Botanical Journal of the Linnean Society, 2018, 186, 435–455. With 3 figures.
A review of the trade in orchids and its implications for
conservation
1
IUCN SSC Orchid Specialist Group, c/o Royal Botanic Gardens, Kew, Richmond TW9 3AB, UK
Department of Zoology, University of Oxford, Radcliffe Observatory Quarter, Woodstock Road, Oxford
OX1 3PS, UK
3
Natural History Museum, University of Oslo, P.O. Box 1172 Blindern, 0318 Oslo, Norway
4
Department of Organismal Biology, Uppsala University, Norbyvägen 18D, 75236 Uppsala, Sweden
5
Conservation Science, Royal Botanic Gardens, Kew, Richmond, Surrey TW7 3AE, UK
6
School of Biological Sciences, 35 Stirling Highway, University of Western Australia, Crawley, Perth, WA
6009, Australia
7
Kadoorie Farm and Botanic Garden, Lam Kam Road, Tai Po, New Territories, Hong Kong
8
Cambridge University Herbarium, The Sainsbury Laboratory, Department of Plant Sciences, Cambridge
University Botanic Gardens, Bateman Street, Cambridge CB2 1LR, UK
9
Sri Lanka Customs, No. 40, Main Street, Colombo 11, Sri Lanka
10
Naturalis Biodiversity Center, Darwinweg 2, 2333 CR Leiden, The Netherlands
11
Leiden University, Rapenburg 70, 2311 EZ Leiden, Netherlands
12
Purwodadi Botanic Garden, Indonesian Institute of Sciences (LIPI), Jalan Raya Surabaya Malang
KM.65, Capang, Purwodadi, Pasuruan, Jawa Timur 67163, Indonesia
13
Durrell Institute of Conservation and Ecology, School of Anthropology and Conservation, Marlowe
Building, University of Kent, Canterbury CT2 7NR, UK
14
School of Geography and the Environment, University of Oxford, South Parks Road, Oxford OX1 3QY,
UK
15
Lancaster Environment Centre, Library Avenue, Lancaster University, Lancaster LA1 4YQ, UK
2
Received 28 June 2017; revised 10 August 2017; accepted for publication 16 October 2017
Orchids are one of the largest plant families and are commercially traded for a variety of purposes, including as
ornamental plants, medicinal products and food. These markets involve thousands of species, which may be traded
legally or illegally, sustainably or unsustainably, and take place at local, national or international scales. In this
review, we provide the first overview of commercial orchid trade globally and highlight the main types that involve
wild-collected plants. Much of this trade is the result of illegal harvest meaning that it is little documented and is
absent from official statistics, at the same time as being of growing conservation concern. We discuss the associated
legal–regulatory context, identify key conservation challenges and highlight four key priorities for addressing these
challenges. These are to (1) research trade dynamics and the impacts of harvest; (2) strengthen the legal trade of
orchids; (3) adopt measures to reduce illegal trade; and (4) raise the profile of orchid trade among policy makers,
conservationists and the public.
ADDITIONAL KEYWORDS: CITES – horticulture – Orchidaceae – over-harvesting – plant trade – wildlife trade.
*Corresponding authors. E-mail: aehinsley@gmail.com and
jacob.phelps@gmail.com
© 2017 The Linnean Society of London, Botanical Journal of the Linnean Society, 2018, 186, 435–455
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AMY HINSLEY1,2*, HUGO J. DE BOER1,3,4, MICHAEL F. FAY1,5,6, STEPHAN W. GALE1,7,
LAUREN M. GARDINER1,5,8, RAJASINGHE S. GUNASEKARA1,9, PANKAJ KUMAR1,7,
SUSANNE MASTERS1,10,11, DESTARIO METUSALA1,12, DAVID L. ROBERTS1,13,
SARINA VELDMAN1,4, SHAN WONG1,14 and JACOB PHELPS1,15*
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A. HINSLEY ET AL.
INTRODUCTION
Table 1. Summary of commercial orchid trade reported to CITES in 1996–2015, including all trade reported by weight
and number of items as reported by importers (exporter-reported trade included in parentheses where this was higher)
Product
Live plants
Roots
Cultures*
Seeds
Dried Plants
Derivatives†
Flowers
Stems
Specimens
Leaves
Artificially propagated trade
Wild trade
Reported in number of items
Reported by weight (kg)
Reported in number
of items
Reported by weight
(kg)
1 119 675 302
4 127 740
1 842 969 (E: 4 937 676)
912 542
730 015
230 138 (E: 7 060 030)
47 842 (E: 70 963)
–
105 (E: 419)
66 (E: 71 650)
16 776 179
762 359
–
– (E: 1)
7 440 721
1 130 050
306 (E: 3000)
31 415 634
–
1180
1 057 251
304 (E: 1178)
1200
–
13 700
418
351 (E: 1095)
–
664
– (E: 5)
576 839
677 842
–
–
157 500 (E: 177 436)
8056
–
– (E: 1665)
–
–
Small amounts of trade reported in unquantifiable units (e.g. boxes, cartons) and potentially misreported terms (e.g. logs, leather products) were
omitted. ‘Wild-sourced’ is defined as trade reported as source W, U and no source; ‘Artificially propagated’ is defined as trade reported under the source
codes for plants (A, D) and captive-bred animals (C, F), the latter to capture low levels of misreported data. Data: CITES trade statistics derived from
the CITES Trade Database, UNEP World Conservation Monitoring Centre, Cambridge, UK, https://trade.cites.org, downloaded March 2017.
*Combined figures for all trade in cultures and trade reported as live plants with the unit ‘flasks’, as a ‘culture’ is likely to refer to a sterile flask
containing multiple seedlings.
†
Combined figures for trade reported as derivatives, extract, medicine and powder.
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Orchids are one of the largest families of flowering
plants (e.g. Chase et al., 2015) and are globally distributed. To date, 29 199 species have been accepted
(Govaerts et al., 2017), with several hundred new
species names published each year (e.g. 370 in 2013;
Schuiteman, 2017), and 31 000 species estimated to
exist in total (Joppa, Roberts & Pimm, 2010). In addition to their geographical and taxonomic diversity,
orchids are also widely used and traded for a variety of reasons, both legally and illegally, sustainably and unsustainably (Fay, 2015, and references
therein). One of the best-known plant groups in
the global horticultural and cut flower trades (De,
2015; FloraHolland, 2015), orchids are also harvested, grown and traded for a variety of purposes,
including as ornamental plants, medicinal products
and food.
Most formal, global orchid trade is in artificially
propagated cut flowers and plants grown under controlled conditions: between 1996 and 2015, most legal,
reported commercial orchid trade reported was from
artificially propagated sources, including 99.9% of >
1.1 billion live orchid plants in trade and > 31 million
kg of stems (UNEP-WCMC, 2017; Table 1). During this
period, Taiwan and Thailand were the largest exporters, with most plants sent to South Korea (40%), the
USA (27%) and Japan (20%) (UNEP-WCMC, 2017).
The reported legal trade in wild-sourced plants was
much lower, peaking at just under 375 000 plants in
1996 (UNEP-WCMC, 2017). However, despite this
well-developed legal trade, orchids are also widely and
illegally harvested from the wild for local, regional and
international trade. There are growing concerns that
trade, although largely unreported, is threatening
wild orchid populations and species in many places
(e.g. Davenport & Ndangalasi, 2003; Flores-Palacios
& Valencia-Diaz, 2007; Subedi et al., 2013; Phelps &
Webb, 2015; Pant et al., 2016). Orchids may be particularly vulnerable to over-harvest because many
species have a limited range and/or occur at low densities due to a variety of interacting factors such as
recent speciation, specialized pollination mechanisms,
habitat specificity and the restricted distribution of
mycorrhizal symbionts (e.g. Dodson & Gentry, 1991;
Swarts & Dixon, 2009; McCormick & Jacquemyn,
2014). The limited ecological studies on the conservation impacts of wild collection of epiphytic orchids
suggest a low tolerance to harvest (Mondragón, 2009;
Hu et al., 2017).
This review provides a first-of-its-kind overview
of the global commercial trade of orchids, focused on
wild plants. Based on literature review and expert
consultation across the IUCN Species Survival
Commission Orchid Specialist Group, in this review
we identify the main types of contemporary commercial trade in orchids globally, provide an overview of
the legal–regulatory context that shapes orchid harvest and trade and discuss the related conservation
challenges.
ORCHID TRADE AND CONSERVATION
TYPES OF COMMERCIAL TRADE
HORTICULTURE
Orchids have long been commercialized as ornamental plants in the horticultural and floricultural trade,
involving several distinct types of markets and consumers. This trade is, unsurprisingly, dominated by
species with attractive flowers, but it also includes species admired for their unusual growth habits (e.g. leafless orchids, such as species of Dendrophylax Rchb.f.
and Chiloschista Lindl.), miniature size (e.g. species
of Platystele Schltr. and Bulbophyllum moniliforme
F.Muell.), scent (e.g. species of Cattleya Lindl. and
Dendrochilum glumaceum Lindl.) and patterned leaves
(e.g. jewel orchids in the genera Anoectochilus Blume,
Goodyera R.Br., Ludisia A.Rich. and Macodes Lindl.).
The vast majority of contemporary orchid trade
involves artificially propagated plants and cut flowers cultivated in commercial greenhouses. Reported
Convention on the International Trade in Endangered
Species of Wild Fauna and Flora (CITES) trade in live
artificially propagated plants is dominated by a small
number of genera, with a large proportion of trade in
hybrids (e.g. Cymbidium Sw., Dendrobium Sw. and
Phalaenopsis Blume; Table 2). Orchids are consistently
ranked among the best sellers in the global potted
plant trade (FloraHolland, 2015; USDA, 2016) and also
comprise c. 10% of all fresh cut flowers traded internationally (De, 2015). This represents an economically
significant global trade, with exports of potted orchids
from the Netherlands alone valued at almost €500 million in 2015 (FloraHolland, 2015). The largest areas of
production are in Thailand, Taiwan, The Netherlands
and Japan, with demand for both potted and cut flowers growing in economic value annually (Griesbach,
2002; Hanks, 2015). There is also considerable domestic
and regional trade in cultivated orchids; Thailand, for
example, sells roughly half of the orchids it produces in
the domestic market (Thammasiri, 2015).
Ornamental horticultural trade also includes wild,
often illegally harvested plants. This can involve smallscale harvest for household use (Hinsley, 2011), but
is also frequently conducted on a commercial scale.
Historically, tropical orchids were collected in the hundreds of thousands for international export to Europe,
dating back to the Victorian orchid fever (Sanders,
2017). For example, Joseph Hooker oversaw the collection of ‘seven men’s loads’ of Vanda coerulea Griff.
ex Lindl. for Kew, although few survived (Allan, 1967:
183). International trade of wild horticultural orchids to
Europe, the USA and Japan was widespread up to the
establishment of CITES in the 1970s (Cribb et al., 2003;
Table 2. Top ten reported orchid taxa commercially traded as artificially propagated live plants in the 10-year periods
1996–2005 and 2006–2015 (as reported by importers), including trade reported at genus and family levels
Rank
1
2
3
4
5
6
7
8
9
10
1996–2005 (total number live plants: 459 857 389)
2006–2015 (total number live plants: 659 817 913)
Reported taxa
Number live plants
(% total)
Reported taxa
Number live plants
(% total)
Orchidaceae species
Orchidaceae hybrids
Dendrobium spp.
Phalaenopsis spp.
Species of Cymbidium Sw.
Species of Oncidium Sw.
Phalaenopsis amabilis
(L.) Blume
Cattleya spp.
Cymbidium kanran Makino
Species of Vanda R.Br.
165 962 470 (36.1)
123 939 767 (27.0)
92 482 163 (20.1)
31 572 618 (6.9)
24 672 878 (5.4)
7 077 873 (1.5)
4 769 951 (1.0)
Orchidaceae hybrids
Cymbidium spp.
Orchidaceae species
Phalaenopsis hybrids
Phalaenopsis spp.
Dendrobium spp.
Cymbidium hybrids
189 447 122 (28.7)
177 536 225 (26.9)
124 907 316 (18.9)
66 683 709 (10.1)
28 954 444 (4.4)
22 692 242 (3.4)
21 813 621 (3.3)
2 375 391 (0.5)
1 478 658 (0.3)
1 130 662 (0.3)
Dendrobium hybrids
Cattleya spp.
Oncidium spp.
15 134 974 (2.3)
2 276 462 (0.4)
1 489 956 (0.2)
Source codes for artificially propagated plants (A, D) and captive-bred animals (C, F) were used, the latter to capture low levels of misreported data.
Data: CITES trade statistics derived from the CITES Trade Database, UNEP World Conservation Monitoring Centre, Cambridge, UK, https://trade.
cites.org, downloaded May 2017.
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Orchids are traded for a wide range of purposes and
at many different scales, from large-scale commercial
trades through to subsistence use (e.g. as medicines,
materials for weaving, ornaments, food, dyes; Lawler,
1984). There are also other, emerging commercial uses
of orchids, such as in perfumes and cosmetic products,
that have been subject to little published research.
Here, we provide an overview of the key types of established commercial trades in orchids globally, focused
on wild-collected plants.
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A. HINSLEY ET AL.
CULTURAL ORNAMENTAL USES
Orchid flowers have historically been and continue to
be traded for their ornamental value in a wide range of
cultural and religious ceremonies. For example, flowers of Dendrobium maccarthiae Thwaites are used
as special temple offerings in Sri Lanka, and flowers
and pseudobulbs of species of Laelia Lindl. are used
in Mexican Day of the Dead ceremonies (Duggal,
1971). Orchid flowers are also used as national symbols, including the national flower of Myanmar,
Bulbophyllum auricomum Lindl., and similar species,
such as B. sukhakulii Seidenf., which are often used to
adorn women’s hair (Goh, 2013).
EDIBLE ORCHIDS
Orchids used for human consumption include globally important products, such as vanilla flavourings
(extracts of Vanilla Plum. ex Mill.), and other edible
products used on national and regional scales.
is the main species used for the food trade, with the
hybrid Vanilla × tahitensis J.W.Moore being the second most cultivated (Lubinsky et al., 2008a, b). Vanilla
seed pods are harvested unripened and processed in
order for the characteristic flavour to develop (Correll,
1953). Madagascar is the biggest producer of Vanilla
with 3719 tonnes being produced in 2014 (comprising
48% of global production), followed by Indonesia with
2000 tonnes (FAOSTAT, 2014).
Salep
Salep is made from the polysaccharide-rich tubers of
wild orchids that are traded predominantly in Turkey
as part of a seasonal trade recorded from as far back as
1850 (Landerer, 1850). Contemporary collection is also
reported in Greece, Iran, Iraq and Albania (Ghorbani
et al., 2014; Kreziou, De Boer & Gravendeel, 2016;
Quave & Pieroni, 2015; A. Ghorbani, H. de Boer, pers.
observ.). After collection, the orchid tubers are boiled
in water, milk or ayran (a yoghurt-based drink) to render the enzymes in them inactive and prevent tubers
from regrowing (Tamer, Karaman & Copur, 2006).
They are then dried and ground into a powder called
salep, which is used to make the drink called salep
and ice cream called maraş dondurma (Kasparek &
Grimm, 1999). Ethnobotanical surveys of plant use in
Turkey report that salep, served in the form of a drink,
is also ascribed medicinal properties (Çömlekçioğlu
& Karaman, 2008; Korkmaz, Fakir & Guller, 2011;
Gürdal & Kültür, 2013).
At least 35 species of orchids are used to make
salep, including species from the genera Anacamptis
Rich., Dactylorhiza Neck. ex Nevski, Himantoglossum
Spreng., Ophrys L., Orchis L., Serapias L. and
Steveniella Schltr. (Kasparek & Grimm, 1999; Kreziou
et al., 2016; Ghorbani et al., 2017). Not everything sold
as salep is, however, salep; tubers or bulbs of plants
other than orchids including Ranunculus ficaria
L. subsp. ficariiformis Rouy & Foucaud and Colchicum
cilicicum (Boiss.) Dammer are sold as salep (Kasparek
& Grimm, 1999; Sezik, 2002; Kreziou et al., 2016),
although this is noted as possibly being rare by
Ghorbani et al. (2014).
Vanilla
Vanilla spp. are globally important edible orchids, with
records of use, cultivation and trade in Mesoamerica
dating back to 1350–1500 (Lubinsky et al., 2008a).
Although wild Vanilla spp. and cultivated varieties are used medicinally in different cultures (e.g.
Madagascar; Randriamiharisoa et al., 2015), Vanilla
is traded primarily as a flavouring, and trade in the
artificially propagated material is exempt from CITES
regulation (CITES, 2017a). Of the numerous edible
cultivated taxa of Vanilla, Vanilla planifolia Andrews
Chikanda
The tubers of terrestrial orchids are used in several
African countries in the production of chikanda, a
large cake with a meat-like structure, made of ground
orchids and peanuts baked with ashes or baking
soda (Kaputo, 1996; Bingham, 2009). Chikanda is a
dish that was traditionally eaten by the Bemba tribe
in northern Zambia (Richards, 1939) and by tribe in
the Katanga province of the Democratic Republic of
Congo (Malaisse & Parent, 1985), the Sumbawanga
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Koopowitz, Lavarack & Dixon, 2003). However, commercial trade in wild plants continues, in response to both
domestic (e.g. Flores-Palacios & Valencia-Diaz, 2007)
and regional horticultural demand from hobbyist growers (e.g. Phelps & Webb, 2015) and specialist international demand from enthusiasts who target rare species
for their collections (Hinsley, Verissimo & Roberts, 2015;
Phelps, 2015). Contemporary, commercial horticultural
trade in wild plants has been formally documented from
Cambodia (Hinsley, 2011), China (Shepherd, Compton
& Warne, 2007; Gale et al., 2014), Indonesia (TRAFFIC,
2008; Hinsley et al., 2016b), Thailand, Myanmar and
Lao PDR (Lamxay, 2009; Schuiteman, 2013; Phelps
& Webb, 2015), Vietnam (Grieser-Johns & Thomson,
2005; Hinsley et al., 2016b), Nepal (Subedi et al., 2013),
Mexico (Flores-Palacios & Valencia-Diaz, 2007) and
Peru (Cribb, 2005). Formal research is limited, but collection of wild orchids for the horticultural trade is also
known to be occurring in many more countries, including Costa Rica, Madagascar, Malaysia, the Philippines
and Venezuela (pers. observ.).
ORCHID TRADE AND CONSERVATION
Faham
On the Indian Ocean islands of Réunion and Mauritius,
the aromatic leaves of Jumellea fragrans (Thouars)
Schltr. and J. rossii Senghas have long been traded as
faham used to flavour rum and in the production of
‘Bourbon tea’ (thé de Bourbon) or ‘Madagascan tea’ (thé
de Madagascar) (Decary, 1955). The leaves are also
used in Creole medicine (Longuefosse, 2006). Little is
known of the scale or nature of contemporary commercial trade.
reportedly first recognized in the 28th century BC by
Shennong, China’s founding emperor and patron deity
of agriculture (Hong, 2004; Bulpitt, 2007). With the
recent development of a consumer economy in China,
demand for Traditional Chinese Medicine (TCM) has
surged (Nijman, 2010; Liu et al., 2014; Zhang & Yin,
2014), further amplifying the value of traditionally
used species (Zhang, Hua & Sun, 2008; Liu et al., 2015).
The most prominently cited orchids in TCM are
various Dendrobium spp. used to make the drug
shi-hu [particularly D. catenatum Lindl. (including D. officinale Kimura & Migo), D. loddigesii
Rolfe, D. moniliforme (L.) Sw. and D. nobile Lindl.)]
(Teoh, 2016; Leon & Lin, 2017). In addition, tubers
of Gastrodia elata Blume (from which tian-ma is
prepared), rhizomes of Bletilla striata (Thunb.)
Rchb.f. (from which bai-ji is derived), the rhizomes
and stems of Anoectochilus spp. (jin-xian-lian) and
the corms of Cremastra appendiculata (D.Don)
Makino, Pleione bulbocodioides (Franch.) Rolfe
and P. yunnanensis (Rolfe) Rolfe (from which shan
ci gu is prepared) are all used (Teoh, 2016; Leon &
Lin, 2017). Only relatively recently have the effects
of some of these drugs been subjected to scientific
scrutiny, with some studies reporting the presence
of bioactive compounds of potential clinical significance in certain species (e.g. Ojemann et al., 2006;
Wang et al., 2014; Paudel et al., 2015).
Ayurvedic medicine
MEDICINAL USES
Orchids are also used in traditional medicine systems
around the world, from subsistence to commercial
levels of exploitation. Some of the most widespread,
commercial medicinal uses of orchids include Chinese
and South Asian Ayurvedic traditional medicine
(Teoh, 2016; Leon & Lin, 2017). They are also known
to be used in some African traditional medicine (e.g.
Vanilla madagascariensis Rolfe in Madagascar:
Randriamiharisoa et al., 2015), North American
folk medicine (e.g. Cypripedium acaule Aiton and
C. parviflorum Salisb.: Henkel, 1906) and the
Unani medicine system [e.g. Dactylorhiza hatagirea
(D.Don) Soó Vanda tessellata (Roxb.) Hook. ex G.Don,
Cymbidium bicolor Lindl. and Ipsea speciosa Lindl.:
Jayaweera & Fosberg, 1980; Thakur & Dixit, 2007;
Khajuria, Kumar & Bisht, 2017]. Medicinal orchids
are also traded much more widely around the world,
including to Europe as various traditional medicines
and health supplements (Brinkmann, 2014).
Chinese traditional medicine
Orchids appeared in the official Chinese pharmacopoeia in the 17th century, but their medicinal value was
Ayurvedic medicine originated in the Indian
Subcontinent and has become globally practised, as
part of the spread of complementary and alternative medicines. It includes a wide range of medicines,
including Asthavarga preparations (e.g. chyawanprash tonic; Dhyani, Nautiyal & Nautiyal, 2010) used
to treat a variety of ailments.
Nepal’s Ayurvedic trade has been reported to
involve c. 94 orchid species (Acharya & Rokaya, 2010;
Subedi et al., 2013), including Crepidium acuminatum
(D.Don) Szlach., Habenaria intermedia D.Don,
Herminium edgeworthii (Hook.f. ex Collett) X.H.Jin,
Schuit., Raskoti & Lu Q.Huang and Malaxis muscifera
(Lindl.) Kuntze (Hossain, 2009; Dhyani et al., 2010;
Khajuria et al., 2017). Eulophia spp. are also widely
used medicinally across large parts of India [E. dabia
(D.Don) Hochr., E. spectabilis Suresh in D.H.Nicolson,
C.R.Suresh & K.S.Manilal (= E. nuda Lindl.): Jalal,
Jayanthi & Kumar, 2014], and D. hatagirea is used
to treat a range of ailments (Pant & Rinchen, 2012).
Estimates suggest that 6200–31 000 kg of D. hatagirea
are harvested annually in the north-eastern
Himalayan region of Sikkim (Rai, Prasad & Sharma,
2000; Uniyal, Awasthi & Rawat, 2002), with each kilo
comprised c. 100 individuals (Pant & Rinchen, 2012).
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region in Tanzania (Leedal, 1975; Cribb & Leedal,
1982; Davenport & Ndangalasi, 2003; Nyomora, 2005),
Malawi (Kasulo, Mwabumba & Munthali, 2009) and
the Bayam people in Cameroon, where the dish is prepared in a similar way with tubers of two species of
Habenaria Willd. and called napssié (Menzepoh, 2011).
Orchid species used for chikanda, generally belong
to three genera (Disa P.J.Bergius, Habenaria and
Satyrium L.; Bingham et al., 2002; Bingham, Kokwe
& Golding, 2003; Davenport & Ndangalasi, 2003;
Hamisy, 2007; Challe & Struik, 2008; Challe & Price,
2009; Nyomora, 2005), but surveys have shown that
species of Brachycorythis Lindl. (Bingham, Kokwe &
Golding, 2003; Hamisy, 2008), Eulophia R.Br. (Hamisy,
2008) and Roeperocharis Rchb.f. (Hamisy, 2008; Challe
& Price, 2009) are now also harvested because of local
scarcity of the other taxa (Veldman et al., 2017).
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A. HINSLEY ET AL.
Paphiopedilum druryi (Bedd.) Stein, an IUCN-listed
Critically Endangered species endemic to southern
India, also continues to be collected for medicinal use
and horticulture (Maridassa, Zahir Hussain & Raju,
2008; Rankou & Kumar, 2015).
LEGAL–REGULATORY CONTEXT
CITES REGULATIONS
The CITES is a multilateral environmental agreement that regulates the international movement
of species that are, or may become, threatened as a
result of international trade. Species of concern are
included in one of three appendices, with > 35 000
species currently listed. Notably, orchids constitute >
70% of CITES-listed species (Fig. 1). This broad inclusion of orchids under CITES, which dates back to
the 1970s, is the result of a precautionary approach,
as many members of the family resemble other species (the so-called ‘look-alike’ principle) (ClementeMunoz, 2009) and are therefore likely candidates for
misidentification by the non-experts often responsible for inspecting trade shipments. Although some
exemptions have been made for certain types of
orchid material (e.g. seeds, seedlings in sterile flasks)
or taxa (e.g. Vanilla, some ornamental hybrids), the
international movement in most orchids, whether
for personal, commercial or scientific purposes, must
be monitored and sanctioned by the relevant CITES
agencies (CITES, 2017a).
The vast majority of legally traded orchid species are listed under CITES Appendix II, which
allows for their legal commercial trade, even if
the plants are wild collected. However, these cases
require import and export permits, and a demonstration that any export will not be detrimental
to the survival of the species (via a CITES NonDetriment Finding). A small number of orchid
species, notably members of two slipper orchid genera (Paphiopedilum Pfitzer and Phragmipedium
Rolfe), are listed on CITES Appendix I, which
does not allow international commercial trade
unless the material is artificially propagated from
legally obtained founder stock (Table 3).
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This prevalence and diversity of orchid trade is remarkable because orchids are among the best-protected
plant taxa globally. Orchids are subject to unique levels of legal protection, including wide protections from
the pressures of international trade, and national
legislation in many countries further restricts their
harvest from the wild.
NATIONAL LEGISLATION
The wild harvest and trade in orchids is also
regulated through national regulations in many
countries, notably protected species lists, restrictions on harvest in protected areas and/or on native
flora, and agricultural and trade legislation, including regulations that serve to operationalize country
commitments to CITES. In addition, orchids can also
be governed by rules associated with phytosanitary
requirements and legislation on food, medicinal or
cosmetic product standards. We highlight examples of
India and the USA to illustrate the diversity of rules
that apply to orchid harvest and trade.
In India, orchid harvest and trade is shaped
by several pieces of national legislation. Eleven
of the c. 1450 orchid species that occur in India
( principally Paphiopedilum spp.) are listed in the
Wildlife Protection Act 1972 and are legally protected
irrespective of where they grow (i.e. whether inside or
outside a designated protected area), although harvest
permission can be granted for research and education
purposes. The collection of all wild flora is prohibited
in protected areas (Ministry of Environment, Forest
and Climate Change, 1927; The Wildlife Protection
Act of India, 1972), although Scheduled Tribes and
other Traditional Forest Dwellers can apply for a
waiver (The State/Union Territory Minor Forest
Produce Act, 2005; Ministry of Law and Justice, 2006).
There is no rule, however, that prohibits the harvest
of non-protected orchids outside protected areas.
Some states have additional local restrictions on the
cutting down of trees (e.g. The West Bengal Trees
(Protection and Conservation in Non-Forest Areas)
Act, 2006) that provide indirect protection to many
epiphytic orchids. India maintains a list of species for
which international trade is banned, including the 11
protected orchid species and a select group of species
perceived to be under threat of trade (e.g. species of
Cypripedium L.; Department of Commerce, 2015).
Trade is further regulated by domestic legislation
informed by the Customs Act (1962), which also makes
provisions for CITES, and the Biological Diversity
Act of India (National Biodiversity Authority, 2002),
which protects all domestic biological resources as,
including prohibition on the collection, import and
export of orchid seeds and DNA samples, with exceptions for some non-commercial uses. As such, orchids
can only be commercially traded from India if proof
can be provided that they were obtained prior to 1972
or they were originally obtained from outside India in
accordance with CITES and phytosanitary regulations
(Department of Commerce, 2015).
In the USA, wild harvest of orchids is similarly
restricted by both generic legislation (e.g. that protects
ORCHID TRADE AND CONSERVATION
441
habitat), as well as protections for particular species.
The harvest of all flora is banned within all federal
lands, including national parks (GPO, 2016). Some
exemptions exist for plant harvest in national parks
by Native American tribes but this is predominantly
for subsistence use and handicrafts (National Parks
Service, 2016). Additional protections ban harvest of
endangered and threatened species nationally, including 15 orchid species, including Piperia yadonii Rand.
Morgan & Ackerman [=Platanthera yadonii (Rand.
Morgan & Ackerman) R.M.Bateman], Spiranthes
delitescens Sheviak and Spiranthes parksii Correll,
except for conservation and restoration purposes
with permits (Federal Endangered Species Act, 1973;
USFWS, 1985). In addition, State-level endangered and
threatened species lists can provide additional protections based on local-level assessments. For example, in
Florida, Dendrophylax lindenii (Lindl.) Benth. ex Rolfe
is recognized as an endangered species, the wild harvest of which is banned [The Florida Statutes (Section
581.185): The Florida Senate, 2016]. Additional State
legislation restricts all wild harvest of native flora
without specific permits (e.g. Preservation of Native
Flora of Florida). International trade is regulated by
the Lacey Act (USDA, 2008), Federal Endangered
Species Act, CITES and State laws. The Lacey Act prohibits the illegal import of wild plants into the USA.
The law is strict enough to cover illegally harvested
wild orchids. These pieces of legislation reinforce the
regulation of wild orchid trade, unless the trader provides an import permit issued by the US Department
of Agriculture (USDA) and other documents, including
CITES and phytosanitary certificates, thereby proving
that the plants are not wild collected.
CONSERVATION CHALLENGES
We identify five main conservation challenges associated with global orchid trade. Notably, (1) trade is
often associated with unsustainable, sometimes illegal, forms of harvest and trade. In addition, (2) there
are shifting patterns in the behaviour of the people
involved in orchid trade, notably consumers and intermediaries. Another hindrance is (3) the taxonomic
complexity of the family, which presents management
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Figure 1. Taxonomic breakdown of CITES Appendices I and II, showing the large proportion of orchids in the total number
of species listed by the Convention. Adapted from original in Hinsley (2016) using updated data from UNEP-WCMC (2015).
Vector images courtesy of the Integration and Application Network, University of Maryland Center for Environmental
Science (ian.umces.edu/symbols/).
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A. HINSLEY ET AL.
Table 3. Restrictions on international trade of orchid species listed in CITES Appendices I and II
Species
CITES regulations*
CITES
Appendix I
Aerangis ellisii
(B.S.Williams) Schltr.
Dendrobium cruentum
Rchb.f.
Laelia jongheana Rchb.f.
[=Cattleya jongheana
(Rchb.f.) Van de Berg]
Laelia lobata (Lindl.)
A.H.Kent (=Cattleya
lobata Lindl.)
Peristeria elata Hook.
Renanthera imschootiana
Rolfe
Paphiopedilum spp.
Phragmipedium spp.
An import permit issued by the Management Authority (MA) of the State
of import is required. This may be issued only if the specimen will not be
used for primarily commercial purposes and if the import is for purposes
that are not detrimental to the survival of the species. In the case of a live
animal or plant, the Scientific Authority (SA) must be satisfied that the
proposed recipient is suitably equipped to house and care for it.
CITES
All other species in the
Appendix II
family Orchidaceae
An export permit or re-export certificate issued by the MA of the State of
export or re-export is also required.
An export permit may be issued only if the specimen was legally obtained,
the trade will not be detrimental to the survival of the species, and an
import permit has already been issued.
A re-export certificate may be issued only if the specimen was imported in
accordance with the provisions of the Convention and, in the case of a live
animal or plant, if an import permit has been issued.
In the case of a live animal or plant, it must be prepared and shipped to
minimize any risk of injury, damage to health or cruel treatment.
An export permit or re-export certificate issued by the MA of the State of
export or re-export is required.
Export permit may be issued only if the specimen was legally obtained and if
the export is not detrimental to the survival of the species.
A re-export certificate may be issued only if the specimen was imported in
accordance with the Convention.
In the case of a live animal or plant, it must be prepared and shipped to
minimize any risk of injury, damage to health or cruel treatment.
No import permit is needed unless required by national law.
*Summary of CITES regulations as presented in Clemente-Munoz (2009).
challenges for species identification. Furthermore, (4)
there are basic gaps in ecological data and conservation status assessments, which limit sustainable management of orchid resources. Finally, (5) institutional
barriers arise from the low priority placed on plants in
broader efforts to address the unsustainable wildlife
trade, and limit the legal international orchid trade
in ways that constrain scientific exchange and potentially beneficial commerce.
UNSUSTAINABLE AND ILLEGAL HARVEST
There is widespread, if largely anecdotal, evidence
that the commercial harvest and trade for several uses
is negatively affecting wild populations. For example,
trade in ornamental Southeast Asian orchids is suspected to be negatively impacting wild populations
at local and regional scales, notably based on reports
from harvesters themselves, who report dramatically
declining populations (Schuiteman et al., 2008). In
addition, out of 347 species identified in ornamental
trade in continental Southeast Asia, 58 of the species were either endemic or had been identified as
domestically threatened in Thailand (Phelps, 2015).
There are also numerous, although largely anecdotal,
cases of species extirpations and extinctions as a result
of intensive harvest, primarily of lady’s slipper orchids
in the genera Paphiopedilum and Phragmipedium.
For example, Paphiopedilum glaucophyllum J.J.Sm. is
now absent from most of its range on Java, Indonesia
(Whitten et al., 1997). More recently, the newly discovered Vietnamese species, Paphiopedilum canhii Aver.
& O.Gruss, suffered commercial harvest of 99.5% of
its population (Averyanov et al., 2014), following the
similar fate of many other charismatic species in the
region [e.g. Malaysian Paphiopedilum spp., such as
P. barbatum (Lindl.) Pfitzer, P. bullenianum (Rchb.f.)
Pfitzer var. bullenianum, P. callosum (Rchb.f.) Stein, P.
lowii (Lindl.) Stein var. lowii, P. niveum (Rchb.f.) Stein;
Leong, 2014]. Similarly, some Neotropical lady’s slippers have been intensively harvested; Phragmipedium
kovachii J.T.Atwood, Dalström & Ric.Fernández was
virtually extirpated from its limited range following
is discovery in Peru in 2001 (Cribb, 2005). However,
other groups are also vulnerable to intensive harvest. Phalaenopsis javanica J.J.Sm. was thought to
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Category
ORCHID TRADE AND CONSERVATION
million orchids are harvested annually, mainly for
export to Turkey (Ghorbani et al., 2014). Kreziou et al.
(2016) also reported a renewed interest from Greece
in salep as a natural product. Similarly, J. fragrans is
now extremely rare in Mauritius, potentially due to
collection for faham (D. Roberts, pers. observ.).
Increased demand and the resulting harvest of
many medicinal orchids is also proving unsustainable in many cases. For example, Ayurvedic medicinal orchids such as Habenaria intermedia and
H. pubescens Lindl. have been extirpated from parts
of their native ranges (Chauhan, Nautiyal & Prasad,
2007), populations of E. dabia and D. hatagirea are
declining in the Indian Himalayan Region due to
over-harvest (Kala, 2000; Jalal et al., 2014) and there
is widespread concern in the related literature about
the conservation impacts of medicinal harvest across
India, Nepal and Bangladesh (e.g. Hossain, 2009;
Subedi et al., 2013; Pant & Raskoti, 2013; Khajuria
et al., 2017). Increased demand for orchid-containing
TCM is reportedly unsustainable in China, and this
has driven sourcing for some orchids (e.g. Dendrobium
spp.) to neighbouring countries, including Lao PDR,
Myanmar, Nepal and Vietnam (Zhang et al., 2008;
Lamxay, 2009; Subedi et al., 2013; Liu et al., 2014;
Phelps, 2015; Pant et al., 2016).
Unsustainable harvest pressure on wild orchid populations can be the result of illegal collection that violates domestic and international legislation. Notably,
much of the unsustainable harvest and international
trade that has been documented by researchers is not
reflected in official CITES trade statistics, including
for salep (Ghorbani et al., 2014), chikanda (Veldman
et al., 2014), ornamental species (Phelps & Webb, 2015)
and medicinal orchids (Lamxay, 2009). This means
that, even in cases of CITES Appendix II listed species,
for which international trade might be legal, trade is
frequently occurring without the requisite permits
and CITES Non-Detriment Findings (Hinsley et al.,
2016c). In many cases, this appears to be an issue of
non-enforcement of environmental and CITES legislation, such as at the open cross-border trade and public
plant markets in many parts of Southeast Asia (Phelps
& Webb, 2015). In other cases, it involves smuggling,
as at the Iran–Iraq and Iran–Turkey borders where
salep passes in bags labelled as almonds (A. Ghorbani,
H. de Boer, pers. observ.). At the Tanzania–Zambia
border, border guards report that no chikanda passes
the border, whereas traders report that they transport
chikanda tubers marked as potatoes in 100- to 150-kg
bags (S. Veldman, H. de Boer, pers. observ.). In other
cases, illegal trade involves the laundering of wild
specimens as artificially propagated species to circumvent protections on wild plants (Phelps, 2015; S. Gale,
L. Gardiner, A. Hinsley, J. Phelps, D. Roberts, pers.
observ.).
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have collected to extinction from its only known site
on Java, Indonesia (Whitten et al., 1997), although a
commercial trader has reportedly rediscovered it in a
new locality (D. Metusala, pers. observ.). Similarly, in
the early 1990s, almost all individuals of Grammangis
spectabilis Bosser & Morat were collected from its
habitat in Madagascar, with only nine individuals
found in the wild during recent surveys (Rajaovelona
& Gardiner, 2017).
Trade in edible orchids is also suspected to lead to
over-harvesting of populations of many species in many
range countries. Although chikanda was traditionally
used at a household scale and in times of famine, its
popularity has increased and it is now a national dish
in Zambia (Davenport & Ndangalasi, 2003; Bingham,
2009; Veldman et al., 2014). Chikanda is sold as a
snack on local markets and in supermarkets and
is advertised on the menus of upscale bars and restaurants (Davenport & Ndangalasi, 2003; Bingham,
2009). To accommodate the increased demand for chikanda, tubers are now also imported from surrounding
countries. In 2003, 2.2–4.1 million tubers were reportedly exported annually from Tanzania to Zambia
(Davenport & Ndangalasi, 2003), a trade volume estimate that was verified in 2014 (Veldman et al., 2014).
Trade in orchids for chikanda is thought to threaten
up to 85 species in Tanzania (Davenport & Ndangalasi,
2003) and Zambia (Bingham & Kokwe, 2001; Golding,
2001). The intensive over-exploitation threat contributed to the establishment of Kitulo National Park in
Tanzania specifically to protect orchids (Davenport &
Bytebier, 2004). Orchids for chikanda have reportedly
become so depleted in Zambia that traders are now
importing tubers from several neighbouring countries
(Davenport & Ndangalasi, 2003; Veldman et al., 2014).
Market surveys and interviews with collectors show
that demand outstrips supply and that intermediaries
and collectors now report sourcing tubers from as far
afield as Mozambique, Malawi, DR Congo and Angola
(Veldman et al., 2014).
Threats from the edible orchid trade are not restricted
to chikanda; trade in several of the orchid species used
for salep is reportedly having an impact on populations in different countries. Collection in Turkey has
been estimated to involve tubers from 30 to 120 million orchid plants annually, producing > 15 tonnes of
salep (Kreutz, 2002; Sezik, 2002). Earlier estimates for
Turkey by Read & Groves (1994; cited in Kasparek &
Grimm, 1999) and Kasparek & Grimm (1999) put the
figure at 10–20 million and 9.8–19.6 million, respectively. More recent estimates suggest that 80 tonnes of
orchid tubers are collected annually in Turkey (Zafer
Kızılkaya; pers. comm. to Hattam, 2013).
The depletion of resources in Turkey has reportedly
caused traders to look abroad and has fuelled an orchid
harvesting boom in neighbouring Iran, where 5.5–11.0
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SHIFTING TRADE AND CONSUMER PATTERNS
Substitutions and adulteration of orchid
products
Emerging online orchid sales
Wildlife trade has become established on the Internet,
with legal and illegal trade in animal and plant products occurring on a variety of online platforms (Shirey
et al., 2013; Lavorgna, 2014; Yu & Jia, 2015). There
is initial evidence that online platforms are becoming increasingly important for the sale of wild orchids
(Hinsley, 2016). A survey of a large international social
media website found that trade was occurring in all
geographical regions and that up to 46% of trade was
in wild-collected plants (Hinsley et al., 2016b). The
availability of wild orchids for sale online may be of
conservation concern, as buyers of ornamental orchids
who shop online are more likely to prefer to buy rare
plants (Hinsley et al., 2015) and online trade is used
by some sellers to bypass CITES regulations (Hinsley
et al., 2016c). To recognize this threat, CITES has multiple Decisions urging Parties to assess the extent and
trends in wildlife e-commerce (CITES, 2017b).
CONSUMER PREFERENCES FOR WILD PLANTS
Efforts to reduce unsustainable and/or illegal wild
harvest of orchids have often prompted efforts to cultivate (artificially propagate) target species to meet
TAXONOMIC COMPLEXITY
Species identification
Orchidaceae is one of the largest family of angiosperms
(Chase et al., 2015), with a taxonomy based heavily on
floral characteristics (and reflected in genetic relationships), meaning that accurate species identification
requires training and is challenging for sterile material. This is further limited by the lack of complete
and up-to-date taxonomic reference material and literature in many countries and genera and is further
aggravated by the tendency by some authors towards
over-description of species in the family – with motivating factors including the charisma, enthusiasm and
vested financial interests that often accompany orchid
work (Pillon & Chase, 2007). Taxonomic challenges
are compounded in the case of products that contain
orchids, in which constituent parts may be processed
by drying and curing, making species identification
based on plant morphology practically impossible.
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In traditional pharmacopoeias, substitutions in which
one species is replaced for another are common (e.g.
Khajuria et al., 2017). However, as an effect of growing demand and reduced wild supply of some orchid
species, there is evidence that some products are
being both substituted and adulterated with other,
non-target species, including those not traditionally
considered in pharmacopoeias. Medicinal orchids in
TCM have been adulterated with both substitute
taxa and farmed products that are purportedly from
the wild (Lau et al., 2001; Zhang et al., 2005; Heubl,
2010; Williamson et al., 2013). For example, many
Dendrobium spp. are often used as adulterants in the
traditional medicine shi hu (Lau et al., 2001; Wu et al.,
2009). Similarly, edible salep is being adulterated with
tubers and bulbs of plants, including substitute orchid
and non-orchid species (e.g. R. ficaria, C. cilicicum;
Sezik, 2002). Substitutions are also occurring among
Eulophia spp. with Ayurvedic medicine, as some species become scarce (Jalal et al., 2014). Increased use of
substitutes and adulterants presents an issue not only
for consumers, but is potentially shifting the impact
of unsustainable wild harvest onto a broader range of
orchid species and onto other taxonomic groups, with
potential cascading conservation effects.
demand and reduce pressures on wild populations.
Such efforts, however, are hampered in some cases by
consumer preferences for wild, often rare plants over
cultivated alternatives.
Preference for wild plants has been shown in ornamental markets due to perceived differences in attributes such as robustness, fragrance and ‘authenticity’
(Phelps, Carrasco & Webb, 2014). Similar preferences
and price premiums have been found for rare species
(Hinsley et al., 2015), supported by surveys of plant
markets in Southeast Asia and Mexico that have
found many species with small, often obscure flowers (Flores-Palacios & Valencia-Diaz, 2007; Phelps &
Webb, 2015). This can be linked to the desire to collect
and be the first to own new or unusual species and
varieties (cf. Hall, Milner-Gulland & Courchamp, 2008;
Hinsley et al., 2015) and to produce new hybrids from
these species that can be named and publically shown
for horticultural awards. This is probably the driver
for a phenomenon by which orchid species enter commercial trade even prior to scientific description (e.g.
Vermeulen, Phelps & Thavipoke, 2014).
The preference of wild-harvested orchids is also
present in some parts of traditional medicine trade,
in which wild-harvested treatments are viewed as
more effective (Liu et al., 2014). This may even extend
to a preference for a specific provenance of the plants
collected from mountains and even villages within a
species range, which are purported to produce plants
of superior quality (Bao, Shun & Chen, 2001). The
greater value placed on these plants (Liu et al., 2015)
has led to populations at many of these ‘famed’ locations becoming economically or biologically extinct
(Bao et al., 2001; Ding et al., 2008; He et al., 2009).
ORCHID TRADE AND CONSERVATION
Genetic tools for orchid identification
Molecular genetic tools aid species-level orchid identification, and such tools are increasingly part of wildlife
trade monitoring for traded animals of conservation
concern (e.g. tigers, pangolins and lizards: Wilson et al.,
2016). Techniques include Sanger sequencing-based
DNA ‘barcoding’ techniques, which for plants typically
compare two or more DNA regions (or ‘markers’) from
each specimen with a library of verified reference samples (i.e. the identity of each reference sample being
known and related to a voucher specimen deposited in
a herbarium for future re-verification; Hollingsworth
et al., 2016). They also include the so-called next-generation sequencing techniques that use the whole genome or a much larger number of markers from across
the entire genome to compare with a reference library.
Barcoding approaches have been trialled for the
monitoring of ornamental orchid trade (Phelps, 2015),
to identify constituent species in processed medicinal
products (e.g. Lau et al., 2001; Wu et al., 2009; Yao et al.,
2009) and, most recently, to identify species in edible
orchid products (Ghorbani et al., 2017; Veldman et al.,
2017). However, the application of these techniques
to orchids has presented several challenges. Notably,
there is still a lack of reference samples for most orchid
groups and high diversity areas, and a high-quality,
vouchered and comprehensive library of reference
sequences is essential for such tools to enable specieslevel identification. Public DNA databases such as
GenBank (https://www.ncbi.nlm.nih.gov/genbank/)
and BOLD (http://www.boldsystems.org/) are important repositories of DNA sequence data and both include
large numbers of DNA sequences of Orchidaceae; however, such databases often include many taxa that
are not vouchered. Since these identifications cannot
be reliably verified, the sequences fall far short of the
minimum criteria to be used as barcode reference
sequences (Nilsson et al., 2006). In many parts of the
world, there are no comprehensive live collections
of orchid taxa in national botanical institutions (e.g.
BGCI, 2017; SE Asia, Phelps, 2015), let alone specimens that represent the range of genetic diversity
across widely distributed species.
Other challenges include the lack of consistent DNA
markers for barcoding that can confidently achieve
species-level identification in areas with high levels of
orchid diversity. Although some studies have proposed
options (Lau et al., 2001; Gigot et al., 2007; Ghorbani
et al., 2017), others have questioned their accuracy
due to large interspecific and intraspecific variation
(Phelps, 2015; Guo et al., 2016); however, extended
reference databases may address this (Veldman
et al., 2017). In addition, it is likely that hybridization, cross-pollination and wide-ranging and therefore
genetically diverse species can reduce the accuracy
of identifications based on limited reference samples.
Furthermore, many orchid species may be virtually
identical when standard DNA barcoding regions are
compared, even though they may be morphologically
different (as the result of rapid evolution of different
floral traits, often due to pollinator-driven adaptation), making such species extremely difficult to distinguish using such regions (DeSalle, Egan & Siddall,
2005). Finding suitable markers for species distinction is facilitated by innovations in high-throughput
sequencing approaches that provide vastly more data
for selection of variable markers, such as gene-capture
and target-enrichment sequencing, genome skimming
and Hyb-Seq (Mamanova et al., 2010). Standard DNA
barcoding is likely to remain important for identification of plants, but genomic barcoding will play an
important role in identification and selection of suitable high-resolution markers (Coissac et al., 2016).
DATA GAPS IN CONSERVATION ASSESSMENTS,
ECOLOGICAL DATA AND HARVEST STUDIES
There are major gaps in our understanding of basic
orchid ecology and conservation (Cribb et al., 2003;
Corlett, 2016). Despite recent efforts to increase the
number of orchids assessed (Fay, 2014; IUCN, 2014),
the number of global IUCN Red List assessments
published remains extremely low. Just 880 orchid species have been formally evaluated using IUCN Red
List Criteria (3% of the family), and many of these
assessments are over a decade old (IUCN, 2017; Nic
Lughadha et al., 2017). These are dominated by recent,
focused Red Listing in certain countries (e.g. China
and Madagascar; Fig. 2) and in a small number of
charismatic genera (e.g. the slipper orchids, subfamily
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These identification barriers present particular
challenges to customs officials expected to implement
trade regulations at border crossings. Non-experts, in
most cases, struggle with even genus-level identification (cf. McGough et al., 2004), and most experts are
unable to identify many orchids confidently to species or subgenus level when presented with sterile
specimens (e.g. Phelps & Webb, 2015). Strengthening
the capacity of customs officers to enforce CITES correctly is a priority for the Convention, highlighted in
Decision 17.34 (CITES, 2017c). However, the diversity
of orchid species in trade and the variety of forms in
which they are traded present customs agents with
a significant challenge and may make it difficult to
determine whether the item is even an orchid, whether
a CITES permit is needed, what CITES Appendix
applies and whether the plant is wild collected or artificially propagated (McGough et al., 2006).
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A. HINSLEY ET AL.
Cypripedioideae) and by the efforts of the Sampled Red
List Index of Plants project (Brummitt & Bachman,
2010; Brummitt et al., 2015a, b).
A lack of conservation assessments presents considerable challenges to efforts to determine the environmental impacts of harvest. In particular, these gaps
hamper the work by CITES scientific authorities to
conduct the necessary non-detriment findings (NDFs)
to ensure that international trade in Appendix II listed
species is not having a negative impact on wild populations, and should be legally permitted.
The lack of global conservation assessments for
orchids reflects profound gaps in the ecological knowledge about orchids and challenges of studying the family. This includes taxonomic challenges, which limit
the viability of research into population dynamics
(and related population viability analyses), especially
in species-rich ecosystems where it is challenging to
reach species-level identifications of non-reproductive
individuals (Mondragón, 2011; although see Tremblay
& Hutchings, 2003; Mondragón, 2009). Moreover,
many orchid species have restricted distributions,
briefly visible growth phases (e.g. many terrestrial
species, leafless species), ephemeral flowers (e.g. species of Sobralia Ruiz & Pav.), short blooming seasons
and/or epiphytic growth habits that make them physically hard to access; in addition, there is a need to consider horizontal and vertical distributions of epiphytic
species (Mondragón, 2011).
INSTITUTIONAL BARRIERS
Plants as a low conservation priority
Amidst growing interests and concern over wildlife
trade, focus has been disproportionately on charismatic megafauna, and as a result, taxa such as plants
have been largely overlooked by conservation organizations, government agencies and the public (Phelps &
Webb, 2015; cf. Nijman et al., 2012; Small, 2012). Where
there has been willingness to tackle some challenging
and contentious trade issues, including non-compliance of countries that have allowed illegal wildlife
trade (e.g. elephant ivory, Van Aarde & Ferreira, 2009;
rosewood, Barrett et al., 2010), there is no similar
public support to address illegal trade in non-timber
plants (see Phelps & Webb, 2015). Similarly, orchids
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Figure 2. Number of native orchid taxa in each country currently assessed for the IUCN Red List (data: IUCN, 2017;
downloaded March 2017).
ORCHID TRADE AND CONSERVATION
Barriers to legal trade
In an effort to protect species from the pressures of
intense international trade (as well as invasive species,
bioprospecting etc.), legislators have placed significant
legislative controls on the legal international trade of
plants, for commercial and scientific purposes. This
can include restrictions on transport of CITES-listed
orchids, which in many countries, require extensive
permitting, are slow and involve high economic costs.
These may represent undue burdens on commercial
and hobbyist traders who seek to comply with the law
(Hinsley et al., 2016c) and may also limit the exchange
and movement of scientific samples needed for taxonomic and conservation research, such as plants, seeds,
dried/pickled specimens and DNA (Roberts & Solow,
2008). CITES allows the international, non-commercial
loan, donation or exchange of museum and herbarium
specimens (Article VII Exemptions and Other Special
Provisions Relating to Trade, paragraph 6 and CITES
Res. Conf. 11.15, Rev. CoP12), between Registered
Scientific Institutions (RSIs, see https://cites.org/common/reg/e_si.html for a list of RSIs by country), and
some in-country CITES authorities grant fee waivers
for movement of orchid specimens and plants for scientific and conservation reasons (e.g. https://www.gov.uk/
government/publications/endangered-species-application-for-a-waiver-from-paying-permit-fees). However,
many countries that are Parties to CITES do not have
any RSIs and, even where they exist, authorities are
often unfamiliar with the processes or unaware of
the exemptions, meaning that costly and time-intensive CITES permits are sometimes still required.
Bureaucratic processes in many countries mean that
the process regularly takes 2–3 months, and often substantially longer, delaying conservation research and
potentially endangering plant material, including live
plants of new species (Roberts & Solow, 2008).
These burdens limit science and legal trade and
potentially create incentives for illegal action, by
hobbyists, commercial traders and even scientists
who are eager to move specimens between countries.
Furthermore, there are particular motivations for rulebreaking when compliance represents such a burden,
relative to the ease with which much illegal activity
seems to occur in many contexts (Hinsley et al., 2016c).
CONSERVATION PRIORITIES IN THE
GLOBAL ORCHID TRADE
Future priorities for the conservation of orchids in
trade must consider the diversity of orchid products,
markets and specific conservation challenges facing
practitioners and policy makers attempting to tackle
illegal and unsustainable trade. Although other areas
of research and conservation action undoubtedly exist,
we consider the following four areas to be the most
pressing and feasible, given existing budgetary and
institutional limitations.
CONDUCT BASIC RESEARCH ON TRADE DYNAMICS AND
IMPACTS OF HARVEST
There are huge gaps in our understanding of orchid
trade. In many regions, there is little certainty over
exactly which species are being actively harvested,
traded and used. Although some work has been done to
document the use of orchid derivatives in key cosmetic
and medicinal products (Brinkmann, 2014), little published information exists, particularly on the species
involved, where the plants originate and whether they
are wild-collected or nursery-grown. For the trade in
orchids for fragrances, flower extracts and cosmetic
products this is, in part, due to industry confidentiality issues (Groves & Rutherford, 2017). As a result,
there is little information on related harvest dynamics,
including sites of harvest, scales of trade, number of
people involved and value chains. These data, however,
are particularly important given the size of the family and the need to prioritize enforcement, research
and conservation efforts. The blanket protection of the
family from trade via CITES and some national legislation potentially creates an illusion of conservation
outcomes, but there is nevertheless a need to understand which species are actually being targeted.
Moreover, there is a need to understand how different commercial trades impact wild populations
and species survival. Little attention has been paid
to assessments of the impact of harvesting and population viability analyses, particularly in tropical and
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are unlikely to be a priority for customs officers, park
rangers or other enforcement officials, when compared to high-profile wildlife products such as ivory
and rhino horn. This bias is manifested in several
ways; for example, the ASEAN Wildlife Enforcement
Network focuses only on fauna, the UK Department
for International Development fund to address illegal
wildlife trade (IWT Challenge Fund) excludes funding
for botanical trade and conservation [UK Department
for Environment, Food & Rural Affairs (DEFRA),
2017] and enforcement and education efforts to
reduce illegal wildlife trade at the Chatuchak Market
in Bangkok have focused on fauna, while the illegal
trade of wild ornamental orchid remains rampant
(Phelps, 2015). This relatively low profile represents
an ongoing challenge to recruiting funding and action
for botanical conservation and promoting sustainable
use of wild plant resources.
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A. HINSLEY ET AL.
subtropical regions of greatest orchid diversity. These
data are, however, instrumental to assessing the
impact of trade on the conservation status of species
(e.g. during Red Listing), understanding how commercial harvest affects populations and determining
whether sustainable harvest is viable (e.g. during
CITES Non-Detriment Findings). Given the size of the
family and the logistical challenges of studying orchids,
species that are known to be facing intense harvest
pressures should be priorities for such research.
International illegal orchid trade should be addressed
via CITES enforcement mechanisms. Although orchids
represent the majority of CITES-listed species (Fig. 1),
in many cases this designation exists only on paper
and existing rules have been poorly operationalized,
with cases of non-compliance being largely overlooked. Moreover, orchids are under-represented on
the contemporary CITES agendas (e.g. CITES 17th
Conference of Parties, https://cites.org/eng/cop/index.
php). Although there is considerable attention on
trade in many species of megafauna, there is apparently comparatively little awareness or concern among
the CITES community about the scope and scale of
orchid trade that does not comply with the provisions
of the Convention.
There is a clear need to raise the profile of orchids
within the CITES process, including ensuring Parties
are aware of and prioritize application of existing regulations to protect plant taxa from unsustainable trade.
For orchids, this may mean efforts to transition existing undocumented and illegal orchid trade into a legal,
regulated trade in Appendix II species (see Table 1).
A priority is thus to understand the scope and potential for shifting some of this into legal trade.
Moreover, there is a need for action by CITES
Parties to address documented cases of illegal trade
in wild plants and other forms of non-compliance with
the Convention. The prevalence of illegal orchid trade
means that most orchid trade is ‘invisible’ in official
records and thus generally overlooked, as shown by
the official reported trade statistics in Figure 3. This
contributes to a lack of awareness of the scale of orchid
trade and prevents real trends from being identified
during the Review of Significant Trade process, which
is designed to alert CITES to emerging unsustainable
trade. Currently, there is no process within CITES to
identify trends in the illegal trade of orchids, although
this does exist for other taxa. For example, in response
to illegal trade of CITES-listed elephants, CITES
Parties have approved two programmes to monitor
and help reduce illegal elephant poaching and trade,
STRENGTHEN AND SUPPORT LEGAL TRADE
Although it may be possible to facilitate legal sustainable trade in some wild Appendix II orchid species,
propagation has been widely proposed as a better conservation strategy (Subedi et al., 2013; Liu et al., 2014).
Propagation for domestic trade can involve growing
plants in greenhouses or shadehouses or semi-wild
cultivation in natural habitats (e.g. Liu et al., 2014),
although for international trade, compliance with the
CITES definition of artificially propagated requires
plants to be grown in ‘non-natural’ and ‘controlled
conditions’ [CITES Res. Conf. 11.11 (Rev. CoP17)].
Propagation may provide a sustainable source of
species that are already traded in large commercial
quantities and newly discovered species for which
propagation may help to offset demand for wild specimens. However, the provision of artificially propagated
plants does not automatically prevent wild harvesting
and there is a need to consider the conditions under
which it is most likely to yield conservation benefits
(Phelps et al., 2014).
One major drawback of trade in artificially propagated plants is the opportunity it presents for wildcollected material to be laundered into the legal trade
chain (Phelps, 2015), meaning that strong traceability
methods are required to confirm the provenance of
propagated plants. Customs agents checking shipments
are unlikely to have specialist knowledge on plants and
identifying the origin of traded orchids using visual
inspection may be difficult for live orchid plants and
impossible for processed derivatives (McGough et al.,
2006). This process may be improved by using more
sophisticated traceability techniques for determining
wild origin. The need for a more coordinated traceability approach for orchids and other horticultural plants
was recognized at the 17th CITES Conference of the
Parties in 2016, with suggestions to create international
frameworks for standardizing traceability of these
products (UNCTAD, 2016). Traceability can involve
physically marking plants, for example with microdots
(as trialled in South African cycads: Nordling, 2014), or
it can draw on molecular techniques discussed above.
Another option is stable isotope analysis, which examines ratios of stable isotopes present in a tissue sample
to establish its geographical origin and potentially the
conditions under which the plant was grown (Nordling,
2014; Hinsley, King & Sinovas, 2016a). This method
has been applied to traceability in the Vanilla trade to
determine natural vanillin from mislabelled artificial
substitutes (Hansen, Fromberg & Frandsen, 2014) and
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REDUCE ILLEGAL TRADE AND CITES
NON-COMPLIANCE
Monitoring the Illegal Killing of Elephants (MIKE)
and the Elephant Trade Information System (ETIS),
which now help to inform policy responses.
ORCHID TRADE AND CONSERVATION
449
to establish provenance in the frog leg trade (Dittrich,
Struck & Rödel, 2017), but has yet to be widely applied.
Implementing robust traceability systems could also
underpin other conservation action, such as the development of certification schemes for sustainably produced orchids, a model that is already applied to certain
plant products in the medicinal and aromatic trade via
the FairWild standard (http://www.fairwild.org).
RAISE THE PROFILE OF ORCHID CONSERVATION
Orchids are unique for their charisma, prominent
place in popular culture and wide following among
horticulturalists (Hansen, 2001). However, efforts to
address unsustainable and illegal trade are hampered
by a lack of awareness of the importance of this work,
and the low profile of orchid conservation relative to
that of other taxonomic groups. This is recognized in
CITES itself, which specifically mentions the importance of working with trade organizations, NGOs and
botanical gardens to educate people on the importance of legal trade and the implementation of the
Convention for plants [Res. Conf. 11.11 (Rev. CoP17)].
However, while local-scale awareness raising of orchid
conservation has taken place in some areas where they
are wild collected (e.g. Nepal; Pant et al., 2016), two
groups that have been difficult to engage have been the
international traders and end users of orchids, particularly in the horticultural trade (Hinsley et al., 2016c).
Members of the horticultural community are often
aware of commercial demand for rare and protected
species, with some actively seeking to buy rare species
(Hinsley et al., 2015). This puts them in a unique position to help to identify emerging conservation issues,
including species that are being targeted for trade
from the wild. Engaging this community more deeply
in conservation efforts has the potential to establish new codes of practice that condemn, rather than
reward, collecting practices that threaten species conservation. We therefore suggest that communities of
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Figure 3. Reported commercial trade in live artificially propagated and wild-sourced orchid plants between 1996 and
2015, as reported by importers. ‘Wild-sourced’ is defined as trade reported as source W, U and no source; ‘Artificially propagated’ is defined as trade reported under the source codes for plants (A, D) and captive-bred animals (C, F), the latter to
capture low levels of misreported data. Data: CITES trade statistics derived from the CITES Trade Database, UNEP World
Conservation Monitoring Centre, Cambridge, UK, https://trade.cites.org, downloaded May 2017.
450
A. HINSLEY ET AL.
CONCLUSIONS
Despite appearing to be, at least on paper, one of the
most legally protected groups of organisms, many
orchid species around the world are under threat
from illegal and unsustainable trade for many purposes, primarily for horticulture, food and medicine.
In addition to habitat preservation, a conservation
priority for orchids should be to better understand
trade and to address its threats. This should take the
form of conducting basic research on trade dynamics
and impacts of harvest, addressing illegal trade and
CITES non-compliance, strengthening and supporting
legal trade and raising the profile of orchid trade as an
important conservation issue – worthy of wider attention and conservation efforts.
ACKNOWLEDGEMENTS
This review resulted from the formation of a group
within the Orchid Specialist Group of the Species
Survival Commission (SSC) of the IUCN. Members
of the SSC are thanked for their support and many
informative conversations. We gratefully acknowledge
funding from the Environment Agency, Abu Dhabi,
which facilitated the Red List assessment of all slipper orchids, allowing the profile of a whole subfamily
of orchids to be raised. A.H. gratefully acknowledges
the support of the Oxford Martin Programme on the
Illegal Wildlife Trade.
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