Sumbawa, and Lombok, all of which are in East Nusa Tenggara province.

A number of surveys have recorded the presence of E. cristata in Indonesia:

• In nine different areas visited during the Snellius-II Expedition in 1984 (Best et al., 1989), E. cristata was found at two: north-east Komodo and Sumbawa.

• During a survey of the reefs of the Pulisan region, north-east Sulawesi, E. cristata was found in five of 21 sites (Scaps et al., 2007).

• E. cristata was not encountered in Jakarta Bay in 1920 and 2005 but it was observed in the offshore Thousand Islands archipelago in 2005 (van der Meij et al., 2010).

• The species was reported to occur in the Raja Ampat Islands, Papua, and Eastern Indonesia (Veron, 2002, in: McKenna et al., 2002). However, during a rapid ecological assessment in 2001, a total of 45 sites were surveyed for corals and E. cristata was found at none (McKenna et al., 2002). During another rapid ecological assessment in 2002 a total of 51 sites were surveyed for corals and E. cristata was found at 21 (Donnelly et al., 2003).

• In Bunaken National Park, the species was found in 23% of the 39 sites surveyed in 2003 (Turak and DeVantier, 2003).

The species was considered to be common in sheltered areas by the Scientific Authority of

Indonesia (2014) whereas it was described as rare, scattered across the waters of Indonesia by

Suharsono (2008a). Best et al., (1989) described it an “uncommon species adapted to soft bottom

conditions”. In Bunaken National Park, it was considered to have a moderately widespread local

distribution and was thought likely to form locally-reproductive populations (Turak and

DeVantier, 2003). Raymakers (2001) reported densities of E. cristata of 0-1/100 m2 in Spermonde

(South Sulawesi). Bruckner and Borneman (2006) found that the density of E. cristata in an area

of 1760 km2 in the Spermonde Archipelago was 0-0.01/m2, with a population estimate of 10,000.

Bruckner and Borneman (2006) reported that there were an estimated 1.8 million Euphyllia

colonies within Spermonde, however, abundance of individual species was highly variable and

only two species were common enough to support collection at existing quotas. E. cristata was

identified at only a single site and collection of the allowable quota would amount to

approximately 70% of the entire population (Bruckner and Borneman, 2006). The authors

estimated that 85% of colonies were within the legal size range as established by Indonesia and it

was assumed that 90% of the allocated quota is taken (Bruckner and Borneman, 2006).

Raymakers (2001) categorised E. cristata as one of the ‘most threatened species’ in Indonesia (of

those reviewed by that author) due to their scarcity and a high export quota. The author

suggested that imports should not be permitted until there are scientific estimates of the

population status in collection areas and proper management in place (Raymakers, 2001).

Nine species in the genus Euphyllia are reported to occur in Indonesia (Species+, speciesplus.net,

2015). However, much of the information in the scientific literature refers to the genus but does

not provide information on which species is being referred to (e.g. Jompa et al., 2007; Lilley, 2001;

Putra et al., 2014; Scaps & Runtukahu, 2008; Siringoringo et al., 2006; Suharsono and Giyanto,

2006).


Plerogyra sinuosa II/B

SYNONYMS: Euphyllia sinuosa, Plerogyra laxa

COMMON NAMES: Bladder Coral

RANGE STATES: American Samoa, Australia, British Indian Ocean Territory (United Kingdom), Djibouti, Egypt, Fiji, Guam, India, Indonesia, Israel, Japan, Kenya, Kiribati, Madagascar, Malaysia, Maldives, Marshall Islands, Mauritius, New Caledonia, Northern Mariana Islands, Palau, Papua New Guinea, Philippines, Saudi Arabia, Singapore, Solomon Islands, Sudan, Taiwan, Province of China, Thailand, Tonga (uncertain), United Republic of Tanzania, United States Minor Outlying Islands, Vanuatu, Viet Nam


EU DECISIONS: Current negative opinion (except maricultured specimens) formed on 08/12/2014. Previous no opinion i) formed on 07/11/2014. Previous positive opinion formed on 22/07/1997, replaced by a negative opinion for Plerogyra spp. on 11/07/2000 and Article 4.6(b) suspension (except maricultured specimens) from 18/02/2005, last confirmed on 04/09/2014.

Current positive opinion for Australia formed on 22/07/1997 and last confirmed on 07/11/2014.

Current positive opinion for Fiji formed on 15/01/2004 and confirmed on 07/11/2014. Previous positive opinion formed on 22/07/1997, replaced by a negative opinion formed on 22/05/2003.

Current no opinion i) formed on 02/12/2011 and confirmed on 07/11/2014 for American Samoa, British Indian Ocean Territory (United Kingdom), Djibouti, Egypt, Guam, India, Israel, Japan, Kenya, Kiribati, Madagascar, Malaysia, Maldives, Marshall Islands, Mauritius, New Caledonia, Northern Mariana Islands, Palau, Papua New Guinea, Philippines, Saudi Arabia, Singapore, Sudan, Taiwan, Province of China, Thailand, United Republic of Tanzania, United States Minor Outlying Islands, Vanuatu, Viet Nam. Previous positive opinions for these countries formed on 22/07/1997.

Current no opinion i) for the Solomon Islands formed on 28/05/2013 and confirmed on 07/11/2014. Previous positive opinion formed on 22/07/1997.

Current positive opinion for raw corals of Plerogyra spp. from Australia formed on 07/11/2014 and current no opinion i) for raw corals of Plerogyra spp. formed on 07/11/2014 for American Samoa, British Indian Ocean Territory (United Kingdom), Djibouti, Egypt, Guam, India, Israel, Japan, Kenya, Kiribati, Madagascar, Malaysia, Maldives, Marshall Islands, Mauritius, New Caledonia, Northern Mariana Islands, Palau, Papua New Guinea, Philippines, Saudi Arabia, Singapore, Solomon Islands, Sudan, Taiwan, Province of China, Thailand, United Republic of Tanzania, United States Minor Outlying Islands, Vanuatu, Viet Nam.

Previous Article 4.6(b) suspension for Tonga applied on 03/09/2008. Previous negative opinion formed on 25/07/2005.

IUCN: NT

19 Trade patterns The species was listed in CITES Appendix II on 18/01/1990 through the listing of the order

Scleractinia. Exports of Plerogyra sinuosa reported by Indonesia have typically been between

20,000 and 30,000 live wild pieces each year, and generally within quota (Table 9).

The quota for P. sinuosa has decreased from 29,000 wild pieces in 2004 to 23,000 in 2014.

However, the quotas established for 2012 and 2013, were exceeded according to trade reported by

Indonesia (Table 9, Figure 3). The total reported exports of 30,332 live wild pieces in 2013 were

higher than exports in any of the previous nine years, and appeared to have exceeded the quota of

23,500 pieces for that year by nearly 7000 pieces. However, this apparent quota excess may be due

to Indonesia reporting on the basis of permits issued rather than actual trade, and therefore

actual trade levels may be less than the volumes reported.

Indonesia established a quota of 1000 pieces of P. sinuosa from mariculture in 2005 and a zero


then, although very low level trade in mariculture specimens has been reported in several years

(Table 10).

Table 9: CITES export quotas for wild-sourced Plerogyra sinuosa from Indonesia and global direct exports, as reported by the countries of import and Indonesia 2004-2013. Importer reported trade data for 2013 may be incomplete; trade data for 2014 are not yet available.

2004 2005 2006 2007 2008 2009 2010 2011 2012 2013 2014

Quota (wild) 29000 28000 28000 28000 25650 28500 28500 28500 25000 23500 23000

Exporter 22931 25510 26195 27838 25576 28159 28371 27284 25791 30332

Importer 23489 27760 24007 25122 21755 21423 18941 20113 19120 16602


Low level imports of wild specimens into the EU have been reported 2004-2013 by both Indonesia

and EU countries, despite the trade suspension being in place (Table 10). Relatively low levels of

trade in source ‘I’ specimens were reported by importers during this period (222 specimens). In

addition, very small amounts of wild sourced trade for non-commercial purposes, trade in source

‘unknown’ and wild sourced trade in raw corals to the EU were also reported.

Jones (2008) reported that Plerogyra was the second most confiscated coral genus in the UK

during the period 2000-2007.

Table 10: Main direct commercial exports of Plerogyra sinuosa from Indonesia to the EU-28 (EU) and the rest of the world (RoW), 2004-2013. (Source ‘mariculture’ includes trade recorded as source ‘F’ and ‘C’).


EU live mariculture Exporter 120

Importer 80

W Exporter 346 315 246 193 146 264 116 201 259 199

Importer 131 24 8 15 25 105 86 82

RoW live mariculture Exporter 220

Importer 85 10 7 8 15 17 8 65

W Exporter 22585 25186 25949 27645 25430 27895 28255 27083 25532 3013

3

Importer 23358 27704 23999 25107 21755 21398 18931 20008 19034 1652

20 Importer Term Source Reported by 2004 2005 2006 2007 2008 2009 2010 2011 2012 2013

0

raw corals mariculture Exporter

Importer 6

W Exporter

Importer 1694 35 76 308 1786 2210 2198 2157 1488 1122


Indirect exports of P. sinuosa originating in Indonesia to the EU-28 comprised low levels of live wild corals re-exported for commercial purposes, primarily via Malaysia (Table 11).

Table 11: Indirect exports of live Plerogyra sinuosa originating in Indonesia to the EU-28, 2004-2013. All trade was wild sourced for commercial purposes. Reported by 2004 2005 2006 2007 2008 2009 2010 2011 2012 2013

Exporter 1 23 95 18

Importer 7 30


Figure 3: Direct imports of wild-sourced (includes source U and unspecified) raw and live Plerogyra sinuosa from Indonesia to the EU-28 and the rest of the world (RoW), 2004-2013 for commercial purposes (purpose T and unspecified), as reported by the importers.

Conservation status Plerogyra sinuosa is a reef-building coral with a colony size varying from 10 cm to more than 1 m

across (Scientific Authority of Indonesia, 2014). It is found in protected reef environments,

especially, but not necessarily, in turbid water (Veron, 2000). It occurs in depths of 3-35 m (Turak

et al., 2014a). The age at maturity was assumed to be three to eight years, based on most reef-


The species was categorised as Near Threatened by the IUCN in 2014 (Turak et al. 2014a). Specific

population trends are unknown, and therefore the decline in coral reef habitat, with about 20%

reefs already destroyed, has been used as a proxy for population decline of this species (Turak et

al., 2014a).

Veron (2000) described the species as “usually uncommon” and Turak et al. (2014a) reported that

“it is widespread and common throughout its range and therefore is likely to be more resilient to

habitat loss and reef degradation because of an assumed large effective population size”.

0

5000

10000

15000

20000

25000

30000

EU28 RoW


21 The main threat to P. sinuosa was reported to be extensive habitat loss due to a combination of

threats, and it is also heavily harvested for the aquarium trade (Turak et al., 2014a). In a study of

the impact of the 2010 coral bleaching event in Wakatobi National Park, Wilson et al. (2012)

classified the genus Plerogyra as relatively “resistant” to bleaching events.

It was reported to be a slow growing species and difficult to propagate, and limited success in

mariculture has been reported (Wabnitz et al., 2003; Wood et al., 2012).

Indonesia: P. sinuosa was reported to be widely distributed throughout Indonesian waters

(Scientific Authority of Indonesia, 2014; Suharsono, 2008a). It is commonly found on reef slopes

more than five meters deep, preferring crevices or small hanging walls (Scientific Authority of

Indonesia, 2014). While large colonies were reported to be frequently found on flat substrates or

small slopes, the corals in trade are mostly small (Scientific Authority of Indonesia, 2014).

P. sinuosa has been found in Bali and adjacent regions, including Komodo (East Nusa Tenggara

Province), Wakatobi (South Sulawesi), Derewan (East Kalimantan) and Bunaken National Park

(North Sulawesi) (Turak and deVantier, 2011). It was found in the waters of Padang, West

Sumatra, based on the collection of Bung Hatta University (Jonker and Johan, 1999). P. sinuosa

was considered to have a widespread local distribution in Bunaken National Park and likely to

form locally-reproductive populations (Turak and DeVantier, 2003).

A number of surveys have recorded the presence of P. sinuosa in Indonesia:

• In nine different areas visited during the Snellius-II Expedition in 1984, P. sinuosa was

found at five: north-east Komodo, Sumbawa, Taka Bone Rate, Salayer, south-west

Sulawesi (Best et al., 1989).

• During a Marine Rapid Assessment Program at the Togean and Banggai Islands in

Sulawesi in 1998, a total of 47 sites were visited and P. sinuosa was found at 14 (Allen and

McKenna, 2001).

• During rapid ecological assessments at Raja Ampat Islands, Papua, Eastern Indonesia in

2001, a total of 45 sites were surveyed for corals and P. sinuosa was found at 12 (McKenna

et al., 2002). In 2002, a total of 51 sites were surveyed for corals and P. sinuosa was found

at 18 (Donnelly et al., 2003).

• P. sinuosa was not encountered in Jakarta Bay in 1920 and 2005 but it was observed in the offshore Thousand Islands archipelago in 2005 (van der Meij et al., 2010).

• During a survey of the reefs of the Pulisan region, north-east Sulawesi, Plerogyra sinuosa was found in 10 of 21 sites (Scaps et al., 2007).

• During a study in 2007 in five locations at Nusalaut Island, Central Maluku District,

P. sinuosa was found at four (Souhoka, 2009).

• In Bunaken National Park in North Sulawesi, the species was found in 56% of the 39 sites surveyed in 2003 (Turak and DeVantier, 2003).

Four species in the genus Plerogyra are reported to occur in Indonesia (Species+, 2015). However,

much of the information in the scientific literature refers to the genus but does not provide

information on which species is being referred to. This includes the following information:

• Raymakers (2001) reported densities of Plerogyra spp. of 8-19/100 m2 in Spermonde

(South Sulawesi) and 33/100 m2 in Lampung (South Sumatra). The market size of

specimens was 5-10 cm, and the wild size was <50 cm (Raymakers, 2001). The author

categorised Plerogyra spp. as ‘threatened to a lesser extent’ (of those reviewed by that

author) with a low estimated abundance – 20-50 colonies/m2 - and a high export quota.

• Referring to the genus Plerogyra, Bruckner and Borneman (2006) stated that the density in an area of 1760 km2 in the Spermonde Archipelago was 0.08-0.19/m2, with a population estimate of 227,000.

22 • In three sites in Wakatobi Marine Park in south-east Sulawesi, Crabbe and Smith (2003)

found Plerogyra to be abundant at 10 and 15 m at Hoga and Kaledupa, but not at Sampela at 10 m. They suggested that this might be as a result of increased sedimentation at Sampela, which was not favourable to Plerogyra.

• During a survey of four sites in Bali (Hoeksema and Putra, 2000), Plerogyra spp. was found in two.

• In Lampung Bay, Lilley (2001) indicated that the estimated population density of Plerogyra spp. was 33 colonies per 100 m2 for sizes smaller than 50 cm and suggested that the genus may be common in Lampung Bay.

• Plerogyra was considered to be a rare genus in the vicinity of Kapoposang Island during a study in 1996 (Yusuf and Rani, 2006, in: Yusuf and Jompa, 2012).

• Using a methodology based on size of colony and frequency of occurrence, Suharsono and Giyanto (2006) described Plerogyra as rare in Bakauheni, Kepulauan Seribu and Teluk Cendrawasih suggesting that harvest should be strictly limited; they described it as very rare in Jepara suggesting that harvest should be prohibited.

Lilley (2001) noted that corals are collected from many sites throughout the archipelago and the

sites at which live corals are harvested, are chosen very selectively by the collectors. The genus

Plerogyra has been recorded in collection sites in Bali, Sumatra, Java, Sulawesi and West Timor

(Lilley, 2001).


Plerogyra turbida II/B

Taxonomic note Nemenzophyllia turbida is considered by CITES to be a synonym of Plerogyra turbida (UNEP-

WCMC, 2012). However, the name Nemenzophyllia turbida is used by Veron (2000), Cairns et al.

(1999), the Scientific Authority of Indonesia (2014), IUCN (Turak et al., 2008) and a number of

other authors. Veron (2000) recognised N. turbida, noting that he had formerly placed the species

in the genus Plerogyra. Veron (2000) also stated that if further research suggests that Plerogyra

discus is the same species, then Plerogyra would once again be applicable.

Trade patterns The species was listed in CITES Appendix II on 18/01/1990 through the listing of the order

Scleractinia.

Exports of P. turbida reported by Indonesia have been approximately 12,000-14,000 live wild

pieces each year (Table 12), and generally within quota. However, in 2013, according to trade

reported by Indonesia, the quota of 12,000 appeared to be exceeded by 2,413 pieces (Table 12) and

the total exports of 14,413 live wild pieces in 2013 are higher than exports in any of the previous

nine years. However, this apparent quota excess may be due to Indonesia reporting on the basis of

permits issued rather than actual trade, and therefore actual trade levels may be less than the

volumes reported. Up until 2012, Indonesia published quotas using the synonym N. turbida, but in

2013 and 2014, quotas were issued using the name P. turbida. Raymakers (2001) noted that during

interviews, collectors and traders stated that the two species can be identified without a doubt.

SYNONYMS: Nemenzophyllia turbida

COMMON NAMES: Jasmine Coral

RANGE STATES: Indonesia, Papua New Guinea, Philippines


EU DECISIONS: Current negative opinion for Plerogyra turbida (except maricultured

specimens) formed on 08/12/2014. Previous negative opinion for

Plerogyra spp. formed on 11/07/2000 and replaced with an Article 4.6(b)

suspension on 18/02/2005, last confirmed on 04/09/2014.

Current positive opinion for raw corals of Plerogyra spp. from Australia

formed on 07/11/2014 and current no opinion i) for raw corals of

Plerogyra spp. formed on 07/11/2014 for American Samoa, British Indian

Ocean Territory (United Kingdom), Djibouti, Egypt, Guam, India, Israel,

Japan, Kenya, Kiribati, Madagascar, Malaysia, Maldives, Marshall Islands,

Mauritius, New Caledonia, Northern Mariana Islands, Palau, Papua New

Guinea, Philippines, Saudi Arabia, Singapore, Solomon Islands, Sudan,

Taiwan, Province of China, Thailand, United Republic of Tanzania, United

States Minor Outlying Islands, Vanuatu, Viet Nam.

IUCN: VU

24 Low level imports of wild specimens into the EU have been reported 2004-2013 by both Indonesia

and EU countries, despite the trade suspension being in place (Table 13, Figure 4). Relatively low

levels of trade in source ‘I’ specimens were reported by importers during this period (195

specimens). Small quantities of wild sourced trade for non-commercial purposes were also traded

in this period. In addition, low levels of commercial trade in sources other than W, C and F were

also reported.

Table 12: CITES export quotas for wild-sourced Plerogyra turbida from Indonesia and global direct exports, as reported by the countries of import and Indonesia 2004-2013. Importer reported trade data for 2013 may be incomplete; trade data for 2014 are not yet available.

Year 2004 2005 2006 2007 2008 2009 2010 2011 2012 2013 2014

Quota (wild) 14000 14000 14000 14000 11700 12610 12610 12610 12000 12000 11000

Exporter 13269 12954 13280 13928 11661 12352 12558 10987 12929 14413

Importer 9000 7462 8392 7372 5534 4032 21209 2189 1899 551


Table 13: Main direct commercial exports of Plerogyra turbida from Indonesia to the EU-28 (EU) and the rest of the world (RoW), 2004-2013. (Source ‘mariculture’ includes trade recorded as source ‘F’ and ‘C’).


EU live mariculture Exporter 120

Importer 33

W Exporter 65 117 101 130 110 338 1445 387 970 397

Importer 5 5 5 5 14 39 10 9 31

RoW live W (kg) Exporter

Importer 20

W Exporter 13204 12834 13179 13798 11551 12014 11113 10600 11959 14016

Importer 8995 7437 8387 7367 5520 4032 21130 2179 1890 520

mariculture Exporter

Importer 68


Importer 42

W Exporter

Importer 526 100 154 89 1137 1548 2726 2341 2568 1666


Indirect exports of P. turbida originating in Indonesia to the EU-28 comprised very low levels of live wild corals re-exported for commercial purposes, via Malaysia and Singapore (Table 14).

Table 14: Indirect exports of live Plerogyra turbida originating in Indonesia to the EU-28, 2004-2013. All trade was wild sourced for commercial purposes. Reported by 2004 2005 2006 2007 2008 2009 2010 2011 2012 2013 Grand Total

Exporter 9 5 14

Importer 2 2


25

Figure 4: Direct imports of wild-sourced (includes source U and unspecified) raw and live Plerogyra turbida from Indonesia to the EU-28 and the rest of the world (RoW), 2004-2013 for commercial purposes (purpose T and unspecified), as reported by the importers.

CITES trade should be reported using the accepted CITES nomenclature. However, the majority

of trade in this species was reported using the synonym Nemenzophyllia turbida. Of 3,334

individual shipment records for 2010-2013, 96 were reported using the name Plerogyra turbida

with the remainder (97%) reported using the synonym, N. turbida. While trade to the EU was low

level, the majority of shipments imported were accepted using the name N. turbida.

Conservation status Plerogyra turbida was reported to be found in shallow, tropical reef environments, in turbid or

sheltered reef environments from 8-30 m (Turak et al., 2008b). The age at maturity was assumed

to be three to eight years, based on most reef-building corals having been reported to reach sexual

maturity at that age (Wallace, 1999).

The species [N. turbida] was categorised as Vulnerable by the IUCN in 2008 (Turak et al. 2008b).

Specific population trends are unknown, and therefore the decline in coral reef habitat, of 38%

over three generation lengths, has been used as a proxy for population decline of this species

(Turak et al., 2008b). Turak et al. (2008b) described the species [N. turbida] as “widespread and

rare throughout its range” and suggested that it may “form very large carpets and can be locally

abundant”. It was described as “rare, but conspicuous” by Veron (2000) and Turak et al. (2008b).

P. turbida was reported to be heavily harvested for the aquarium trade and has suffered an

extensive reduction of coral reef habitat due to a combination of threats (Turak et al., 2008b).

This species is particularly susceptible to bleaching, disease, and other threats (Turak et al.,

2008b). In a study of the impact of the 2010 coral bleaching event in Wakatobi National Park,

Wilson et al. (2012) classified the genus Plerogyra as relatively “resistant” to bleaching events.

Indonesia: The species [N. turbida] was reported to be widespread across Indonesia, with its

preferred habitat on offshore reefs, typically having a gentle slope ranging from 150 to horizontal

(Scientific Authority of Indonesia, 2014). It occurs in depths of more than 15 meters with a sandy

or muddy substrate and low light intensity (Scientific Authority of Indonesia, 2014). It was

reported to have a “clumped” distribution pattern, with occasional large patches of the species;

colonies are usually less than 100 cm across but occasionally form very large stand reefs which

consist mostly of a single species (Scientific Authority of Indonesia, 2014).

0

5000

10000

15000

20000

25000

30000

EU28 RoW


26 The distribution map provided in Suharsono (2008a) indicates that P. turbida occurs only in

eastern Indonesia, from Sulawesi eastwards. However, it was reported from collecion sites in the

following areas: Bali Strait; South Sumatra; North Sumatra; South Sulawesi; West Bali; West

Timor; West Java; West Java; East Java; Jawa Island, Central Java (Lilley, 2001). The species

[N. turbida] has also been found in Derewan (Turak and deVantier, 2011) and the Spermonde

Archipelago, South Sulawesi (Raymakers, 2001).

A number of surveys have recorded the presence of P. turbida in Indonesia:

• In nine different areas visited during the Snellius-II Expedition in 1984 (Best et al., 1989), P. turbida was found at one, north-east Komodo.

• During a Marine Rapid Assessment Program at Raja Ampat Islands, Papua, Eastern

Indonesia in 2001 (McKenna et al., 2002), a total of 45 sites were surveyed for corals and

P. turbida was not recorded. However, the authors noted that the species did occur in

eastern Indonesia, as reported by Veron (2000).

• During another rapid ecological assessment at Raja Ampat Islands, Papua, Eastern

Indonesia in 2002 (Donnelly et al., 2003) a total of 51 sites were surveyed for corals and

P. turbida was found at two.

The species considered to be rare by Suharsono (2008a). It was considered to be rare in the

vicinity of Kapoposang Island in the Spermonde Archipelago during a study in 1996 (Yusuf and

Rani, 2006, in: Yusuf and Jompa, 2012). Raymakers (2001) categorised [N. turbida] as threatened to

a lesser extent (of those reviewed by that author), with a low estimated abundance – 20-50

colonies/m2 and a high export quota.

In the Spermonde Archipelago, the species [N. turbida] was found at depths of 30 m at a density

of 220-790 colonies/100 m2 (Raymakers, 2001). Raymakers (2001) noted that the maximum

allowable depth for diving is about 20 m, which prevents scientists from surveying certain sites,

such as the largest patches of P. sinuosa [N. turbida] which have been observed at depths of 30-35

m in the Spermonde Archipelago. Bruckner and Borneman (2006) undertook a survey of 12

locations in the Spermonde Archipelago in Southwest Sulawesi, an area with approximately 150

islands which they reported was the largest coral collection area in Indonesia. They found that the

species [N. turbida] formed isolated, low-relief coral mounds in deeper (30-35 m) soft-bottom

nearshore locations (Bruckner and Borneman, 2006). Two patches were found in their study, each

about 100-300 m x 100 m wide, with densities of 5-8 colonies/m2 within the densest part of the

patch and an estimated maximum of 10,000 colonies in each patch (Bruckner and Borneman,

2006). The authors suggested that if these were the only populations of this species in

Spermonde, annual harvest of 3000 colonies could represent up to 30% of the total population

(Bruckner and Borneman, 2006). However, based on the extensive nature of deep, nearshore soft-

bottom environments and the distance between the patches surveyed in this study, they

estimated that the total population may exceed 800,000 colonies, in which case the annual

harvest would represent up to 0.4% of the total population (Bruckner and Borneman, 2006). The

authors also noted reports from coral collectors which indicated that several other aggregates

exist in similar environments (Bruckner and Borneman, 2006).

Corals in trade are small, under 15 cm across (Scientific Authority of Indonesia, 2014) to 21 cm

(Raymakers, 2001).

27 SCLERACTINIA: Dendrophylliidae

Eguchipsammia fistula II/B

Taxonomic note The Scientific Authority of Indonesia (2014) uses the name Dendrophyllia fistula, which is

considered by CITES to be a synonym of Eguchipsammia fistula (UNEP-WCMC, 2012), based on

Cairns et al. (1999). Similarly, Cairns (2014) considered D. fistula to be a synonym of E. fistula.


Scleractinia. Exports of Eguchipsammia fistula reported by Indonesia have been approximately

16,000-18,000 live wild pieces each year, and generally within quota (Table 15). However, no trade

was reported by Indonesia in 2011 and 2012.

The quota for E. fistula has decreased from 19,500 wild pieces in 2004 to 15,000 in 2014. In 2013,

according to trade reported by Indonesia, the quota of 15,000 appeared to be exceeded by over

3000 pieces (Table 15). However, this apparent quota excess may be due to Indonesia reporting on

the basis of permits issued rather than actual trade, and therefore actual trade levels may be less

than the volumes reported.

Indonesia established a zero export quota for pieces of E. fistula from mariculture in 2007. It has

not established a quota for mariculture since then, and some very low trade in mariculture

specimens has been reported (Table 16).

Table 15: CITES export quotas for wild-sourced Eguchipsammia fistula from Indonesia and global direct exports, as reported by the countries of import and Indonesia 2004-2013. Importer reported trade data for 2013 may be incomplete; trade data for 2014 are not yet available.

Year 2004 2005 2006 2007 2008 2009 2010 2011 2012 2013 2014

Quota (wild) 19500 19500 19500 19500 18900 18900 18900 18900 15500 15000 15000

Exporter 16388 18271 18893 19334 18859 18630 18831 18158

Importer 8479 11453 10790 10690 4198 3055 4823 4078 2865 469


SYNONYMS: Dendrophyllia fistula, Balanophyllia fistula

RANGE STATES: Australia, Indonesia, Japan, Maldives, Marshall Islands, Mozambique, New

Zealand, Philippines, United Republic of Tanzania, United States Minor

Outlying Islands, United States


EU DECISIONS: Current negative opinion for wild-sourced specimens from Indonesia formed

on 08/12/2014. Previous Article 4.6(b) suspension for wild-sourced applied

on 10/09/2012 and last confirmed on 04/09/2014. Previous negative opinion

formed on 14/09/2007 and confirmed on 02/12/2011.

IUCN: Not yet assessed.

28 CITES trade should be reported using the accepted CITES nomenclature, however in this case the

majority of trade was reported using the synonym Dendrophyllia fistula. Of 2373 individual

shipment records for 2010-2013, 113 were reported using the accepted name E. fistula with the

remainder (95%) reported under the name the D. fistula. While trade to the EU was low level, the

majority of shipments imported were accepted using the name D. fistula. Up until 2012, Indonesia

has published quotas using the name D. fistula, but in 2013 and 2014, quotas were issued using the

accepted name Eguchipsammia fistula.


and EU countries, despite the trade suspension being in place (Table 16, Figure 5). Relatively low

levels of trade in source ‘I’ specimens were reported by importers during this period (151

specimens) and small amounts of wild sourced carvings, wild sourced corals for non-commercial

purposes and live corals reported as sources other than W, F or C were traded during this period.

Table 16: Main direct exports of Eguchipsammia fistula from Indonesia to the EU-28 (EU) and the rest of the world (RoW), 2004-2013. (Source ‘mariculture’ includes trade recorded as source ‘F’ and ‘C’).


EU live W Exporter 7593 8389 8378 6564 649 1009 1832 440

Importer 6304 7319 6980 5490 63 111 84 56 163 33

raw corals W Exporter

Importer 188 85 178 7

RoW live mariculture Exporter

Importer 7 15 20

W Exporter 8795 9882 10515 12770 18210 17621 16999 17802

Importer 2175 4118 3810 5200 4135 2944 4739 4022 2727 436


Importer 5 5

W Exporter

Importer 1931 348 180 40 5190 5599 5175 5004 3684 2832


Figure 5: Direct imports of wild-sourced (includes source U and unspecified) raw and live Eguchipsammia fistula from Indonesia to the EU-28 and the rest of the world (RoW), 2004-2013 for commercial purposes (purpose T and unspecified), as reported by the importers.

0

2000

4000

6000

8000

10000

12000

EU28 RoW


29 Indirect exports of E. fistulata originating in Indonesia to the EU-28 comprised very low levels of

live wild corals re-exported for commercial purposes, primarily via Malaysia (Table 17).

Table 17: Indirect exports of live Eguchipsammia fistulata originating in Indonesia to the EU-28, 2004-2013. All trade was wild sourced for commercial purposes. Reported by 2004 2005 2006 2007 2008 2009 2010 2011 2012 2013

Exporter 23 39 9

Importer


Conservation status The Scientific Authority of Indonesia (2014) stated that Eguchipsammia fistula [Dendrophyllia

fistula] is a reef-building coral that is mostly found on steep reef slopes, hanging walls or in small

caves or overhangs in a shallow reef environment. As it is azooxanthellae, the corals do not need

sunlight to survive, and so they are able to occupy a wide range of habitats (Scientific Authority of

Indonesia, 2014). The age at maturity was assumed to be three to eight years, based on most reef-


The species has not yet been assessed by the IUCN.

Eguchipsammia [Dendrophyllia] species was found to easily be confused with Tubastraea species

underwater, as these genera were believed to be indistinguishable when they are alive and

without examination of the pattern of septa fusion (Scientific Authority of Indonesia, 2014; Veron,

2000).

Indonesia: Reported to be very common and widely distributed all over Indonesian waters at 1 –

20 m depth (Scientific Authority of Indonesia, 2014). However, the species is not mentioned in

key references such as Veron (2000), Suharsono (2008a) and the IUCN Red List, nor is it

mentioned in the numerous coral surveys that have taken place in various places in Indonesia.

This may be because it is not present in the habitats being surveyed e.g. if it prefers deeper water,

it is difficult to identify to species level, or because it is rare.

The Scientific Authority of Indonesia (2014) states that the number harvested and the export

quota have decreased steadily. This species was reported to have been successfully transplanted

[for mariculture] (Scientific Authority of Indonesia, 2014).

30 SCLERACTINIA: Fungiidae

Heliofungia actiniformis II/B


Scleractinia. Exports of Heliofungia actiniformis reported by Indonesia have been approximately

40,000-50,000 live wild pieces each year, and generally within quota (Table 18). The quota for

H. actiniformis has decreased from 49,000 wild pieces in 2004 to 37,000 in 2014.

However, the quotas established for 2012 and 2013, were exceeded according to trade reported by

Indonesia (Table 18). The total exports of 49,747 live wild pieces in 2013 were higher than exports

in any of the previous nine years, and appeared to exceed the quota for that year by more than

10,000 pieces. However, Indonesia’s annual report to CITES may be based on permits issued

rather than actual trade, and therefore actual trade levels may be less than the volumes reported.

Indonesia established a zero quota for mariculture specimens in 2007. It has not established a

quota for mariculture since then, although low level trade in mariculture specimens has been

reported in several years. Wabnitz et al. (2003) and Wood et al. (2012) reported limited success

with the mariculture of Heliofungia.

Table 18: CITES export quotas for wild-sourced Heliofungia actiniformis from Indonesia and global direct exports, as reported by the countries of import and Indonesia 2004-2013. Importer reported trade data for 2013 may be incomplete; trade data for 2014 are not yet available.

2004 2005 2006 2007 2008 2009 2010 2011 2012 2013 2014

Quota (wild) 49000 48500 48500 48500 40500 44650 44650 42750 40000 39000 37000

Exporter 40046 45529 46543 48266 40374 44131 44112 40230 41396 49747

Importer 35958 40275 33126 32318 22732 17504 26393 15518 16668 13514


SYNONYMS: Fungia actiniformis, Fungia crassitentaculata, Fungia diversidens

COMMON NAMES: Mushroom Coral, Disk Coral

RANGE STATES: Australia, Fiji, Indonesia, Japan, Malaysia, Mozambique, New Caledonia, Palau, Papua New Guinea, Philippines, Singapore, Solomon Islands, Taiwan, Province of China, Vanuatu, Viet Nam


EU DECISIONS: Current negative opinion for wild-sourced specimens from Indonesia

formed on 08/12/2014. Previous Article 4.6(b) suspension applied on

10/09/2012 and last confirmed on 04/09/2014. Previous negative opinion

formed on 14/09/2007 and confirmed on 02/12/2011.

IUCN: VU

31 Low level imports of wild specimens into the EU have been reported 2008-2013 by both Indonesia

and EU countries, despite the trade being suspension in place (Table 19, Figure 6). Low levels of

trade in source ‘I’ were reported by importers during this period (154 specimens). Very low levels

of wild sourced trade for non-commercial purposes were also reported. In addition, small

quantities of corals reported as sources other than W, C and F were traded for commercial

purposes.

Table 19: Main direct commercial exports of Heliofungia actiniformis from Indonesia to the EU-28 (EU) and the rest of the world (RoW), 2004-2013. (Source ‘mariculture’ includes trade recorded as source ‘F’ and ‘C’).


EU live W Exporter 10588 11385 10740 8486 1290 2058 2004 1278 1004 1177

Importer 9859 11070 8551 7324 128 10 79 20 62 48


Importer 232 147 20 163 10


Importer 42 15 10 10 6 23 20 40

W Exporter 29458 34130 35801 39780 39084 42073 42108 38952 40392 48570

Importer 26099 29165 24575 24994 22604 17494 26297 15498 16606 13466


Importer 2194 298 387 352 5957 7368 6648 6008 4443 3086


Figure 6: Direct imports of wild-sourced (includes source U and unspecified) raw and live Heliofungia actiniformis from Indonesia to the EU-28 and the rest of the world (RoW), 2004-2013 for commercial purposes (purpose T and unspecified), as reported by the importers.

Indirect exports of H. actiniformis originating in Indonesia to the EU-28 comprised relatively low

levels of live wild corals re-exported for commercial purposes, primarily via Malaysia (Table 20).

0

5000

10000

15000

20000

25000

30000

35000

EU28 RoW


32 Table 20: Indirect exports of live Heliofungia actiniformis originating in Indonesia to the EU-28, 2004-2013. All trade was wild sourced for commercial purposes. Reported by 2004 2005 2006 2007 2008 2009 2010 2011 2012 2013

Exporter 67 330 33

Importer 27


Conservation status This genus has one species, Heliofungia actiniformis, which is usually found on flat soft or rubble

substrates, especially in reef lagoons or shallow turbid environments (Veron, 2000). The depth

range is 1-25 m (Hoeksema 1990 in: Hoeksema et al., 2008). The size of H. actiniformis was

reported to vary, with adults growing up to 30 cm in diameter (Scientific Authority of Indonesia,

2014). The age at maturity was assumed to be three to eight years, based on most reef-building

corals having been reported to reach sexual maturity at that age (Wallace, 1999).

The species was categorised as Vulnerable by the IUCN in 2008 (Hoeksema et al., 2008). Specific

population trends are unknown, and therefore the decline in coral reef habitat, of 36% over three

generation lengths, has been used as a proxy for population decline of this species (Hoeksema et

al., 2008).

H. actiniformis was described as common by Veron (2000) and as widespread and locally

common throughout its range by Hoeksema et al. (2008).

This species is heavily harvested for aquarium trade and has suffered extensive reduction of coral

reef habitat due to a combination of threats (Hoeksema et al., 2008). This species was also

thoughts to be particularly susceptible to bleaching and disease (Wilkinson 2004 in: Hoeksema et

al., 2008). However, in a study of the impact of the 2010 coral bleaching event in Wakatobi

National Park, Wilson et al. (2012) classified the genus Heliofungia as relatively “resistant” to

bleaching events. In one study, 1% of the specimens were recorded as bleached (Hoeksema, 1991

in: Hoeksema et al., 2008). In a study on Indonesia reefs in Spermonde and Buton reefs in

Sulawesi Yusuf and Jompa (2012) found that Heliofungia was among the genera most resistant to

bleaching.

Indonesia: H. actiniformis was reported to be widely distributed in Indonesia (Scientific

Authority of Indonesia, Suhardono, 2008a). Its distribution was considered to be clumped, with

juveniles and adults found in one place (Scientific Authority of Indonesia, 2014).

H. actiniformis has been found in Bali and adjacent regions, including Komodo (East Nusa

Tenggara Province), Wakatobi (South Sulawesi), Derewan (East Kalimantan) and Bunaken

National Park (North Sulawesi) (Turak and deVantier, 2011). It was observed in Jakarta Bay in 1920

and 2005 and in the offshore Thousand Islands archipelago in 2005 (van der Meij et al., 2010). A

number of surveys have recorded the presence of H. actiniformis throughout Indonesia:


Sulawesi in 1998, a total of 47 sites were visited and H. actiniformis was found at 20 (Allen

and McKenna, 2001).

• In nine different areas visited during the Snellius-II Expedition in 1984, H. actiniformis

was found at six: Lucipara Islands, north-east Komodo, Sumbawa, Taka Bone Rate,

Salayer and South West Sulawesi (Best et al., 1989).

• Chou et al. (2010) noted that Heliofungia was recorded at Bintan Island in 2007 but not in

1993.

33 • During rapid ecological assessments at Raja Ampat Islands, Papua, Eastern Indonesia in

2001, a total of 45 sites were surveyed for corals and H. actiniformis was found at 17

(McKenna et al., 2002); in 2002, a total of 51 sites were surveyed for corals and

H. actiniformis was found at 20 (Donnelly et al., 2003).

• During a survey of four sites in Bali, H. actiniformis was found in all four (Hoeksema and

Putra, 2000).

• Putra et al. (2014) recorded Heliofungia at one of six study sites in in the Krakatau Islands.

• Hoeksema (2012) reported that H. actiniformis was found on all 13 reefs surveyed in Spermonde Archipelago (Makassar Strait, Indonesia) in 1984–1986; a total 342 individual corals were found in all transect sample units together (28,250 m2).

• Recorded at two of nine sites surveyed at the end of the Luwuk Pensinsula, Sulawesi in 2007 (Scaps and Runtukahu, 2008).

• During a survey of the reefs of the Pulisan region, north-east Sulawesi, E. cristata was found in 10 of 21 sites (Scaps et al., 2007).

• Reported in Bunaken National Park in North Sulawesi, where it was considered to have a widespread local distribution, occurring in 33% or more of the 39 sites surveyed in 2003 (Turak and DeVantier, 2003). The authors suggested that they are likely to form locally-reproductive populations (Turak and DeVantier, 2003).

The genus Heliofungia was recorded in the following collection sites: Banyuwangi, Bali Strait;

Belitung Island, south Sumatra; Binuangeun, west Java; Cilamaya, west Java; Gilmanuk West Bali;

Jepara Central Java; Kupang, West Timor; Labuhan, west Java; Lampung, south Sumatra; Madura

Island, east Java; Pulau Untung Jawa Island, Central Java; Sibolga, north Sumatra; and Ujung

Pandang, South Sulawesi (Lilley, 2001).

Only the green or brightly coloured specimens were reported to be collected for trade, and

usually those between 10 -15 cm in diameter, whereas the larger and duller specimens were not

collected (Kittweiss and Wolff, 2010; Scientific Authority of Indonesia, 2014). In the Spermonde

Archipelago, Knittweiss and Wolff (2010) found that almost all polyps larger than 11 cm were dull

brown colour morphs of no commercial value. Knittweiss and Wolff (2010) recommended that a

study on whether the gene pool of H. actiniformis was influenced by the selective harvesting of

colourful polyps was needed. In terms of polyp price, Knittweiss and Wolff (2010) found that

larger (8-11 cm) polyps with purple tentacles attained the highest price.

Suharsono (2008a) described the species as common, and scattered throughout Indonesian

waters. Using a methodology based on size of colony and frequency of occurrence, Suharsono and

Giyanto (2006) described Heliofungia as uncommon in Bakauheni, suggesting harvest should be

limited; rare in Kepulauan Seribu and Jepara, suggesting that harvest should be strictly limited;

and very rare in Teluk Cendrawasih, suggesting that harvest should be prohibited.

Hoeksema (2012) noted that during a field survey in 1984–1986 in the Spermonde Archipelago,

there were no signs of H. actiniformis fishing. However, Knittweis & Wolff (2010) suggested that

the highest quotas in Sulawesi were regularly allocated to H. actiniformis, with harvest quotas

being stable at 6,000 pieces (i.e. individual polyps) from 1999 to 2002, rising to 7,000 pieces in

2003 and stabilising at 9,500 pieces between 2004 and 2006 in the Spermonde Archipelago. The

authors found that harvesting practices had a high impact on the overall population structure, as

illustrated by a decline in young polyps at harvested sites compared to unharvested areas

(Knittweiss and Wolff, 2010). The authors noted that fishermen collect every coral that they feel

middlemen might buy, with middlemen then selecting a proportion of the corals, meaning that a

much higher number of H. actiniformis was harvested than permitted by the quotas (Knittweiss

and Wolff, 2010). Knittweiss and Wolff (2010) concluded that harvest quotas for H. actiniformis

should be reduced significantly and that a size limit of 5 cm limit should be introduced. Since

H. actiniformis only reaches reproductive maturity at a size of 8 cm (Abe, 1937), reductions in

34 fishing effort as well as a strict enforcement of existing marine protected areas would in addition

be imperative to protect this species’ spawning stock (Knittweiss and Wolff, 2010).

The Scientific Authority of Indonesia (2014) noted that reports stating that Heliofungia in

Supermonde and Makassar are smaller and depleted in number cannot be confirmed. It suggested

that coral was often depleted when next to big cities in Indonesia, as is the case in Spermonde

(Scientific Authority of Indonesia, 2014).

35 SCLERACTINIA: Merulinidae

Hydnophora microconos II/B


Scleractinia. Exports of Hydnophora microconos reported by Indonesia have been 4000-8000 live

wild pieces each year and generally within quota (Table 21).

The quota for H. microconos has increased from 4750 wild pieces in 2004 to 6500 pieces in 2014.

The quotas established for 2012 and 2013, appeared to be exceeded according to trade reported by

Indonesia (Table 21). The total exports of 8330 live wild pieces in 2013 were higher than exports in

any of the previous nine years, and appeared to exceed the quota of 6500 pieces for that year by

nearly 2000 pieces. However, Indonesia’s annual report to CITES may be based on permits issued

rather than actual trade, and therefore actual trade levels may be less than the volumes reported.

SYNONYMS: Monticularia microconos

RANGE STATES: American Samoa, Australia, Bangladesh, British Indian Ocean Territory (United Kingdom), China, Cocos (Keeling) Islands, Cook Islands, Djibouti, Egypt, Fiji, French Polynesia, Guam, India, Indonesia, Israel, Japan, Jordan, Kenya, Kiribati, Madagascar, Malaysia, Maldives, Marshall Islands, Mauritius, Micronesia (Federated States of), Mozambique, Myanmar, New Caledonia, Oman, Palau, Papua New Guinea, Philippines, Réunion, Saudi Arabia, Seychelles, Solomon Islands, South Africa, Sudan, Taiwan, Province of China, Thailand, Tonga, Tuvalu, United Republic of Tanzania, United States Minor Outlying Islands, Vanuatu, Viet Nam, Yemen


EU DECISIONS: Current negative opinion for wild-sourced specimens from Indonesia (except maricultured specimens) formed on 08/12/2014. Previous Article 4.6(b) suspension applied on 10/05/2006 and last confirmed on 04/09/2014. Previous negative opinion formed on 11/07/2000, replaced by a positive opinion on 15/50/2002 and with a negative opinion formed on 22/05/2003.

IUCN: NT

36 Table 21: CITES export quotas for wild-sourced and maricultured Hydnophora microconos from Indonesia and global direct exports, as reported by the countries of import and Indonesia 2004-2013. Importer reported trade data for 2013 may be incomplete; trade data for 2014 are not yet available.

2004 2005 2006 2007 2008 2009 2010 2011 2012 2013 2014

WILD

Quota 4750 4750 4750 4750 5850 6305 6305 6305 6500 6500 6500

Live Exporter 4503 4518 4539 4714 5829 6210 6254 5841 6812 8330

Importer 2706 3191 2776 2424 2222 1857 1288 2007 2157 1249

MARICULTURE

Quota 2000 579 1029

Live Exporter 270 395 240

Importer 125 5 6

Raw corals

Exporter

Importer 5



and EU countries, despite the trade suspension being in place (Table 22, Figure 7).

Indonesia established a quota for mariculture specimens in 2004, 2005 and 2007. It has not

established a quota for mariculture since then, although very low level trade in mariculture

specimens has been reported in 2011 and 2013.

Very low levels of source ‘I’ trade were reported by importers during this period. In addition, very

small amounts of wild sourced trade for non-commercial purposes were reported 2004-2013.

Table 22: Main direct commercial exports of Hydnophora microconos from Indonesia to the EU-28 (EU) and the rest of the world (RoW), 2004-2013. (Source ‘mariculture’ includes trade recorded as source ‘F’ and ‘C’).


EU live mariculture Exporter 30 145 98

Importer 125

W Exporter 292 144 155 247 353 398 449 244 307 283

Importer 65 87 12 30 37 50 9 3 22

RoW live mariculture Exporter 240 250 142

Importer 5 6

W Exporter 4211 4374 4384 4467 5476 5812 5805 5597 6505 8047

Importer 2641 3104 2764 2394 2185 1807 1279 2004 2157 1227


Importer 5

W Exporter

Importer 591 87 32 1226 1538 1298 1183 994 705


37

Figure 7: Direct imports of wild-sourced (includes source U and unspecified) raw and live Hydnophora microconos from Indonesia to the EU-28 and the rest of the world (RoW), 2004-2013 for commercial purposes (purpose T and unspecified), as reported by the importers.

Indirect exports of H. microconos originating in Indonesia to the EU-28 comprised very low levels

of live wild corals re-exported for commercial purposes, via Singapore (Table 23).

Table 23: Indirect exports of live Heliofungia actiniformis originating in Indonesia to the EU-28, 2004-2013. All trade was wild sourced for commercial purposes. Reported by 2004 2005 2006 2007 2008 2009 2010 2011 2012 2013

Exporter 5 5

Importer


Conservation status Hydnophora microconos was reported to be found in all reef environments, though primarily in

lagoons and protected slopes in the Pacific (Veron, 2000). Sheppard et al. (2014) considered the

species to be widespread throughout its range. The age at maturity was assumed to be three to

eight years, based on most reef-building corals having been reported to reach sexual maturity at

that age (Wallace, 1999).

The species was categorised as Near Threatened by the IUCN in 20014 (Sheppard et al., 2014).

Specific population trends are unknown, and therefore the decline in coral reef habitat, with 20%

of reefs already destroyed, has been used as a proxy for population decline of this species

(Sheppard et al., 2014).

It was described by Veron (2000) as an uncommon species, however, more recently Sheppard et

al. (2014) considered it to be common throughout its range.

The most important known threat was reported to be extensive reduction of coral reef habitat due

to a combination of threats, however, this species was also reported to be moderately susceptible

to bleaching and harvesting for aquarium trade (Sheppard et al., 2014).

Indonesia: The Scientific Authority of Indonesia (2014) reported that “Colonies are found on

almost all reefs from reef flats down to 15 meters depth, widely spread and common in Indonesia

and Brunei (Turak and DeVantier 2011)”. The distribution map provided in Suharsono (2008a)

indicated that H. microconos is relatively widely distributed in Indonesia, and occurs in Sumatra,

Java, Papua New Guinea, Bali, West Timor, Sulawesi and the Maluku Islands. H. microconos has

also been found in regions adjacent to Bali, including Komodo (East Nusa Tenggara Province),

0

1000

2000

3000

4000

EU28 RoW


38 Wakatobi (South Sulawesi), Derewan (East Kalimantan) and Bunaken National Park (North

Sulawesi) (Turak and deVantier, 2011). It was recorded at Giliketapang Island, East Java

(Puspitasari et al., 2013) and in Long island, Jepara, Java (Indarjo et al., 2004).

A number of surveys have recorded the presence of H. microconos in Indonesia:

• In nine different areas visited during the Snellius-II Expedition in 1984, H. microconos

was found at seven: Tukang Besi, Sumba, north-east Komodo, Sumbawa, Taka Bone Rate,

Salayer, south-west Sulawesi (Best et al., 1989).


2001, a total of 45 sites were surveyed for corals and H. microconos was found at 30

(McKenna et al., 2002); in 2002, a total of 51 sites were surveyed for corals and

H. microconos was found at 29 (Donnelly et al., 2003).

• H. microconos was found in the waters of Padang, West Sumatra, based on the collection

of Bung Hatta University (Jonker and Johan, 1999).


Sulawesi in 1998 (Allen and McKenna, 2001), a total of 47 sites were visited and

H. microconos was found at 11.

• During a survey of the reefs of the Pulisan region, north-east Sulawesi, H. microconos was

found in 18 of 21 sites (Scaps et al., 2007).

• The species was found in four of five stations at Marabatuan Island and Matasirih Island,

South Kalimantan (Munasik and Siringoringo, 2011).

• H. microconos was observed in Jakarta Bay in 1920 and 2005 and in the offshore Thousand

Islands archipelago in 2005 (van der Meij et al., 2010).

• During a study in 2007 in five locations at Nusalaut Island, Central Maluku District, H. microconos was found at two (Souhoka, 2009).

The species was not encountered by Giyanto (2012) during surveys in 2012 in the waters of

Ternate, Tidore and the surrounding areas.

• It was considered to have a widespread local distribution in Bunaken National Park in

North Sulawesi, occurring in 46% of the 39 sites surveyed in 2003 (Turak and DeVantier,

2003). The authors considered these to be locally-reproductive populations (Turak and

DeVantier, 2003).

In 1992, it was considered to be a dominant species on the lower slopes of the reefs at Sanur and

Nusa Dua, Bali at depths of 5-7 m (van Woesik, 1997 in: Hopley & Suharsono, 2000). Raymakers

(2001) later categorised H. microconos as threatened to a lesser extent (of those reviewed by that

author) with a low estimated abundance – 20-50 colonies/100 m2 - and a high export quota.

However, the Scientific Authority of Indonesia (2014) suggested that the quota for this species is

quite small relative to its abundance in the wild. The Scientific Authority of Indonesia (2014)

reported that only the smaller specimens (<15 cm in diameter) that are brightly coloured (yellow,

bright orange or green) were collected.

Six species in the genus Hydnophora are reported to occur in Indonesia (Scientific Authority of

Indonesia, 2014; Species+, 2015). However, much of the information in the scientific literature

refers to the genus and does not provide information on which species is being referred to (e.g.

Bruckner and Borneman 2006; Chou et al 2010; Guest et al; Gunawan et al., 2006; Hoeksema &

Putra, 2000; Jompa et al.; Lilley, 2001; Putra et al., 2014; Raymakers, 2001; Scaps & Runtukahu,

2008; and Wilson et al., 2012).

39 SCLERACTINIA: Mussidae

Blastomussa wellsi II/B


Scleractinia. Exports of Blastomussa wellsi reported by Indonesia have typically been between

3000-4000 live wild pieces each year and generally within quota (Table 24).

The quota for wild-sourced B. wellsi has decreased slightly from 3800 wild pieces in 2004 to 3500

in 2014. However, the quotas established for 2012 and 2013, appear to have been exceeded

according to trade reported by Indonesia (Table 24). The total reported export of 4354 live wild

pieces in 2013 was higher than exports in any of the previous nine years, and appear to exceed the

quota of for that year by approximately 850 pieces. However, Indonesia’s annual report to CITES

may be based on permits issued rather than actual trade, and therefore actual trade levels may be

less than the volumes reported.

Indonesia established a quota of 2400 pieces of B. wellsi from mariculture in 2005 and a zero


then, although low level trade in mariculture specimens has been reported in several years (Table

25).

RANGE STATES: Australia, Egypt, Fiji, Indonesia, Israel, Japan, Malaysia, New Caledonia, Papua New Guinea, Philippines, Solomon Islands, Tonga, Vanuatu, Viet Nam


EU DECISIONS: Current negative opinion for wild-sourced specimens from Indonesia (except maricultured specimens) formed on 08/12/2014. Previous Article 4.6(b) suspension for Blastomussa spp. from Indonesia applied on 18/02/2005 and most recently confirmed on 04/09/2014. Previous negative opinion for the species Blastomussa wellsi from Indonesia formed on 30/01/2003.

Current positive opinion for wild-sourced specimens from Australia formed on 14/09/2007 and confirmed on 20/06/2011. Positive opinion for Blastomussa spp. from Australia formed on 07/11/2014.

Current no opinion i) for Blastomussa spp. from Fiji formed on 03/09/2014. Previous negative opinion for Blastomussa wellsi formed on 22/05/2003, formalised as an Article 4.6(b) suspension on 03/09/2008 and replaced by a no opinion on 15/09/2008.

Previous negative opinion wild-sourced specimens from Tonga formed on 22/04/2005 and removed on 12/06/2006.

IUCN: NT

40 Table 24: CITES export quotas for wild-sourced Blastomussa wellsi from Indonesia and global direct exports, as reported by the countries of import and Indonesia 2004-2013. Importer reported trade data for 2013 may be incomplete; trade data for 2014 are not yet available.

2004 2005 2006 2007 2008 2009 2010 2011 2012 2013 2014

Quota 3800 3800 3750 3750 3150 3500 3500 3500 3500 3500 3500

Exporter 3555 3584 3622 3733 3145 3424 3490 3300 3650 4354

Importer 2489 3260 3366 3367 2987 2846 2747 2625 2776 3017


Very low level imports of wild specimens into the EU have been reported 2008-2013 by both

Indonesia and EU countries (Table 25, Figure 8) despite the trade being suspension in place. Low

levels of source ‘I’ trade were reported by importers during this period (138 specimens). In

addition, small quantities of wild sourced trade for non-commercial purposes, wild sourced trade

reported by weight and trade in corals of unknown source were also reported 2004-2013.

Blastomussa was the ninth most confiscated coral genus in the UK during the period 2000-2007

(Jones, 2008).

Table 25: Main direct commercial exports of Blastomussa wellsi from Indonesia to the EU-28 (EU) and the rest of the world (RoW), 2004-2013. (Source ‘mariculture’ includes trade recorded as source ‘F’ and ‘C’).



Importer 13 2 4 2 2


Importer 5 4 6 27

W Exporter 3497 3520 3604 3721 3128 3376 3461 3291 3610 4331

Importer 2476 3256 3364 3367 2983 2846 2747 2625 2774 3015


Importer 198 14 9 43 216 192 194 225 181 77


Indirect exports of B. wellsi originating in Indonesia to the EU-28 comprised very low levels of live

wild corals re-exported for commercial purposes, the majority via Israel (Table 26).

Table 26: Indirect exports of live Blastomussa wellsi originating in Indonesia to the EU-28, 2004-2013. All trade was wild sourced for commercial purposes. 2004 2005 2006 2007 2008 2009 2010 2011 2012 2013

Exporter 3

Importer 50


41

Figure 8: Direct imports of wild-sourced (includes source U and unspecified) raw and live Blastomussa wellsi from Indonesia to the EU-28 and the rest of the world (RoW), 2004-2013 for commercial purposes (purpose T and unspecified), as reported by the importers.

Conservation status Blastomussa wellsi was considered to be widespread and is found at depths up to 40 m, and lives

on reef slopes protected from wave action and turbid environments (Turak et al., 2008c). The age

at maturity was assumed to be three to eight years, based on most reef-building corals having

been reported to reach sexual maturity at that age (Wallace, 1999).

The species was categorised as Near Threatened by the IUCN in 2008 (Turak et al., 2008c).

Specific population trends are unknown, and therefore the decline in coral reef habitat, with an

estimated 18% reefs already destroyed, has been used as a proxy for population decline of this

species (Turak et al., 2008c).

The species was described as uncommon by Turak et al. (2008c) and Veron (2000).

Turak et al. (2008c) considered the most important known threat for corals to be extensive

reduction of coral reef habitat due to a combination of threats, but also referred to the harvest of

the aquarium trade within the threats to this species.

Blastomussa are slow growing, with little known about their life histories and characteristics and

were therefore considered difficult to propagate (Wabnitz et al., 2003).

Indonesia: The Scientific Authority of Indonesia (2014) stated that B. wellsi was found

throughout Indonesian waters while Suharsono (2008a) stated that it is scattered throughout the

waters of Indonesia, usually in deep waters. Its preferred habitat are mid-shore reefs in low light

in a protected environment at a depth of more than 20 meters with a sandy, dead coral or muddy

bottom (Scientific Authority of Indonesia, 2014). The species was recorded at the Spermonde

Reefs at depths of 15 metres (Lilley, 2001; Raymakers 2001).

A number of surveys have recorded the presence of B. wellsi in Indonesia:


2001, a total of 45 sites were surveyed for corals and B. wellsi was found at one (McKenna

et al., 2002); in 2002, a total of 51 sites were surveyed for corals and B. wellsi was not

found at any (Donnelly et al., 2003).

• The species was not found in Bali and adjacent regions during two surveys (Hoeksema and Putra, 2000; Turak and deVantier, 2011).

0

1000

2000

3000

4000

EU28 RoW


42 • During a survey of the reefs of the Pulisan region, north-east Sulawesi, B. wellsi was found

in two of 21 sites (Scaps et al., 2007).

Lilley (2001) noted that, while the species is considered to be uncommon, in places where they are

found, they can be abundant. Blastomussa was considered to be a rare genus in the vicinity of

Kapoposang Island (Spermonde) during a study in 1996 (Yusuf and Rani, 2006, in: Yusuf and

Jompa, 2012).

The Scientific Authority of Indonesia (2014) stated that B. wellsi was relatively uncommon and

Suharsono (2008a) suggested that it is rarely found in Indonesia. Bruckner and Borneman (2006)

undertook a survey of 12 locations in the Spermonde Archipelago in Southwest Sulawesi, an area

with approximately 150 islands which they reported was the largest coral collection area in

Indonesia. The authors reported that “B. wellsi was found at the base of one outer reef (20-25 m

depth) in one transect at a density of 1.2 colonies/m2, and in other transects at densities of < 0.2

colonies/m2 population” (Bruckner and Borneman, 2006). The survey gave an overal density of

B. wellsi in an area of 160 km2 in the Spermonde Archipelago of 0-0.05/m2, with a population

estimate of 8,000 (Bruckner and Borneman, 2006). Raymakers (2001) noted that the species

occurs in Spermonde at low densities of 5 colonies/100 m2.

The authors estimated that at Spermonde Archipelago, 100% of colonies were within the legal size

range as established by Indonesia, with the annual harvest quota representing 30% of the

population (Bruckner and Borneman, 2006). While two species of Blastomussa occur in

Indonesia, Bruckner and Borneman (2006) noted that government authorities have only

established a quota for one species at a time. They explained that “in 1999, a quota of 9,000 was

established for B. wellsi, which was reduced to 8,000 in 2000 and set at 0 in 2001. In 2001 B. wellsi

was replaced with B. merleti at a quota of 2500”. Lilley (2001) noted that B. wellsi had already been

collected from Lampung Bay for at least ten years prior to the study. At this location, it lives in

turbid waters at a depth of 27 m, near the Maitem Islands. Lilley (2001) observed one collector

who brought 15 colonies of B. wellsi to the surface, during 30 minutes of searching. Market size

was reported to be 4-6 cm by Raymakers (2001).

43 SCLERACTINIA: Mussidae

Scolymia vitiensis II/B


Scleractinia. Exports of S. vitiensis reported by Indonesia have been approximately 4000-5000 live

wild specimens annually between 2004 and 2013 (Table 27).

The quota during this period has been 4500 live wild pieces each year, 2004-2014 with an

additional zero quota for specimens from mariculture in 2007. However, the 2012 and 2013 quotas

for wild specimens were exceeded according to trade reported by Indonesia. Indonesia reported

total exports of 5762 live wild pieces in 2013, which was higher than exports in any of the previous

nine years, and exceeded the quota of 4500 pieces for that year by over 1000 pieces. However,

Indonesia’s annual report to CITES may be based on permits issued rather than actual trade, and

therefore actual trade levels may be less than the volumes reported.

SYNONYMS: Lithophyllia vitiensis, Parascolymia vitiensis

COMMON NAMES: Doughnut Coral

RANGE STATES: Australia, British Indian Ocean Territory (United Kingdom), Cook Islands, Djibouti, Fiji, Indonesia, Japan, Madagascar, Malaysia, Maldives, Mauritius, New Caledonia, Papua New Guinea, Philippines, Pitcairn Islands (United Kingdom) (uncertain), Réunion, Saudi Arabia, Solomon Islands, South Africa (uncertain), Taiwan, Province of China, Tonga, Vanuatu, Viet Nam


EU DECISIONS: Current negative opinion for wild-sourced specimens from Indonesia (except maricultured specimens) formed on 08/12/2014. Previous Article 4.6(b) suspension applied on 10/05/2006 and last confirmed on 04/09/2014. Previous negative opinion formed on 22/05/2003.

Current Article 4.6(b) suspension for wild-sourced Scolymia spp. from Tonga applied on 28/05/2015. Previous Article 4.6(b) suspension for wild-sourced Scolymia vitiensis applied on 03/09/2008 and most recently confirmed on 04/09/2014. Previous negative opinion for wild-sourced Scolymia vitiensis formed on 24/04/2005.

Current no opinion i) for wild-sourced Scolymia spp. from Fiji formed on 07/11/2014. Previous negative opinion for wild-sourced Scolymia vitiensis formed on 22/05/2003 and removed on 15/01/2004.

IUCN: NT

44 Table 27: CITES export quotas for wild-sourced Scolymia vitiensis from Indonesia and global direct exports, as reported by the countries of import and Indonesia 2004-2013. Importer reported trade data for 2013 may be incomplete; trade data for 2014 are not yet available.

2004 2005 2006 2007 2008 2009 2010 2011 2012 2013 2014

Quota (wild) 4500 4500 4500 4500 4500 4500 4500 4500 4500 4500 4500

Exporter 3997 4098 4380 4455 4049 4438 4453 4234 4693 5762

Importer 2557 3238 2511 2668 2863 2598 2039 2483 2929 2933


Very low level imports of wild specimens into the EU have been reported 2008-2013 by Indonesia

and to a lesser extent EU countries, despite the trade being suspension in place (Table 28, Figure

9). Very low levels of source ‘I’ trade were reported during this period (35 specimens). In addition,

very small quantities of wild sourced live corals for breeding purposes and wild sourced raw corals

for commercial purposes were also reported during this period.

Table 28: Main direct commercial exports of Scolymia vitiensis from Indonesia to the EU-28 (EU) and the rest of the world (RoW), 2004-2013. (Source ‘mariculture’ includes trade recorded as source ‘F’ and ‘C’). All trade for commercial purposes.



Importer 14

6

4


105

Importer

W Exporter 3913 4080 4343 4432 4013 4397 4425 4191 4669 5697

Importer 2543 3228 2505 2668 2859 2598 2039 2483 2929 2933


Importer

4

1

W Exporter

Importer 264 23 4 68 248 953 437 356 345 228


Indirect exports of S. vitiensis originating in Indonesia to the EU-28 comprised very low levels of live wild corals re-exported for commercial purposes in 2007 via Singapore (Table 29).

Table 29: Indirect exports of live Scolymia vitiensis originating in Indonesia to the EU-28, 2004-2013. All trade was wild sourced for commercial purposes. 2004 2005 2006 2007 2008 2009 2010 2011 2012 2013

Exporter 10

Importer 4


45

Figure 9: Direct imports of wild-sourced (includes source U and unspecified) raw and live Scolymia vitiensis from Indonesia to the EU-28 and the rest of the world (RoW), 2004-2013 for commercial purposes (purpose T and unspecified), as reported by the importers.

Conservation status Scolymia vitiensis was considered to be a widespread species, found in deep waters up to 50 m

(Turak et al., 2008a). Scolymia vitiensis were reported to be partly reef-building corals but are

mostly found at the bottom of reef slopes (Scientific Authority of Indonesia, 2014). Veron (2000)

noted that there is a wide latitudinal variation in this species, with subtropical forms usually

solitary, flat and less than 60 mm in diameter, whereas tropical forms are larger and sometimes

colonial. The age at maturity was assumed to be three to eight years, based on most reef-building

corals having been reported to reach sexual maturity at that age (Wallace, 1999).

The species was categorised as Near Threatened by the IUCN (Turak et al., 2008a). Specific

population trends are unknown, and therefore the decline in coral reef habitat, with about 21%

reefs already destroyed, has been used as a proxy for population decline of this species (Turak et

al., 2008a).

It was described as rare throughout its range (Turak et al., 2008a), usually uncommon, and rare in

the south-west Indian Ocean (Veron, 2000; Turak et al., 2008a).

The main known threat for this species was reported to be extensive reduction of coral reef

habitat due to a combination of threats, however, this species was also noted to be harvested for

the aquarium trade (Turak et al., 2008a). Scolymia vitiensis was thought to be more resilient to

some of the threats faced by corals (Wilkinson 2004 in Turak et al., 2008a). In a study of the

impact of the 2010 coral bleaching event in Wakatobi National Park, Wilson et al. (2012) classified

the genus Scolymia as of “intermediate” susceptibility to bleaching events.

Scolymia is a slow growing genus that is difficult to propagate, so there has been limited success

in mariculture (Wood et al., 2012).

Indonesia: The Scientific Authority of Indonesia (2014) reported that the species occurred

throughout Indonesia in sheltered areas and in the deeper water at the bottom of reef slopes.

Similarly, Suharsono (2008a) reported that the species was found scattered throughout Indonesia,

usually found in sheltered spots. The distribution map provided in Suharsono (2008a) indicated

that S. vitiensis is relatively widely distributed in Indonesia.

Lilley (2001) reported the occurrence of the species at Komodo and Rinca, Karimunjawa, Subawa,

Selayar and Spermonde (Lilley, 2001). S. vitiensis has been found in Bali and adjacent regions,

0

1000

2000

3000

4000

EU28 RoW


46 including Wakatobi (South Sulawesi) and Derewan (East Kalimantan) (Turak and deVantier,

2011).

A number of surveys have recorded the presence of S. vitiensis in Indonesia:

• During a Marine Rapid Assessment Program at the Togean and Banggai Islands in Sulawesi in 1998 (Allen and McKenna, 2001), Scolymia vitiensis was found at 16 out of 47 sites surveyed. Describing S. vitiensis as “wide-ranging”, the authors noted that it was found in low numbers at 16 sites in the Togeans, but was absent in the Banggai Group (Allen and McKenna, 2001).

• In nine different areas visited during the Snellius-II Expedition in 1984 (Best et al., 1989), S. vitiensis was found at four: Northeast Komodo, Sumbawa, Salayer and SouthWest Sulawesi.

• During rapid ecological assessments at Raja Ampat Islands, Papua, Eastern Indonesia in 2001, a total of 45 sites were surveyed for corals and S. vitiensis was found at one (McKenna et al., 2002); in 2002, a total of 51 sites were surveyed for corals and S. vitiensis was found at three (Donnelly et al., 2003).

• During a survey of the reefs of the Pulisan region, north-east Sulawesi, S. vitiensis was found in 3 of 21 sites (Scaps et al., 2007).

The Scientific Authority of Indonesia (2014) described the species as relatively common. No

further information on the status of the species in Indonesia was identified.

47 SCLERACTINIA: PECTINIIDAE

Mycedium elephantotus II/B

Trade patterns Indonesia published a CITES export quota of 2500 live, wild-taken Mycedium elephantotus for

2014 retrospectively in 2015, as it had been missed from the quota list in 2014. Indonesia had not

published export quotas for this species previously. Annual reports for 2014 are not required to be

submitted until 31 October 2015, so quota compliance cannot be assessed. Direct exports of

M. elephantotus from Indonesia to the EU-28 and the rest of the world 2004-2013, comprised very

low levels of trade consisting of live corals exported for commercial purposes, of mainly captive-

born origin (Table 30). No trade in M. elephantotus from Indonesia was reported before 2011. No

indirect exports of M. elephantotus to the EU-28 originating in Indonesia were reported 2004-

2013.

Table 30: Main direct exports of Mycedium elephantotus from Indonesia to the EU-28 (EU) and the rest of the world (RoW), 2004-2013. All reported trade was in live corals and for commercial purposes.

Importer Source Reported by 2004 2005 2006 2007 2008 2009 2010 2011 2012 2013

EU F Importer 110 30

Exporter 5

W Importer 5

Exporter

RoW F Importer

Exporter 90

W Importer 20 20

Exporter


SYNONYMS: Madrepora elephantotus, Mycedium tenuicostatum, Mycedium tubifex, Phyllastraea tubifex

RANGE STATES: American Samoa, Australia, British Indian Ocean Territory (United Kingdom), Cocos (Keeling) Islands, Cook Islands, Djibouti, Egypt, Fiji, French Polynesia, India, Indonesia, Israel, Japan, Jordan, Kenya, Kiribati, Madagascar, Malaysia, Maldives, Mauritius, Mozambique, Myanmar, New Caledonia, Palau, Papua New Guinea, Philippines, Réunion, Samoa, Saudi Arabia, Seychelles, Singapore, Solomon Islands, Sudan, Taiwan, Province of China, Thailand, Tonga, United Republic of Tanzania, Vanuatu, Viet Nam


EU DECISIONS: No current or historical opinions or suspensions.

IUCN: Least Concern

48 Conservation status M. elephantotus is a zooxanthellate coral with laminar or encrusting colonies (Veron, 2000).

Veron (2000) noted that it could be found in most reef environments that were protected from

strong wave action. It was reported to be tolerant of shaded conditions (Dinesen, 1983) and

sedimentation, occurring in shallow water in turbid conditions (Dikou and van Woesik, 2006).

The species was regarded as a habitat/ecological generalist in Australian waters (Roelofs and

Silcock, 2008). M. elephantotus was reported to be found to at least 40 m depth (Sheppard et al.,

2014) and to be commonly found from 12-15 m, rarely at 3-11 m, in the South China Sea and Gulf of

Siam (Titlyanov and Titlyanova, 2002).

M. elephantotus was reported to be a hermaphroditic broadcast spawner with an annual

reproductive cycle (Dai et al., 2000). Age at maturity was assumed to be three to eight years based

on most reef-building corals having been reported to reach sexual maturity at that age (Wallace,

1999).

M. elephantotus was reported to be widespread in the Indo-Pacific (Veron, 2000; Roelofs and

Silcock, 2008). Sheppard et al. (2014) reported its range to extend from the Red Sea to the central

Pacific. Veron (2000) and Sheppard et al. (2014) reported M. elephantotus to be common. The

species was categorised by the IUCN as Least Concern and, although species specific information

on population was not available and the population trend was unknown, a population reduction

of 20% over three generations was inferred from estimated habitat loss within its range (Sheppard

et al., 2014). Re-assessment in 10 years was considered important due to predicted threats from

climate change and ocean acidification (Sheppard et al., 2014).

The species was reported to be targeted for the aquarium trade (Sheppard et al., 2014). However,

the main threat to corals was reported to be global climate change, in particular, temperature

extremes leading to bleaching and increased susceptibility to disease, increased severity of El

Niño Southern Oscillation events, storms and ocean acidification (Sheppard et al., 2014). Reported

anthropogenic threats to corals include fisheries (including chemical and dynamite fishing),

human development, invasive species, pollution and sedimentation, although the severity of these

combined threats for individual species were not known (Sheppard et al., 2014). White Plague-like

disease was also reported in M. elephantotus (Sutherland et al., 2004). The species was reported to

have moderate susceptibility to bleaching (Roelofs and Silcock, 2008).

Indonesia: Suharsono (2008a) reported M. elephantotus to be spread throughout Indonesian

waters and mapped records from 14 provinces: Aceh, West Sumatra, Bengkulu, Riau, Bangka-

Belitung, Banten, Central Java, West Nusa Tenggara, East Nusa Tenggara, South Sulawesi,

Southeast Sulawesi, Central Sulawesi, Maluku and Papua. In addition it was reported from Bali

and East Kalimantan (Turak and DeVantier, 2011) and North Sulawesi (Turak and DeVantier,

2003).

A number of surveys have recorded the presence of M. elephantotus in these provinces.

• In nine areas surveyed by the Snellius-II expedition in 1984 and the Buginesia project

(1980), M. elephantotus was recorded from seven sites: Tukang Besi Islands (Southeast

Sulawesi), Sumba and Komodo (East Nusa Tenggara), Subawa (West Nusa Tenggara),

Taka Bone Rate, Salayer and Spermonde (South Sulawesi) (Best et al., 1989).

• In other sites surveyed across Sulawesi, it was reported from 23 of 27 sites surveyed at

Wakatobi National Park (Southeast Sulawesi) (Hoeksema, 2003) and from 15 of 47 sites

surveyed around the Banggai and Togean Islands (Central Sulawesi) (Allen and McKenna,

2001).

• Siringoringo and Hadi (2013) also recorded it from six of nine sites surveyed around the

Banggai Islands.

49 The following surveys recorded the presence of M. elephantotus in provinces were harvest is not

permitted:

• Chou et al. (2010) reported M. elephantotus from Bintan Island (Riau) in 1993 and again in

2007.

• A longitudinal study in Jakarta Bay reported the species from around 1920 and again in

2005 (van der Meij et al., 2010).

• Reported from Bunaken National Park (North Sulawesi) in areas of moderate coral cover

(Devantier et al., 2006) and also by (Yap et al., 2013).

• Turak and DeVantier (2003) recorded M. elephantotus from 28 of the 39 sites surveyed in

Bunaken National Park (North Sulawesi).

• Scaps et al. (2007) recorded the species at each of 21 sites surveyed in the Pulisan region

(North Sulawesi).

• Turak and DeVantier (2011) reported it from five exposed locations out of 47 sampling

stations in on the south and west coasts of Bali and the adjacent island of Nusa Penida

(Bali Province).

• Souhoka (2009) reported M. elephantotus from each of five sites investigated around

Nusalaut Island (Maluku).

• M. elephantotus was reported from 24 of 45 sites surveyed at Raja Ampat Islands (Papua

Province) (McKenna et al., 2002). Donnelly et al. (2003) reported it from 41 of 51 sites

surveyed in another survey of the Raja Ampat Islands.

In a study to standardise quantification coral abundance, the genus Mycedium was categorised as

rare from Bakauheni (Lampung), uncommon at Kepalauan Seribu (Jakarta) and Jepara (Central

Java), common at Teluk Cendrawasih (West Papua) but was not recorded at Merak (Banten)

(Suharsono and Giyanto, 2006).

50 SCLERACTINIA: TRACHYPHYLLIIDAE

Trachyphyllia geoffroyi II/B

Taxonomic note CITES recognises Trachyphyllia geoffroyi as an accepted species (UNEP-WCMC, 2012), based on

Veron (2000). T. geoffroyi includes the synonym Wellsophyllia radiata (UNEP-WCMC, 2012). Best

and Hoeksema (1987) placed W. radiata in the genus Trachyphyllia, noting its occurrence in

Indonesia, Singapore and north-west Australia. It was made a synonym of T. geoffroyi by Veron

and Hodgson (1989) who noted that it was primarily characterized by having adjoined, rather

than phaceloid, corallites, which appears to be an ecomorph correlated with soft substrates.

Similarly, Hoeksema (2014) considered W. radiata to be a synonym of T. geoffroyi.

However, the Scientific Authority of Indonesia (2014) and Suharsono (2008) recognise W. radiata

and T. geoffroyi as two separate species on the basis of clear differences in the shape of the walls

of colonies, noting that both taxa occupy the same habitat but they are both highly distinctive.

In this species account, information is provided on T. geoffroyi including the taxon W. radiata.

SYNONYMS: Antillia duncani, Antillia flabelliformis, Antillia geoffroyi, Antillia infundibuliformis, Antillia lonsdaleia, Antillia orientalis, Antillia sinuata, Antillophyllia lonsdaleia, Callogyra formosa, Manicina amarantum, Trachyphyllia amarantum, Trachyphyllia lelandi, Trachyphyllia radiata, Turbinolia geoffroyi, Wellsophyllia geoffroyi, Wellsophyllia radiata

COMMON NAMES: Crater Coral, Folded Coral, Puffed Coral

RANGE STATES: Australia, British Indian Ocean Territory (United Kingdom), Egypt, Fiji, India, Indonesia, Israel, Japan, Jordan, Madagascar, Malaysia, Maldives, Mozambique, Myanmar, New Caledonia, Papua New Guinea, Philippines, Saudi Arabia, Seychelles, Singapore, Solomon Islands, Sudan, Thailand, Tonga, United Republic of Tanzania, Viet Nam


EU DECISIONS: Current negative opinion for wild-sourced specimens from Indonesia (except maricultured specimens) formed on 08/12/2014. Previous Article 4.6(b) suspension (except maricultured specimens) applied on 18/02/2005 and last confirmed on 04/09/2014. Previous negative opinion formed on 16/09/1999, replaced by a positive opinion on 15/05/2002 and again with a negative opinion on 22/05/2003.

Current Article 4.6(b) suspension for wild-sourced specimens from Fiji applied on 03/09/2008 and last confirmed on 28/05/2015. Previous negative opinion formed on 22/05/2003 and confirmed on 25/10/2005.

Current positive opinion for wild-sourced specimen from Australia formed on 20/06/2011.

Previous negative opinion for wild-sourced specimens from Tonga formed on 22/04/2005 and removed on 12/06/2006.

IUCN: Near Threatened

51 Trade patterns Trachyphyllia geoffroyi was listed in CITES Appendix II on 18/01/1990 through the listing of the

order Scleractinia. As Indonesia considers Wellsophyllia radiata to be an accepted species, it has

reported trade in both T. geoffroyi and W. radiata and has published separate quotas for both taxa

for all years, with the quota for 2014 in prep and the 2015 quotas not yet published.

Exports of T. geoffroyi (including the taxon W. radiata) reported by Indonesia have typically been

between 50,000 and 60,000 live wild pieces each year and generally within quota (Table 31). The

quota for T. geoffroyi has decreased from 52,000 wild pieces in 2004 to 42,000 in 2014, whereas the

quota for W. radiata has remained stable at 10,000 pieces. However, the total reported exports of

65,069 live wild pieces in 2013 were higher than exports in any of the previous nine years, and

appear to have exceeded the combined quota (T. geoffroyi and W. radiata) of 52,000 pieces for

that year by approximately 13,000 pieces (Table 31).

Table 31: CITES export quotas for wild-sourced Trachyphyllia geoffroyi and Wellsophyllia radiata from Indonesia and global direct exports, as reported by the countries of import and Indonesia 2004-2013. Importer reported trade data for 2013 may be incomplete; trade data for 2014 are not yet available.

Quota 2004 2005 2006 2007 2008 2009 2010 2011 2012 2013 2014

Trachyphyllia geoffroyi (wild) 52000 51000 51000 51000 45000 48500 50000 47500 43500 42000 42,000

Wellsophyllia radiata (wild) 10000 10000 10000 10000 9000 9000 9000 9000 10000 10000 In prep.

Exporter1 50838 56459 57864 60798 53928 56903 58529 53049 45299 65069

Importer1 45838 53407 48160 48346 40222 38525 46134 36602 37831 35188


1 includes trade reported as Trachyphyllia geoffroyi and as Wellsophyllia radiata

Breaking this down further, it is apparent that the 2013 quota established by Indonesia for

T. geoffroyi was 42,000 pieces and Indonesia reported exports of 53,130. The 2013 quota

established for W. radiata was 10,000 pieces with trade reported by Indonesia amounting to 11,939

pieces. However, Indonesia’s annual report to CITES may be based on permits issued rather than

actual trade, and therefore actual trade levels may be less than the volumes reported.

Indonesia established a quota of 1,000 pieces of T. geoffroyi from mariculture in 2005 and a zero

quota for mariculture specimens of T. geoffroyi and W. radiata in 2007. It has not established a

quota for mariculture since then, although low level trade in mariculture specimens has been

reported (Table 32).


and EU countries, despite the trade suspension in place (Table 32). Low levels of trade in source ‘I’

were reported by importers during this period (465 specimens). Very low levels of wild sourced

trade for non-commercial purposes and commercial trade in sources O and U were also reported

during this period. Additionally, very low levels of wild sourced commercial trade in carvings and

live corals reported by weight were reported.

52 Table 32: Main direct commercial exports of Trachyphyllia geoffroyi from Indonesia to the EU-28 (EU) and the rest of the world (RoW), 2004-2013. (Source ‘mariculture’ includes trade recorded as source ‘F’ and ‘C’).



Importer 156 40 51 36 48 60 18 15 30 19


Importer 100 15 10 17 40 61 28 78

W Exporter 50452 56236 57342 60336 53451 56130 57591 52685 45063 64619

Importer 45682 53302 48109 48310 40174 38465 46116 36587 37801 35169


Importer 2 20 7

W Exporter

Importer 3805 176 126 458 6189 6947 5923 5895 4677 3084


Figure 9: Direct imports of wild-sourced (includes source U and unspecified) raw and live Trachyphyllia geoffroyi from Indonesia to the EU-28 and the rest of the world (RoW), 2004-2013 for commercial purposes (purpose T and unspecified), as reported by the importers. Indirect exports of T. geoffroyi originating in Indonesia to the EU-28 comprised very low levels of live wild corals re-exported for commercial purposes, primarily via Singapore (Table 33).

Table 33: Indirect exports of live Trachyphyllia geoffroyi originating in Indonesia to the EU-28, 2004-2013. All trade was wild sourced for commercial purposes. 2004 2005 2006 2007 2008 2009 2010 2011 2012 2013

Exporter 15 33 50 5 4

Importer 15 15


CITES trade should be reported using the accepted CITES nomenclature, however, of 13,771

individual shipment records for 2010-2013, 11,740 were reported using the name T. geoffroyi with

the remainder, 2,030 (15%), reported under the name the W. radiata. While trade to the EU was

low level, about half of shipments imported were accepted using the name W. radiata.

0

10000

20000

30000

40000

50000

60000

EU28 RoW


53 The Scientific Authority of Indonesia (2014) noted that the misidentification of, and use of

synonyms for, corals such as Wellsophyllia and Trachyphyllia could lead to inconsistencies in

trade data. Lilley (2001) stated that T. geoffroyi and W. radiata are considered to represent two

separate species by the traders. Similarly Raymakers (2001) noted that during interviews,

collectors and traders stated that the two species can be identified without a doubt.

Jones (2008) reported that Trachyphyllia was the top confiscated coral genus in the UK during the

period 2000-2007.

Conservation status Trachyphyllia geoffroyi is the only species in the genus Trachyphyllia (Veron, 2000). It occurs in

inter-reef environments and on soft substrates around continental islands (Veron, 2000). It is rare

on reefs, common around continental islands and some inter-reef areas (Veron, 2000). The

species is typically found as solitary unattached colonies but occasionally forms massive colonies

(Sheppard et al. 2008). The age at maturity was assumed to be three to eight years, based on most

reef-building corals having been reported to reach sexual maturity at that age (Wallace, 1999).

The species was categorised as Near Threatened by the IUCN in 2008 (Sheppard et al. 2008).

Specific population trends are unknown and the estimated habitat loss of 22% from reefs already

destroyed within its range was considered to be the best inference of population reduction

(Sheppard et al. 2008). Sheppard et al. (2008) suggested that “it is very widespread, and although

uncommon within its range, it can be found in deeper waters and off-reef areas, and therefore is

likely to be more resilient to habitat loss and reef degradation because of an assumed large

effective population size that is highly connected and/or stable with enhanced genetic variability”.

Habitat loss is the main threat to the species, however, it is also highly susceptible to harvesting

for the aquarium trade (Sheppard et al. 2008).

It was considered to be a slow growing species and difficult to propagate and limited success in

mariculture has been reported (Wabnitz et al., 2003; Wood et al., 2012).

Indonesia: T. geoffroyi was reported to have a wide distribution and is found throughout

Indonesian waters (Suharsono, 2008a; Scientific Authority of Indonesia, 2014). The species was

reported to be found from shallow waters to 30 meters depth (Scientific Authority of Indonesia,

2014; Suharsono, 2008a).

The species has been recorded from Lampung Bay, Komodo and Rinca Islands, Pulau Pari (Jakarta

Bay), the Inner bay of Ambon (Mollucas), Lombok and Sumbawa Islands (Nusa Tenggara), and

Spermonde reef (South Sulawesi) (Lilley, 2001). In the Spermonde Archipelago, T. geoffroyi was

found to be primarily free-living, occurring in shallow, nearshore (0-3 m depth) and deeper

offshore (algal flats at 25-50 m depth) soft bottom habitats (Bruckner and Borneman, 2006). The

genus Trachyphyllia has been recorded in the following collection sites: Banyuwangi (Bali Strait),

West Bali (Bali Strait), Binuangeun (west Java), Gilmanuk, Jepara Central Java (Java Sea), Sibolga,

North Sumatra (Indian Ocean) (Lilley, 2001).

The Scientific Authority of Indonesia (2014) recognises two separate species (T. geoffroyi and

W. radiata) and stated that W. radiata occupied the same habitat as Trachyphyllia, and was

widespread throughout Indonesian waters. However, Suharsono (2008a) indicated that

W. radiata was scattered throughout Indonesian waters but that is was not common and usually

living on sandy substrates in quiet waters.

A number of surveys have recorded the presence of T. geoffroyi in Indonesia:

54 • In nine different areas visited during the Snellius-II Expedition in 1984 (Best et al., 1989),

T. geoffroyi was found at three: North East Komodo, Sumbawa and South West Sulawesi.

• During a Marine Rapid Assessment Program at the Togean and Banggai Islands in Sulawesi in 1998, a total of 47 sites were visited and T. geoffroyi was found at two (Allen and McKenna, 2001).

• Bruckner and Borneman (2006) undertook a survey of 12 locations in the Spermonde Archipelago in South West Sulawesi, an area with approximately 150 islands which they reported was the largest coral collection area in Indonesia. Their observations of T. geoffroyi included isolated attached colonies with growth forms that have previously been identified as Wellsophyllia radiata (Bruckner and Borneman, 2006).

• The species was recorded in Pulau dua kecil, Luwuk Pensinsula, Sulawesi (Scaps and Runtukahu, 2008).

• During rapid ecological assessments at Raja Ampat Islands, Papua, Eastern Indonesia in 2001, a total of 45 sites were surveyed for corals and T. geoffroyi was found at two (McKenna et al., 2002); in 2002 a total of 51 sites were surveyed for corals and T. geoffroyi was found at one (Donnelly et al., 2003).

• The species was found in Bali and adjacent regions, including Komodo (East Nusa Tenggara Province), Wakatobi (South Sulawesi), Derewan (East Kalimantan) and Bunaken National Park (North Sulawesi) (Turak and deVantier, 2011); a survey of four sites in Bali confirmed the genus at one site (Hoeksema and Putra, 2000).

• In Bunaken National Park in North Sulawesi it was considered to have a locally restricted distribution, occurring in 5% of the 39 sites surveyed (Turak and DeVantier, 2003).

The Scientific Authority of Indonesia (2014) stated that the species was very common in sheltered

areas such as around continental islands and in inter-reef areas. The Scientific Authority of

Indonesia (2014) considered the species to be abundant, with small and large colonies usually

found together and colonies numbering in the hundreds to thousands in one area (clumped

distribution). Best et al., (1989) considered the species to be uncommon. Bruckner and Borneman

(2006) referred to Trachyphyllia as “unusual and/or uncommon corals most preferred by

collectors”. During a survey of the reefs of the Pulisan region, north-east Sulawesi, Scaps et al.

(2007) remarked that “Some monospecifc genera that were not observed in our study

(Catalaphyllia, Stylarea, Australomussa, Cynarina, Trachyphyllia) can be considered as rare.”

Trachyphyllia was considered to be rare in the vicinity of Kapoposang Island during a study in

1996 (Yusuf and Rani, 2006, in: Yusuf and Jompa, 2012). In Bunaken National Park in North

Sulawesi, Turak and DeVantier (2003) suggested that species with average rank abundance of < 1.5

may not form locally-reproductive populations. Using a methodology based on size of colony and

frequency of occurrence, Suharsono and Giyanto (2006) described Trachyphyllia as rare in

Kepulauan Seribu, suggesting that harvest should be strictly limited.

Bruckner and Borneman (2006) reported densities of <0.3 colonies/m2 from the Spermonde

Archipelago, and Raymakers (2001) reported densities of 0.1/m2 (10/100m2) and 0.28/m2 (28/100

m2). In Lampung Bay, Lilley (2001) indicated that the estimated population density of T. geoffroyi

was 0.45/m2 (45 colonies per 100 m2) with sizes smaller than 50 cm. Overall Raymakers (2001)

categorised T. geoffroyi as threatened to a lesser extent (of those reviewed by that author) with a

low estimated abundance – 20-50 colonies/100 m2 (based on densities in Spermonde, Sumatra)

and Lampong, Sulawesi) and a high export quota.

Bruckner and Borneman (2006) estimated that the quota for this species represented only 1.9% of

the total population in Spermonde. They found that collectors preferentially targeted colourful

red and green morphs, which may be more vulnerable to overcollection. Lilley (2001) noted that

T. geoffroyi has been collected for at least 15 years in Lampung Bay, and that the red-coloured

specimens were most sought-after, fetching a higher price than specimens of other colours. The

Scientific Authority of Indonesia (2014) also noted that fishermen only collect the bright and

colourful corals but not the dark brown and pale corals.

55 Bruckner and Borneman (2006) suggested that localized declines in Trachyphyllia may occur as a

result of collection pressures, but a few individuals of a species will probably remain in other

habitats because they are not the preferred colour morph, shape, or size, or because they have

experienced partial mortality and are not desirable targets.

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61 Appendix Table 1: Purpose of trade

Code Description

T Commercial

Z Zoo

G Botanical garden

Q Circus or travelling exhibition

S Scientific

H Hunting trophy

P Personal

M Medical (including biomedical research)

E Educational

N Reintroduction or introduction into the wild

B Breeding in captivity or artificial propagation

L Law enforcement / judicial / forensic

Table 2: Source of specimens

Code Description

W Specimens taken from the wild

R Ranched specimens: specimens of animals reared in a controlled environment, taken as eggs or juveniles

from the wild, where they would otherwise have had a very low probability of surviving to adulthood

D Appendix-I animals bred in captivity for commercial purposes in operations included in the Secretariat's

Register, in accordance with Resolution Conf. 12.10 (Rev. CoP15), and Appendix-I plants artificially

propagated for commercial purposes, as well as parts and derivatives thereof, exported under the provisions

of Article VII, paragraph 4, of the Convention

A Plants that are artificially propagated in accordance with Resolution Conf. 11.11 (Rev. CoP15), as well as

parts and derivatives thereof, exported under the provisions of Article VII, paragraph 5 (specimens of species

included in Appendix I that have been propagated artificially for non-commercial purposes and specimens of

species included in Appendices II and III)

C Animals bred in captivity in accordance with Resolution Conf. 10.16 (Rev.), as well as parts and derivatives

thereof, exported under the provisions of Article VII, paragraph 5

F Animals born in captivity (F1 or subsequent generations) that do not fulfil the definition of ‘bred in captivity’ in

Resolution Conf. 10.16 (Rev.), as well as parts and derivatives thereof

U Source unknown (must be justified)

I Confiscated or seized specimens (may be used with another code)

O Pre-Convention specimens

Documents

Review of selected corals from Indonesia