The IUCN Red List of Threatened Species™
ISSN 2307-8235 (online)
IUCN 2022: T215341339A2813403
Scope(s): Global
Language: English
Dalbergia oliveri, Tamalan
Assessment by: Barstow,  M. et al.
View on www.iucnredlist.org
Short citation: Barstow,  M. et al. 2022. Dalbergia oliveri. The IUCN Red List of Threatened Species
2022: e.T215341339A2813403. https://dx.doi.org/10.2305/IUCN.UK.2022-
1.RLTS.T215341339A2813403.en [see full citation at end]
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THE IUCN RED LIST OF THREATENED SPECIES™
Taxonomy
Kingdom Phylum Class Order Family
Plantae Tracheophyta Magnoliopsida Fabales Fabaceae
Scientific Name:  Dalbergia oliveri Gamble ex Prain
Synonym(s):
• Dalbergia bariensis Pierre
• Dalbergia dongnaiensis Pierre
• Dalbergia duperreana Pierre
• Dalbergia mammosa Pierre
Common Name(s):
• Burmese: Tamalan, Chingchan
• English: Burmese Rosewood
• Central Khmer: Neang Nuon
• Lao: Kampee, Mai Kor Phee, Pa Dong Daeng
• Thai: Mai Ching Chan
• Vietnamese: Cam Lai
Taxonomic Source(s):
WCVP. 2022. World Checklist of Vascular Plants (WCVP), version 2.0. Facilitated by the Royal Botanic
Gardens, Kew. Available at: http://wcvp.science.kew.org/. (Accessed: 2022).
Assessment Information
Red List Category & Criteria: Critically Endangered A2cd+3cd+4cd ver 3.1
Year Published: 2022
Date Assessed: July  3, 2020
Justification:
Dalbergia oliveri (Burmese Rosewood) is native to Thailand, Cambodia, Viet Nam, Myanmar and Laos
PDR. The species has a wide geographic range, and is widespread in each country within its range
however the subpopulations are small and scattered. The species was once more common and
widespread, however in recent years the species has come under increasing pressure from the
international timber market. This is due to a rise in demand for rosewood timber for the production of
hongmu furniture within China and Viet Nam with China as the major consumer. Imports of Rosewood
to China have increase by 65-times since 2005, including imports of this species. Already, half of China's
rosewood is from range states of Dalbergia oliveri. Demand on the species has also increased as other
species of hongmu timber producing trees have declined in the wild and are also put under increasing
conservation protocol, causing a shift in harvest to D. oliveri. Overexploitation is also driven by
corruption in political systems and crime syndicates, who can target D. oliveri trees for harvest in
National Parks and through the guise of land development (as is the case in Cambodia). Due to the value
earned for D. oliveri logs on the international market, there is drive to keep harvesting the trees even
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though they become rarer and there is also increasing risk.
Complete population information is not available for each country in it's range. However, the greatest
loss is recorded from Myanmar where the species is predicted to reach commercial exhaustion between
2016 and 2023. In Viet Nam, rosewood species (not just D. oliveri) are considered to have declined by 50
to 60% in the last few decades and in Thailand rosewood trees now only remain in protected areas.
Therefore, it is suspected that the population of the species has experienced a decline of at least 80% in
the last three generations, and decline will continue at a similar rate into the future. Decline is
continuing due to limited capacity to police the illegal logging of the species due to corruption and
expense. There is also continuing decline due to lowland forest loss. The species is therefore assessed as
Critically Endangered.
Geographic Range
Range Description:
This species is native to Laos PDR, Myanmar, Cambodia, Thailand and Viet Nam. The species is
widespread in Cambodia, Laos PDR and Myanmar. In Thailand the species is found in the Northeast of
the country (Winfield 2016). A recent quantitative study based on species distribution modeling
estimated the species’ potential natural range at 997,383 km2 (Gaisberger et al. 2022).
Using herbarium records, field surveys and observations it is calculated that the species has an extent of
occurrence of 1,489,222 km2.
Country Occurrence:
Native, Extant (resident): Cambodia; Lao People's Democratic Republic; Myanmar; Thailand; Viet Nam
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Population
Currently this species is the main target for rosewood trade in Southeast Asia (CoP17 inf 79. 2017).
Therefore, this species experiences continuing population decline due to demand for rosewood timber
on the international timber market. A major consumer of rosewood timber is China and there has been
a boom in rosewood consumption in the country due to a growing wealth and a consequent demand for
traditional Ming and Qing Dynasty style furniture made from hongmu or rosewood timber (Treanor
2015). Dalbergia oliveri is listed as an official hongmu species hence it is under significant pressure in
the wild from timber harvest. In general, global hongmu resources are considered by Treanor (2015) 'to
be increasingly under threat from extinction'. Specifically to this species, a 2016a EIA) report stated that
'the commercial extinction of Burmese Rosewood is imminent'. The species has considerable value at all
stages of the supply chain encouraging exploitation and is broadly considered to be one of the most
expensive timber species in the world (CoP16 Prop. 60 2013). The majority of rosewood trade into China
(at least 50%) since the year 2000, is from D. oliveri range states (CoP17 inf 79 2015, EIA 2016a),
therefore there has been high pressure on rosewood tree stocks in this region. Dalbergia oliveri alone
contributes to one third of all rosewood trade in to China (CoP17 inf 79 2016). However, considering the
popularity of this species in trade over the last two decades, there is a paucity of population information
available for the species. Also often population and trade data is not species specific and recorded at the
generic or trade name level due to difficulty in distinguishing Dalbergia species at the point of trade.
In general across the range of the species the population is in decline due to overexploitation for timber
and also due to conversion of lowland habitat to agriculture and settlement space. This rate of decline
has increased in the last decade, as there has been a shift in demand from the desirable and now
increasingly rare species of Dalberia cochinchinensis (common name Siamese Rosewood) to Dalbergia
oliveri (EIA 2016a). This has occurred due to the continuing high demand for hongmu, additional
protective conservation measures targeted at D. cochinchinensis and the declining stocks of other
hongmu producing species across the globe, leaving D. oliveri under high pressure in the wild. This has
slowed down the population decline, but mature trees are still taken from inside and outside of
protected areas (EIA 2014) where they are found and there are continued pressures from human
development within the species' range states.
Like other species of Dalbergia this species is slow growing (CTSP 2004). Seed production is generally
sufficient but can vary widely between individuals and subpopulations (CTSP 2004), natural
regeneration is limited (Aerts et al. 2009) and seedlings grow slowly compared to D. cochinchinesis (I.
Theilade and T. So, pers. comm.) so very few trees reach maturity (Winfield et al. 2016). These attributes
require the species to have a long harvest (CoP16 Prop60 2013), rotation cycle and selective, sustainable
logging methodology in place to enable regeneration. However, this has not occurred for the species
and now regeneration is only occasionally observed in the wild (Winfield et al. 2016). Seed production
varies between individuals, and the trees do not necessarily bear seed every year. The species is able of
coppice regeneration from stumps and clonal reproduction from root suckers (Hartvig et al. 2018, So et
al. 2010), and seed regeneration and shoots from root suckers may be difficult to distinguish. This raises
additional concern to the population status of the species in the future and ability to recover from
historical logging. The species exhibit high levels of genetic diversity (Hartvig et al. 2018), but in some
subpopulations level of clonality can be high (Hartvig et al. 2018) and thus the effective population size
can be smaller than expected from number of individuals observed in natural subpopulations. Levels of
genetic diversity vary considerably across the range of the species, most diverse subpopulations are
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found in central Cambodia and least diverse in Southeast Cambodia and Viet Nam and a high levels of
genetic differentiation across the distribution area indicates somewhat limited level of gene flow among
regions (Hartvig et al. 2018). There are currently no signs of inbreeding in the species (Hartvig et al.
2018).
In Cambodia the species is widespread, however, subpopulations are small and dispersed (Hartvig et al.
2018). It is found in Koh Kong, Kampong Speu, Kampong Chhnang, Pursat,Preah Vihear, Mondul Kiri,
Ratanak Kiri, Stoeng Treng, Kratie, Battambang and Kampong Thom provinces. Important sites include
the Cardamom mountains, Keo Seima Protection Forest and Tbeng Meanchey in Preah Vihear, but all
are subject to illegal logging. The species experiences high local loss and very few trees that can be used
as seed sources remain present (Winfield et al. 2015). This has been caused due to overexploitation for
timber despite an export ban on round logs, established in 2002, and a ban of rosewood harvest
declared in 2013 (Treanor 2015, EIA 2016b). The species is still at risk in the country as these policies
lack enforcement capacity (Treanor 2015) and due to corruption. Between 2013 and 2014, the extent of
hongmu export has increased by 150% (Global Witness 2015). The expansion of human settlement and
agricultural development is also a major threat to the species in Cambodia. This is mostly done through
the over provision of Economic Land Concessions (ELC), which are used to clear forested land for
agricultural development (Treanor 2015). However, permits that allow too much land to be cleared are
often offered and they have historically been given to foreign investors and timber companies (Global
Witness 2015). They are also given for areas with a high rosewood density contributing further to the
species decline. The use of ELC permits has caused the loss of at least 20% of Cambodian primary forest
(data from 2010) (Treanor 2015), which will have had a negative impact on the species.
There is limited population information for this species in Laos PDR. Illegal logging has been observed
from subpopulations in national parks (Hartvig, pers obs). Field surveys by the National Agriculture and
Forestry Research Institute (NAFRI) in 2021-2022 in the provinces of Bolirkhamsay, Khammouan,
Savannaketh, Salavan, Champasak and Attapue found very few large trees across all forest classes. Trees
remain mainly on farmlands and are small to medium-sized. Alongside Cambodia, Lao PDR is one of the
main contributors of rosewood to China and between 2013 and 2014 exports of Rosewood (D.
cochinchinensis and D. oliveri) from these two countries increased by 150% (Global Witness 2015). This
suggests significant demand for Burmese rosewood from Laos PDR and significant pressure and loss of
the subpopulation here.
In general, in Viet Nam rosewood stock is suspected to have declined by 50 to 60% in the last five to ten
years (CoP16 Prop. 60 2013). In the past 60 years the species has been mostly lost from Tai Phu Forest,
where it was once the dominant species (Winfield et al. 2016) and additionally across the country the
species is considered to be becoming locally extinct (Winfield et al. 2016). Viet Nam acts as the main
transit pathway for rosewood timber to China, and mostly registers imports of 'Rosewood' not exports
(UNEP - WCMC 2018). There is a high occurrence of trafficking of timber across the border between
Cambodia and Viet Nam as reported by EIA in 2017 and 2018, with Cambodian logs being 'legalised'
upon entry over the border at Viet Nam. Logging was encouraged by quotas and occurred in protected
areas in 2016-17 (EIA 2017) but this system has since changed (in 2018 - EIA 2018) but there is still high
quantities of Cambodian timber (and likely D. oliveri) being taken across the border to Viet Nam in
complete disregard for Cambodian timber ban (EIA 2018).
In Thailand the species is under similar pressures across it's range. It is likely that the species exists in
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protected areas alongside, Dalbergia cochinchinensis. Siamese Rosewood in National Parks is still at risk
in Thailand, due to the illegal timber trade, timber smuggling and poaching (Arnold 2013, Stokes 2017,
Solomon and Paddock 2019). As D. oliveri grows in similar habitats to D. cochinchinensis and is found
alongside this species it is also likely that D. oliveri in Thailand is at risk of poaching from these areas,
although never explicitly stated. Further information on D. oliveri standing stock in Thailand should be
collected (as has been done for D. cochinchinensis) to provide further information on the threat to the
species in the country.
In 2014, a Myanmar Forestry document accounted for over 2 million trees of D. oliveri in the state of
Sagaing, just under 1 million in the state of Shan and all other states having less than 250,000 individuals
(Kyaw et al. 2014). This accounts for 1,203,600 m3, 354,000 m3 and 141,600 – 212,400 m3 timber
respectively (EIA 2014). Myanmar is one of China's main suppliers of hongmu timber (D. oliveria and
Pterocarpus macrocarpus) before the CITES listing of Dalbergia species and post this international policy
implementation. Between 2000 and 2013, 624,000 m3 of rosewood (D. oliveri and P. macrocarpus) was
traded, with the majority of the trade occurring in 2013 (EIA 2014). In 2013 at total of 237,000 m3 of
rosewood was exported to China, triple the volume traded in 2012 and six times the volume traded in
2010 (EIA 2014). This shows the huge and continuously increasing demand for rosewood out of
Myanmar. There are not figures post 2013. There has been an increase in the seized volume of timber in
transit from from Myanmar to China. In the 2014 EIA report 'Myanmar's Rosewood Crisis' they predict
that with the current rate of extraction of rosewood (D. oliveri and P. macrocarpus) the species could
become extinct from the country in the next 13 years, but if exploitation were to carry on exponentially
increasing rosewood (D. oliveri and P. macrocarpus) would become extinct in the next three years i.e.
before 2020 (EIA 2014). Current status of the species in Myanmar is not available, however it is obvious
that the species has experienced a high rate of population decline and the species is close to if not
extinct from the country.
Across the range of the species (except in Thailand) this species remains exploited for timber despite
various logging bans and a depleted population size. The species is subject to illegal logging and
harvesting the impact of which is compounded by the natural biology of the species to be slow growing.
Demand for rosewood timber continues to be high and pressure on D. oliveri to meet this demand will
also remain. Although more recent information is not available this is highlighted by an increase in
export of rosewood from Laos and Cambodia by 150% in 2013-2014 (Global Witness 2015). Therefore, it
is suspected that across all range states the population will have experienced decline of at least 80% in a
single generation. This rate of loss is suspected to continue into the next 100 years. If stumps are left,
there is potential for the species to coppice and regenerate allowing the population to recover but more
information is needed to confirm to what extent this is occurring in the wild.
Current Population Trend:  Decreasing
Habitat and Ecology (see Appendix for additional information)
Dalbergia oliveri is a large tree species. It can attain a height of over 20 m and a diameter at breast
height of over 60 cm (CTSP 2004). It is found in a variety of forest types including primary and secondary
forests, evergreen, semi-evergreen and semi-deciduous forests and is most often found along streams
(CTSP 2004). The species is mainly found in low densities. The species can be found growing in
association with Dalbergia cochinchinensis. The species can have a long regeneration time and
establishment in the wild is now rarely seen. It can also have high seed set but low rates of germination
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in natural subpopulations (Winfield 2014). It occurs in lowland areas from 100 to 800 m asl, and rarely
exceeds 1,000 m asl. Dalbergia oliveri is site specific and prefers fertile soils. The seedlings and juveniles
of the species are shade tolerant but past this phase the species is light demanding (Winfield 2014). The
species is assumed to be insect pollinated and Hartvig et al. 2018 considered it likely that the seed of
the species was dispersed by wind and water.
Systems:  Terrestrial
Use and Trade
This species produces a desirable rosewood timber. It is one of only 33 registered hongmu producing
species and due to a recent increasing wealth in the Chinese middle class, there is a demand for
hongmu products e.g. furniture in Ming and Quing dynasty design (EIA 2016a). Hongmu furniture is also
desirable in Viet Nam but China is the main market for these products. Dalbergia oliveri was not the
original target species for hongmu furniture production but as other hongmu producing timbers have
become rarer (e.g. D. odifera or D. cochinchinensis) there has been a shift in trade and demand for D.
oliveri (CoP17 Inf. 79 2015, EIA 2016a). The timber can also be used for interior decoration, fire art
articles and carving, musical instruments and some construction activities (Winfield et al. 2016). The
species is traded under the name Burmese Rosewood or Tamalan (Winfield et al. 2016).
Due to rarity of the species and other hongmu timber trees, logs and products of D. oliveri are
increasing in price. Winfield et al (2015) reported that from the Mekong Burmese Rosewood was worth
2,000 to 3,000 US dollars per m3 and from Myanmar one ton of Burmese Rosewood could fetch 7,000
US Dollars. Between 2000 and 2013, rosewood (D. oliveri and Pterocarpus macrocarpus) trade between
Myanmar and China totaled US$737 million (EIA 2014). In 2013, US$324 million of Rosewood (D. oliveri
and Pterocarpus macrocarpus) was traded between Myanmar and China which is three times the value
of the trade in 2012 (EIA 2014). In 2014, an additional US$52 million imports occurred between
Myanmar and China (EIA 2014).
Much of the current trade of D. oliveri is illegal due to the listing of the species on CITES in 2016. Logging
and trade of this precious species also goes against much national legislation with many nations having
logging bans in place since the early 2000's. There is limited capacity to enforce the regulations, and the
value of D. oliveri drives the continuing illegal trade of the species. Since the species has been listed on
CITES this requires import and export permits to show the species was legally and sustainably harvested,
however most range countries do not have non-detriment findings to support the continued harvest of
Dalbergia species (EIA 2016b). This means there is often forgery, bribery and corruption across the
supply chain of the species. Between 2017 and 2018, CITES trade database records 154,471 m3 of
imports of D. oliveri in range state countries. Much of this trade is between Laos and China, sometimes
with Viet Nam operating in the middle. It is also key to note that the value of exports (275,569 m3) is
larger than the registered value of imports. Most of the registered trade takes the form of sawn wood,
logs, or wood products (CITES trade database 2020).
The species has been used locally for crafts and furniture, as well as for stilts and construction of houses,
before broad international demand began (van Sam et al. 2004, CTSP 2004).
Threats (see Appendix for additional information)
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A quantitative vulnerability assessment indicates that 71% of the total modelled distribution range of
Dalbergia oliveri is under medium to very high threat from the combination of current threats
(overexploitation, habitat conversion, fire, and overgrazing) (Gaisberger et al. 2022).
This species is threatened by overexploitation for timber. This threat has emerged in the last two
decades (since 1990) and has caused a high decline in the global population of the species. There is high
demand for the hongmu timber this tree produces, due to a growing Chinese wealth (CoP17 Inf. 79
2015, Winfield et al. 2016). Due to this there is a rife illegal trade of Dalbergia oliveri and other hongmu
producing timber trees from Southeast Asia. The threat to the species has recently increased due to the
global, conservation protection of D. cochinchinensis and the growing rarity of other hongmu producing
timber species in the wild (CoP17 Inf. 79 2015). This has caused a shift in trade to D. oliveri, putting
pressure on an already depleted population (CoP17 Inf. 79 2015). 
In the range states of D. oliveri, there is national level protection often banning the logging of the
species and the exportation of it's round logs (Winfield et al. 2016). There is also international
legislation, the listing of the species on CITES Appendix II, to limit the import and export of the species.
However there is often poor capacity to enforce these policies and loop holes exist which enable the
trade of D. oliveri products (EIA 2016b). Also protective policies are often flouted, due to the value
earned from rosewood timber on unofficial markets which drives people into the continual illegal
exploitation of the species. There is also corruption and bribery at all stages of the supply chain (Arnold
2013, Stokes 2017, Solomon and Paddock 2019). Due to these activities species can more easily be
removed from protected areas and there is forgery of import and export permits (Global Witness 2015).
There is also poverty in many places where the species is found, and timber barons and crime syndicates
can often take advantage of this enabling the continuation of illegal activities and limiting the success of
conservation (Global Witness 2015). Some of the largest remaining populations of the species, ranging
from 70 to a few hundred individuals, are found in Community Forests (unpublished data, Institute of
Forest and Wildlife Research and Development, Cambodia).
The species is found in a region of the world with a high rate of habitat loss. Therefore deforestation is a
major threat to the species (Winfield et al. 2016, Gaisberger et al. 2022). This leads to land use change,
including the conversion of land to industrial agricultural (e.g. rubber plantations), human settlements,
hydroelectric power and other anthropocentric activities (Winfield et al. 2016). In Cambodia habitat loss
is a particular threat. This is mostly driven by the over delivery of economic land concessions (ELC's)
since the 1990's (Treanor 2015). This encouraged forests to be developed for human use, however the
quota of annual permits were often exceeded, permits were sold to foreign investors and the upper
boundary of land in a concession was also exceeded. It is also suggested that ELC's were unfairly granted
to areas with known rosewood subpopulations acting as a method to legalise the logging of these trees
(Global Witness 2015).
The species is also biologically predisposed to threat from logging and deforestation activities. This is
due to the long life cycle of the species, often requiring multiple decade to reach maturity and become
of harvestable diameter. Although some seedlings and seed set were witnessed in the wild (Treanor
2015, Winfield et al. 2016), regeneration to juvenile and mature trees is even more limited. Loss of
habitat limits the area in which the species can regenerate, logging activities make an inhospitable
environment for regeneration and cutting of mature trees reduce the possibility of seed set and cross
pollination. These factors all contribute to the future decline of the species and may be further
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exacerbated by climate change. In fact, a quantitative vulnerability assessment indicates that 13% of the
total modelled distribution range of D. oliveri is under medium to very high threat from climate change
by 2055 (Gaisberger et al., 2022).
Conservation Actions (see Appendix for additional information)
There are country level conservation practises and policy in place for the species which are upheld to
varying degrees.
• In Cambodia, it has been illegal to harvest rare tree species since 2002, which includes D. oliveri (EIA
2012). There has also been a been a ban on the processing, use and export of the species since 2013
however there is still known illegal trade routes for the species in the country (Winfield et al. 2016). 
• in 2008 Lao PDR banned the logging of the species and in 2011 banned the export of the species. Also
under 2007 Forestry Law efforts should be made to enrich non-timber products from forest trees, this
includes surveying and planning conservation for threatened species (Winfield et al. 2016).
• In Thailand the species is a specifically restricted timber and since 1989 there has been a logging ban
of Natural Forest Specimens (Winfield et al. 2016). In Thailand the species remains present in protected
areas (CoP16 Prop 60 2013).
• In Viet Nam, use of the species for scientific purposes only (including breeding and artificial
propagation) and commercial harvesting of the species was banned in 2014 (EIA 2012). The country
passed an original logging ban in 1992 which was expanded in 2006 to include logs and sawn wood from
natural forests, excluding plantations. The country has also ratified CITES and initialed a EU FLEGHT VPA
(EIA 2018), but despite this between 2016-17 there were quotas to encourage timber trade across the
border between Viet Nam and Cambodia with protected areas targeted for the harvest of such timber
(EIA 2017). EIA 2017, also found that records of timber imports into Viet Nam are much lower than
those from countries exporting to Viet Nam, therefore more work needs to be done to improve
transparency and discourage illegal logging activities in Viet Nam.
• In Myanmar, the species is a 'reserved' tree which means explicit permission from the Ministry of
Environmental Conservation and Forestry (MOECAF) is needed to harvest this species (Kyaw 2014).
The species is on CITES Appendix II along with all other species of Dalbergia (since 2016). This requires
declaration at import and export of trade in Dalbergia oliveri for records and also correct permits to be
held by importers and exporters which acts as limit to trade. However, there is still illegal trade of the
species with loop holes and bribery across the supply chain. There is also difficulty in identifying some
species of Dalbergia at the point of export due to similarities in the heartwood of the genus, therefore
some individuals may be misdeclared as a less threatened species. It is due to similar activities that
often National legislation to protect the species is difficult to implement. 
The species is assessed as Endangered in the Vietnam Red Data Book for Plants (2007). The species was
also assessed as Endangered on the IUCN Red List in 1998 (Nghia 1998). The species is found in some
protected areas, however, the adequacy of these sites is limited by funds and ability to police them. It is
still known that individuals of D. oliveri are removed from protected areas. More successful
opportunities for enforcement should occur alongside the expansion of designated protected areas
specifically targeted to the protection of Siamese Rosewood and D.oliveri.
A recent quantitative study based on species distribution modelling estimated that populations in the
following ecoregions are particularly underrepresented in protected area networks: Irrawaddy dry
forests, Myanmar coastal rainforests, Northern Indochina subtropical forests, and Northern Khorat
Plateau moist deciduous forests (Gaisberger et al. 2022). These sites should be prioritized for in situ
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conservation.
In general more information on the remaining localities of the species needs to be collected alongside
information on population size and regeneration potential. Viable ex situ collections should be
developed as well as effective in situ conservation activities. While in situ conservation is desirable, the
high level of threat from illegal logging and the challenges of enforcing protection laws, as described
above, means that ex situ protection should also be given high priority. Ex situ conservation should be
based on germplasm material from representative subpopulations across the distribution area in order
to conserve a broad range of the genetic variation in the species, which reportedly show high degree of
differentiation and potential local adaptation (Hartvig 2018). The species already exists in a few botanic
garden collections (BGCI 2020), but more collections need to be made. Botanic gardens need to support
seed collection, propagation and establishment of plantations for this species.
As part of a regional project “Conserving Rosewood Genetic Resources for Resilient Livelihoods in
Greater Mekong” (UK Darwin Initiative in 2018-2022), two new in situ reserves and three new ex situ
reserves were established for D. oliveri. The in situ reserves are in Lao PDR (established by the National
Agriculture and Forestry Research Institute, NAFRI) and Viet Nam (Vietnamese Academy of Agricultural
Sciences). The ex situ reserves are in Lao PDR, Vietnam and Cambodia (Institute for Forest and Wildlife
Research and Development). A small grafted seed orchard was also established by a farmer for seed
production in Pursat province, Cambodia,  in 2021, with technical and financial support from the same
project.
All national and international policy should remain in place and be further enforced and enhanced to
reduce the complete extinction of the species. This should be hinged on the support of the international
conservation community.
Credits
Assessor(s): Barstow, M., Boshier, D., Bountithiponh, C., Changtragoon, S., Gaisberger, H.,
Hartvig, I., Hung, H., Jalonen, R., Kanchanarak, T., Mackay, J., Ping, H.,
Thammavong, B., Theilade, I., Tran, T., Win, P. & Zheng, Y.
Reviewer(s): Oldfield, S. & Souladeth, P.
© The IUCN Red List of Threatened Species: Dalbergia oliveri – published in 2022. 9
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Citation
Barstow, M., Boshier, D., Bountithiponh, C., Changtragoon, S., Gaisberger, H., Hartvig, I., Hung, H.,
Jalonen, R., Kanchanarak, T., Mackay, J., Ping, H., Thammavong, B., Theilade, I., Tran, T., Win, P. & Zheng,
Y. 2022. Dalbergia oliveri. The IUCN Red List of Threatened Species 2022: e.T215341339A2813403.
https://dx.doi.org/10.2305/IUCN.UK.2022-1.RLTS.T215341339A2813403.en
Disclaimer
To make use of this information, please check the Terms of Use.
External Resources
For Supplementary Material, and for Images and External Links to Additional Information, please see the
Red List website.
© The IUCN Red List of Threatened Species: Dalbergia oliveri – published in 2022. 11
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Appendix
Habitats
(http://www.iucnredlist.org/technical-documents/classification-schemes)
Major
Habitat Season Suitability
Importance?
1. Forest -> 1.6. Forest - Subtropical/Tropical Moist Lowland - Suitable -
Plant Growth Forms
(http://www.iucnredlist.org/technical-documents/classification-schemes)
Plant Growth Form
TL. Tree - large
Use and Trade
(http://www.iucnredlist.org/technical-documents/classification-schemes)
End Use Local National International
9. Construction or structural materials No Yes Yes
11. Other household goods No Yes Yes
12. Handicrafts, jewellery, etc. No Yes Yes
Threats
(http://www.iucnredlist.org/technical-documents/classification-schemes)
Threat Timing Scope Severity Impact Score
1. Residential & commercial development -> 1.1. Ongoing Unknown Rapid declines Unknown
Housing & urban areas
Stresses: 1. Ecosystem stresses -> 1.1. Ecosystem conversion
1. Ecosystem stresses -> 1.2. Ecosystem degradation
2. Species Stresses -> 2.1. Species mortality
2. Species Stresses -> 2.2. Species disturbance
2. Agriculture & aquaculture -> 2.1. Annual & Ongoing Unknown Rapid declines Unknown
perennial non-timber crops -> 2.1.3. Agro-industry
farming
Stresses: 1. Ecosystem stresses -> 1.1. Ecosystem conversion
1. Ecosystem stresses -> 1.2. Ecosystem degradation
2. Species Stresses -> 2.1. Species mortality
2. Species Stresses -> 2.2. Species disturbance
2. Agriculture & aquaculture -> 2.2. Wood & pulp Ongoing Unknown Rapid declines Unknown
plantations -> 2.2.2. Agro-industry plantations
Stresses: 1. Ecosystem stresses -> 1.1. Ecosystem conversion
© The IUCN Red List of Threatened Species: Dalbergia oliveri – published in 2022. 12
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1. Ecosystem stresses -> 1.2. Ecosystem degradation
2. Species Stresses -> 2.1. Species mortality
2. Species Stresses -> 2.2. Species disturbance
4. Transportation & service corridors -> 4.1. Roads & Ongoing Unknown Unknown Unknown
railroads
Stresses: 1. Ecosystem stresses -> 1.1. Ecosystem conversion
1. Ecosystem stresses -> 1.2. Ecosystem degradation
2. Species Stresses -> 2.1. Species mortality
2. Species Stresses -> 2.2. Species disturbance
5. Biological resource use -> 5.3. Logging & wood Ongoing Whole (>90%) Very rapid High impact: 9
harvesting -> 5.3.2. Intentional use: (large scale) declines
[harvest]
Stresses: 1. Ecosystem stresses -> 1.1. Ecosystem conversion
1. Ecosystem stresses -> 1.2. Ecosystem degradation
2. Species Stresses -> 2.1. Species mortality
2. Species Stresses -> 2.2. Species disturbance
Conservation Actions Needed
(http://www.iucnredlist.org/technical-documents/classification-schemes)
Conservation Action Needed
1. Land/water protection -> 1.1. Site/area protection
1. Land/water protection -> 1.2. Resource & habitat protection
3. Species management -> 3.2. Species recovery
5. Law & policy -> 5.2. Policies and regulations
5. Law & policy -> 5.4. Compliance and enforcement -> 5.4.1. International level
5. Law & policy -> 5.4. Compliance and enforcement -> 5.4.2. National level
5. Law & policy -> 5.4. Compliance and enforcement -> 5.4.3. Sub-national level
6. Livelihood, economic & other incentives -> 6.2. Substitution
6. Livelihood, economic & other incentives -> 6.3. Market forces
6. Livelihood, economic & other incentives -> 6.4. Conservation payments
Research Needed
(http://www.iucnredlist.org/technical-documents/classification-schemes)
Research Needed
1. Research -> 1.2. Population size, distribution & trends
1. Research -> 1.4. Harvest, use & livelihoods
2. Conservation Planning -> 2.1. Species Action/Recovery Plan
2. Conservation Planning -> 2.3. Harvest & Trade Management Plan
© The IUCN Red List of Threatened Species: Dalbergia oliveri – published in 2022. 13
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Additional Data Fields
Distribution
Estimated extent of occurrence (EOO) (km²): 1489222
Habitats and Ecology
Generation Length (years): 60-100
© The IUCN Red List of Threatened Species: Dalbergia oliveri – published in 2022. 14
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The IUCN Red List of Threatened Species™
ISSN 2307-8235 (online)
IUCN 2022: T215341339A2813403
Scope(s): Global
Language: English
The IUCN Red List Partnership
The IUCN Red List of Threatened Species™ is produced and managed by the IUCN Global Species
Programme, the IUCN Species Survival Commission (SSC) and The IUCN Red List Partnership.
The IUCN Red List Partners are: ABQ BioPark; Arizona State University; BirdLife International; Botanic
Gardens Conservation International; Conservation International; Missouri Botanical Garden;
NatureServe; Re:wild; Royal Botanic Gardens, Kew; Sapienza University of Rome; Texas A&M University;
and Zoological Society of London.
THE IUCN RED LIST OF THREATENED SPECIES™
© The IUCN Red List of Threatened Species: Dalbergia oliveri – published in 2022. 15
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