Comparing and contrasting threat assessments of plant species at the global and sub-global level
Evidence-based assessments of extinction risk are established tools used to inform the conservation of plant species, and form the basis of key targets within the framework of the Global Strategy for Plant Conservation (GSPC). An overall picture of plants threat assessments is challenging due to the use of a variety of methodologies and range in scope from global to subnational. In this study, we quantify the state of progress in assessing the extinction risk of all land plants, determine the key geographic and taxonomic gaps with respect to our understanding of plant extinction risk, and evaluate the impact of different sources and methodologies on the utility of plant assessments. To this end, we have analyzed a cleaned dataset compiled from IUCN Red List of Threatened Species and Regional Red Lists. We reveal that there are assessments available for 89,810 distinct species or 25% of all accepted land plant species. However unlike with other major organismal lineages the bulk of the plant species assessments are derived from Regional Red Lists, and not the Global IUCN Red List. We demonstrate that this bias towards regional assessments results in distinct taxonomic and geographic strengths and weaknesses, and we identify substantial taxonomic and geographic gaps in the assessment coverage. With species that have been assessed in common at both global and regional levels, we explore the implications of combining threat assessments from different sources. We find that half of global and regional assessments do not agree on the exact category of extinction risk for a species. Regional assessments assign a higher risk of extinction; or underestimate extinction risk with almost equal frequency. We conclude with recommended interventions, but support the suggestion that all threat assessments should be pooled to provide more data and broaden the scope of threat assessments for monitoring progress towards GSPC targets.
KeywordsIUCN Red List Regional Red Lists Biodiversity Threatened species Convention on Biological Diversity GSPC
At the tenth Conference of the Parties to the Convention on Biological Diversity (CBD) it was widely accepted that the proposed 2010 Biodiversity target to significantly reduce the rate of biodiversity loss had not been met (Balmford et al. 2005; Walpole et al. 2009; Butchart et al. 2010; Brummitt et al. 2015). The Parties to the Convention responded by declaring a Decade of Biodiversity, and Decision X/2 in particular which sets out 20 new biodiversity targets (Tittensor et al. 2014). In response to the CBD, a plant-specific program called the Global Strategy for Plant Conservation (GSPC) (Wyse Jackson and Kennedy 2009) set sixteen targets for the conservation of plant species by the year 2020 (Paton and Lughadha 2011). Of these sixteen targets, three GSPC targets make specific reference to threatened plant species.
GSPC Target 2 calls for assessment of the threat status of all known plant species, as far as possible, to guide conservation action. GSPC Target 7 calls for at least 75% of known threatened plant species to be conserved in situ. GSPC Target 8 requires that at least 75% of threatened plant species are held in ex situ collections, preferably in the country of origin, with at least 20% available for recovery and restoration programs (Paton and Lughadha 2011). Clearly gains towards GSPC Target 2 are required before progress towards GSPC Target 7 and GSPC Target 8 can be meaningfully measured and monitored.
In addition to the internationally focused IUCN-RL, there is a wide range of different types of lists for threatened plant species that focus on assessments on a sub-global scale, termed Regional Red Lists or RRL, including: sub-national assessments (Chua et al. 2010; Cortini Pedrotti and Aleffi 2011; Ah-Peng et al. 2012); national assessments (Dines et al. 2005; Natcheva et al. 2006; Tefnu and Goia 2012, and many others listed at http://www.nationalredlist.org/t); supra-national but sub-global assessments (Eastwood et al. 2009; Bilz et al. 2011); assessments of particular ecological habitats (Witkowski et al. 2003; González-Espinosa et al. 2011) and; focused assessments on endemic species (León-Yánez et al. 2011). The extent of RRL has been rapidly increasing in response to the 2020 Biodiversity Targets (Rodriguez 2008; Zamin et al. 2010). RRL have five major functions: classifying the status of species at the level at which they are managed, evaluating locally threatened taxa, informing local conservation priorities, providing data for global assessments, and underpinning the legal protection of species (Rodriguez 2008; Zamin et al. 2010; Harris et al. 2012). RRL can commonly use the same or similar criteria as the IUCN-RL to assess extinction risk, but exact processes can vary and may not be consistent between different regions. Given their prevalence and importance for conservation, a number of studies have sought to compare RRL with IUCN-RL assessments in order to integrate RRL data into the global IUCN-RL (Rodriguez 2008; Moser et al. 2016), or to apply IUCN-RL assessments and criteria at regional levels (Gärdenfors et al. 2001). Typically, comparisons between RRL and IUCN-RL assessments will find differences in total number of evaluated taxa (Rodriguez 2008; Brito et al. 2010), in the geographic distribution of assessments (Brito et al. 2010; Zamin et al. 2010), in taxonomic sampling (Rodriguez 2008; Zamin et al. 2010), and in the level of threat status assigned to the same species (Brito et al. 2010; Morais et al. 2012; Harris et al. 2012; Helfman 2013). Differences in the level of threat status assigned can be further distinguished into three categories: (1) differences in abundance of individual species at different geographic scales such that a species will have fewer populations at sub-global scales leading to a higher category of assigned threat status at sub-global levels; (2) different scientific understanding resulting in differing species delineations, change in status over time, altered interpretation of the same data, and new or rediscovered species; (3) discrepancies that result from regional inequalities in the availability of financial resources and expertise, regional differences in the value attached to different units and types of biodiversity, politicization or bureaucracy associated with regional and global assessments, the application of different protocols, and the misapplication of common protocols (Collen et al. 2008; Kozlowski 2008; Brito et al. 2010; Zamin et al. 2010).
Clearly such differences between assessment lists can challenge the evaluation of GSPC targets, as articulated by a recent assessment of progress towards GSPC Target 2. A recent CBD report (CBD 2014) concluded that the proportion of plants assessed globally by IUCN has only reached approximately 6% of total plant diversity, but that many more plant species have been assessed at a regional level by a variety of different systems. It should be noted that many of these regional assessments will be of endemic species, and essentially constitute global assessments, and thus this figure of 6% was always likely to be an under-estimate of global assessments. Nonetheless, given the degree of fragmentation in threat assessments, the report identified that a global perspective on progress toward GSPC Target 2 is lacking, and made the following recommendations: (a) A working list of all available evidence-based conservation assessments for plants, to be maintained as an online resource and developed to include all plant species by 2020; (b) a published interim threatened species list, an output from (a) above, from which other GSPC targets can be measured by 2015; (c) An assessment of the threat status of a globally representative sample of plant species by 2015; and (d) Regional Red Lists developed or updated to assist in obtaining an overview of threat levels at a global level. Of these recommendations, (a) has been met (see https://www.bgci.org/threat_search.php), and (c) has been met through the IUCN Sampled Red List Index for Plants (SRLI) (Brummitt et al. 2015), which has extrapolated sampled species to non-assessed species and estimated that over 20% of plant species are threatened with extinction. However while the SRLI provides an important baseline measure, it does not provide the necessary foundation of data for GSPC Target 7 and 8 which deal with in situ and ex situ conservation.
In light of the recommendations from the 2010 progress report, we have analysed a cleaned dataset of evidence-based conservation assessments derived from both RRL and IUCN-RL sources ((a) above). We have then compared RRL and IUCN-RL derived data, and sought to evaluate the different datasets in light of the following questions: (a) what assessment sources are driving the accumulation of plant conservation assessments? (b) what proportion of land plant species have been subject to conservation assessment, and subsequently what percentage been found to be threatened? (c) to what extent do these assessments, and different sources of assessment, adequately and equitably represent the phylogenetic diversity of land plants, and their geographic distributions? d) to what extent do different sources affect the level of assigned threat status, and what are the implications for merging assessments? In answering these questions, we hope to assess whether we have information available that is sufficiently relevant, sensitive, and unbiased to establish a baseline against which subsequent progress towards GSPC targets can be measured, and to provide a better theoretical understanding of the data, to help identify interventions that may be needed, to increase the extent, quality and utility of evidence-based threat assessments of plants.
Data acquisition and management
We downloaded the full list of 20755 IUCN-RL assessed plant species corresponding to version 2015-4 from the IUCN-RL website on January 4th 2016. Conservation assessments for plant species were obtained from a pre-release version of BGCI ThreatSearch (https://www.bgci.org/threat_search.php, accessed: 2016-02-10). After acquisition in UTF8-encoded, plain text, CSV format, all of the data was tracked in a private git repository to ensure that all subsequent changes to the data were traceable and recorded (Ram 2013).
Data cleaning and normalisation
Higher-level classification annotation
We used the R package taxonlookup version 1.1.1 (Pennell et al. 2016) to annotate every included assessment species with current information on higher-classification of the taxon: Family, Order and Higher-level group. We also used taxonlookup to provide authoritative species counts per genus, family, order, and higher-level hierarchies based upon TPL accepted species names only (e.g. for Fig. 5). By using accepted names-only we recognise that the species totals will be a minimum estimate with many unresolved names on the TPL.
Geographic occurrence and endemicity
IUCN-RL provides data on known countries of occurrence of each species for all IUCN-RL assessed species, so we used this data as count data per country. For the set of species with only regional assessments, we used the country issuing the RRL assessment as the occurrence data for that species. We are aware that species nationally listed in one country may also occur in other countries—our data therefore serve as lower bounds on the true extent of country-level occurrence for nationally assessed species. Where a species is assessed by both the IUCN-RL and at least one RRL, we use the country-level occurrence data given by IUCN-RL. For analyses of combined IUCN-RL and RRL assessments we avoided double counting the same species in the same country (Figs. 7, 8). For the purpose of this study we define an endemic species as one that is present in only one country, with ‘countries’ defined as one of 249 territories recognized by the ISO 3166-1 standard. In order to assess country-endemicity of each IUCN-RL species (shown in Fig. 6b) we used official IUCN-RL data that provides country-level distribution information for each assessment taxon. Assessments of country-endemicity relied solely upon IUCN-RL data that provides country-level distribution information for each assessed taxon. There have been many significant critiques of uncritical use of online species occurrence data (Yesson et al. 2007; Beck et al. 2013, 2014; Mesibov 2013; Otegui et al. 2013), so we emphasize here that in this case we are only interested in accuracy to the country-level for the purpose of assessing endemicity. As opposed to species distribution modeling, a relatively coarse country-level analysis is justified here, since the implementation of CBD and GSPC are focused with respect to country boundaries.
Standardising conservation assessment classification
We standardised assessments where possible to IUCN 3.1 Categories and Criteria. Thus permitted assessment classifications were Data Deficient (DD), Least Concern (LC), Near Threatened (NT), Vulnerable (VU), Endangered (EN), Critically Endangered (CR), Regionally Extinct (RE), Extinct in the Wild (EW), and Extinct (EX). The vast majority of included RRL assessments use IUCN Criteria for assessing extinction risk. However, RRL assessments such as ‘Rare’ and ‘Very Rare’ were excluded from all analyses as the natural rarity of taxa is distinct to assessment of extinction risk. Furthermore, we decided that we could not confidently reconcile Mexican governmental extinction risk assessments (NOM-059-SEMARNAT-2010) with IUCN Criteria, so we do not include these in any analyses. For reconciling NatureServe (North American non-profit assessor) criteria we follow NatureServe’s own guidance (NatureServe 2012) and assign the following as equivalents: GX = EX, GXC = EW, GH = RE, G1 = CR or EN, G2 = VU, G3 = NT, G4 = LC, G5 = LC. For a species with a NatureServe G1 assessment we score the difference conservatively e.g. the difference between a G1 and VU assessment is counted as just 1 (treating G1 as EN) and the difference between a G1 and EX assessment is counted as just 3 (treating G1 as CR). For all relevant calculations we define ‘threatened’ as those species that have been assessed as either VU, EN or CR.
Ranked-comparisons between assessments
For the purpose of comparison between global IUCN-RL and RRL assessments for the same species, each assessment status was also given an equivalent numerical score: LC = 7, NT = 6, VU = 5, EN = 4, CR = 3, RE = 2, EW = 1, EX = 0. This is an arbitrarily-chosen scoring system (c.f. Moser et al. 2016) designed to promote clarity where there is a difference in threat assessment rank; we do not intend to symbolize that CR(3) is somehow twice as imperiled as NT(6), or that the difference between NT and VU is the same as the difference between EW and EX—these numbers are indications of relative rank only and the difference of 1 unit between them is purely to provide interpretive clarity. Our ‘Difference in Assessment’ for a species between IUCN-RL and RRL is the numerical score for the IUCN-RL assessment minus the numerical score for the RRL assessment. The Difference in Assessment is thus an integer bounded between − 7 and + 7. Species assessments of Data Deficient (DD) or Not Evaluated (NE), were discarded as incomparable. As an illustrative example we discuss the Difference in Assessment for the species Hopea shingkeng between IUCN-RL and China’s Higher Plants Red List (Zhao et al. 2014). The IUCN-RL has an assessment for this species listing it as Extinct (0) (Ashton 1998), whilst China’s Higher Plants Red List assesses it as Endangered (4). The Difference in Assessment for this species is thus considered to be − 4 (0 minus 4). We note that both of these assessments cannot simultaneously be true for this species; it is either extinct OR extant, these are mutually exclusive conditions, but without further information we cannot further determine which assessment is correct. Nevertheless it objectively highlights a significant conflict in assessment for a species. Differences in assessments were statistically modelled using the lm() function of the ‘stats’ R package (R Core Team 2017), to examine if there were any significant factors determining difference in assessment. Specifically we used stepwise multiple linear regression analysis inclusive of these variables: country endemism (scored as binary; endemic or not), temporal difference between assessment years, regional list source, taxonomic issues (scored as binary; yes or no), and country of origin.
Accumulation rates and redundancy
Phylogenetic coverage and taxonomic bias
The number of unique land plant species assessed by each data source, by higher-level groupings, after data cleaning and normalisation processes
Regional Red List assessed
Geographic comparisons between IUCN-RL and RRL coverage
Difference in like-for-like assessments between IUCN-RL and RRL
Modeling difference in assessment
We applied a variety of different models to the available data, with the aim of finding explanatory variables for the observed difference in assessment rank between IUCN-RL and RRL assessments of the same species. Our best model (BIC = 15,729.18) is a simple two-parameter linear model which tries to explains difference in assessment, as a function of: (1) the years elapsed between the assessment pairs, which range from the RRL assessment being 16 years newer [− 16] to the RRL assessment being 30 years older than the most recent global IUCN-RL assessment [+ 30], with a median of 0 and mean of − 0.22; and (2) the number of countries the species is known from, which ranges from 1 to 248, with a median of 1 and a mean of 6.6. These two parameters are both statistically significant factors (p < 0.0001) in this model, but together they only explain less than 6% of the observed difference in assessment (adjusted R2 value = 0.05519). We also ran a three parameter model, modeling taxonomic change as a possible factor in difference in assessment. If one or both of the assessments was published under what we now think of as a synonym, it is scored as ‘1’, if both assessments were published under the current accepted name then it was scored as ‘0’. Adding this third binary parameter into the model gave us a BIC of 15,734.38 which is larger (worse) than the BIC of the two-parameter model. It did not significantly add to the explanatory power of the two parameter model and synonymy as a factor itself was not significant (p = 0.0734).
Quantifying evidence-based threat assessments for plant species
We find that of the 350,699 accepted plant species (TPL 2013), 25.6% have been subject to some form of evidence-based threat assessments, of which 9.1% have been designated as threatened by either the IUCN-RL or a RRL. The accumulation of plant species assessments in recent years has been impressive, rising from 36,618 in 2003, to 89,810 species-level assessments in 2015 (Fig. 3). However, this accumulation has been largely driven by RRL, as evidenced by the fact that in 2003, 47% were IUCN-RL assessments, whereas in 2015, only 23% are IUCN-RL assessments (Fig. 3). Indeed, by 2015 there are five times more plant species assessed solely by RRL than solely by IUCN-RL, with 69,443 and 14,555 species respectively, equating to 19.8 and 4.2% of total plant species diversity respectively (Fig. 4). In other words, efforts to assess plant species by RRL have extended our knowledge to 69,443 additional species that have no current IUCN-RL assessments. Moreover, our results demonstrate a considerable proportion of non-overlap between both taxa assessed by the IUCN-RL and RRL (Fig. 3). From the 89,810 species-level assessments, only 5812 have been assessed in common by IUCN-RL and RRL (Fig. 4).
Plants are unarguably under-represented in the IUCN-RL 2015-4 data relative to vertebrates, as evidenced by the fact that only 6% of accepted plant species have had global IUCN-RL assessments. The extent of this under-representation is not a new finding, although our analyses suggest that the situation remains severe 5 years on from the GSPC report, which estimated 10% coverage of plant diversity by IUCN-RL criteria and protocols in 2010. Previous explanations for this under-representation have suggested that, whereas metazoan assessments have been a top-down global process led by specialist groups, global plant assessments have been bottom-up and organized primarily by countries that already have well-developed RRL for plant species (Zamin et al. 2010). Consistent with this explanation, our analyses show that the bulk of plant species assessments do indeed stem from RRL, where the greater attention to plant diversity may reflect the priorities of local conservation practitioners, policy makers and the public. Our analyses certainly support the contention that RRL have emerged as the major contributor to the threat assessment process within the plant kingdom. Furthermore, there is valuable complementarity between the RRL and IUCN-RL datasets, as only 6.4% of species have been assessed in common (Fig. 4), supporting in principle, the integration of these data sources to better assess GSPC targets.
Methodological challenges in normalising RRL and IUCN-RL data
Nonetheless as our methodology highlights, in practice, there are notable procedural challenges in normalizing RRL and the IUCN-RL, in order to compare the data sources, and with a view to their eventual integration. Ultimately, as discussed below, in order to normalize the datasets for comparison, 3.2% of all assessments were discarded in our analyses (Fig. 2). Of the initial 98,844 assessments of plant species, there were also problems arising from assessments based on inadequately described taxa, which resulted in 129 discarded assessments. Aside from ‘species novum’ taxa there were also assessments for nomina nuda such as ‘Rughidia milleri’ and ‘Oreofraga morrisiana’, neither of which have ever been published to our knowledge, or that of The Plant List (TPL 2013). Finally, changes in taxonomy since the time of assessment, together with on-going taxonomic uncertainty and taxonomic disagreement clearly affect a substantial number of published assessments. A total of 2131 assessments were discarded because, according to TPL, they were no longer considered to be a species-level taxon, or because they were considered to be synonymous with another assessed taxon. Again with the bulk of this discrepancy coming from the RRL, with 1837 examples of these. In total, issues with systematics caused us to discard 388 (1.8%) of IUCN-RL assessments, and 2834 (3.6%) of the published RRL assessments (Fig. 2). Evidently the degree of discrepancy found within RRL data sources, relative to TPL, appears to be considerably higher than the IUCN-RL, owing in part to the IUCN-RL usage of TPL since its release in 2010.
Gaps in taxonomic and phylogenetic coverage
Bias in taxonomic coverage across conservation assessments is a well-established phenomenon, and plants have previously been identified as under-represented in conservation science and policy. Our analyses reveal similar biases in coverage within assessments of plant species at the level of the four major groupings of land plants, angiosperms, gymnosperms, pteridophytes, and bryophytes. Considering all assessments, both RRL and IUCN, coverage per group is; 80,942 species or 26.6% of angiosperms, 988 species or 89.3% of gymnosperms, 3677 species or 34.4% of pteridophytes, and 4303 species or 12.2% of bryophytes. Although by raw count there are vastly more angiosperm assessments, in terms of percentage coverage, due to the high species diversity of angiosperms the overall percentage coverage of the group is low (26.6%) relative to gymnosperms and pteridophytes. The coverage of gymnosperms is exceptionally good, as there is an active group (Conifer Specialist Group) working on the conservation assessments of these taxa and there are relatively few species to assess. As might be expected, given smaller research communities and more limited pools of taxonomic expertise, the number of assessments for bryophytes is the lowest both as an absolute number and as a proportion.
Perhaps more instructive, is the comparison of the taxonomic coverage between the IUCN-RL and RRL data sets. The IUCN-RL has better coverage of gymnosperms, but much poorer coverage of angiosperms. Relative to RRL, IUCN-RL coverage of bryophyte species is exceptionally poor, where just 102/34,556 species (0.3%) of accepted bryophyte species have an IUCN-RL assessment. With over 4000 bryophyte assessments, the RRL are providing key coverage for the early diverging land plant lineages, in absence of a coherent international program. Although a predictable deficiency, the lack of coverage of bryophyte species fails to recognize that bryophytes form dominant communities across a significant fraction of the Earth’s surface. Bryophytes typically occur in tundra, boreal, and peatland ecosystems (Lindo and Gonzalez 2010), where they provide a habitat to a highly diverse microbiota (Kauserud et al. 2008), and play a central role in the detrital networks and nutrient cycling in these ecosystems (Turetsky 2003).
Higher numbers of assessments in RRL datasets versus IUCN-RL hold across lower taxonomic hierarchies. At the ordinal level, mean percentage coverage relative to all accepted species by RRL is 32.5% per order, whereas the IUCN-RL assessments cover an average of 14.9% of species per order (Fig. 5). Consistent with these mean values, the same data mapped across a consensus topology of the land plants in Fig. 5, show that RRL have more even and proportional sampling across the major orders of land plants. RRL species assessments equal or exceed the number of IUCN-RL species assessments for all but the Cycadales, Pinales, Gnetales, Magnoliales, Dilleniales, Canellales, Berberidopsidales, and Mettenusiales (Fig. 5). That the IUCN-RL assesses far more species in the order Magnoliales is due to active specialist groups focusing on their assessments, such as the publication of the Red List of Magnoliaceae (Rivers et al. 2015), evidence of the success of focused taxonomic intervention of global assessment in key groups.
Overall, the results clearly suggest that in terms of enriching taxonomic coverage, much could be gained from merging RRL and the IUCN-RL into one single pool of plant species threat assessments as suggested by Zamin et al. (2010). This has now been turned into reality in the publication by BGCI of a global database ThreatSearch (www.bgci.org/threat_search.php), which has assembled regional and global assessments of plants in a single portal.
As with taxonomic bias, the geographical bias in conservation activity, including biodiversity data collection and publication has been well documented (Reddy and Dávalos 2003; Boakes et al. 2010; Trimble and van Aarde 2012; Oliveira et al. 2016). In general, despite high species diversity, tropical areas are understudied and underrepresented in biodiversity data (Kier et al. 2005; Collen et al. 2008). Consistent with this observation, previous studies have highlighted similarly large gaps in evidence-based conservation assessments across all continents that transect the tropics: Africa, Asia, Australasia and South America (Collen et al. 2008; Zamin et al. 2010). The RRL for Ecuador (León-Yánez et al. 2011), Malaysia (Chua et al. 2010) and the Philippines (Fernando et al. 2008) are notable exceptions to this tropical deficit. Limited availability of financial resources, using Gross Domestic Product as an indicator, is also strongly correlated with limited biodiversity data, again contributing to gaps in conservation assessments across these same continents (Zamin et al. 2010). In addition, specifically with respect to RRL coverage, previous studies have identified substantial gaps in data from West Africa, Central Africa, Australasia, and the Caribbean (Zamin et al. 2010).
Our analyses of plant focused conservation assessments are consistent with these previous studies, as depicted cartographically, conservation assessment coverage does not correlate well with the natural geographic distribution of plant species diversity (Fig. 7). The average percentage of total plant biodiversity assessed across Africa (including the Middle East), Asia (including Oceania and the Pacific Islands), and South America is 13.3, 21.8, and 7.6% respectively, compared to Europe (including Central Asia) and North America (including the Caribbean and Central America) at 27.7 and 16.0% respectively (Fig. 7). However there are notable differences in the extent of geographic coverage between IUCN and RRL assessments of plant species, with IUCN having at least one species in 249/249 countries while the RRL cover 89/249 countries (Fig. 6). There are also clear differences in geographic focus. The RRL have a disproportionate bias towards assessments of plants in the USA and China, but are still notably absent from West Africa, Central Africa, and the Middle East (Fig. 6). The IUCN-RL thus often offers the only conservation assessments across large tracts of continent for which RRL are apparently absent (Fig. 6).
Clearly the globally operating IUCN-RL is providing key biodiversity data in areas where resources are limiting the production of regional red lists. Simply put, with respect to plant species assessments, IUCN-RL often usefully complements the geographic gaps in RRL coverage, and vice versa.
Threat assessment between and among RRL and IUCN-RL datasets
Taxonomic and geographic gaps can undermine the efficacy and utility of evidence-based conservation assessments for biological conservation. The absence of certain species from the assessment process also has the potential to lead species to extinction, and discrepancies between different sources can undermine the credibility of both global and regional red lists. Discrepancies are commonly ascribed to a number of causes, including: regional inequalities in the availability of financial resources and expertise, regional differences in the value attached to different units and types of biodiversity, politicization of bureaucracy associated with regional and global assessments, the application of different protocols, the misapplication of common protocols, taxonomic uncertainty and disagreement, and differences in abundance of individual species at different geographical scales (Collen et al. 2008; Kozlowski 2008; Brito et al. 2010; Zamin et al. 2010).
Taking the RRL and IUCN-RL dataset for plant species as a whole, there are clearly considerable differences in the proportion of species considered as imperiled: 59% of IUCN-RL assessed taxa are considered threatened compared with only 33% in digitally-available RRL assessments. We explicitly recognize that due to the biases operating within these compiled datasets, this estimate cannot be meaningfully compared with, or substituted for, the recent figures obtained by the relatively unbiased Sampled Red List Index for Plants, which estimates that more than 20% of plant species are threatened with extinction. It is likely that the IUCN-RL overestimates the overall extinction of species mainly because over many years most effort has been focused on assessing the species that scientists expect to be threatened, due both to the limited resources available for assessments and to a natural tendency to select species considered to be most in need of assessment.
The 4524 species that have been assessed by both IUCN-RL and RRL with adequate data (i.e. not data deficient), give us a unique window on the comparability of IUCN-RL and RRL assessments of plant species. We observe (Fig. 8a) that 49.1% of IUCN-RL and RRL threat assessments do not agree on the exact category of extinction risk that has been assigned. That discord is just as common as agreement between IUCN-RL and RRL assessments has been noted before in the context of fish (Helfman 2013), but not plants. We find that 15.7% (709) of our sample is composed of species that are not recognized as threatened (Least Concern or Near Threatened) by the IUCN-RL, yet considered threatened or extinct per RRL. In this regard our results differ strongly from that of Brito et al. (2010) who analysed just four RRL but across all taxa, not just plants. Brito et al. (2010) found that only 2% of species assessed in common were not considered threatened by IUCN-RL, but were considered threatened on an RRL. In the same analysis, Brito et al. (2010) estimated that 14% of plants were listed as globally threatened but not nationally threatened, whereas our analysis finds that 8.3% (377) of plant species are considered globally threatened by IUCN-RL, but not considered threatened by RRL assessment. But here we analyze results in a more fine-grained way than a simple binary comparison of threatened and non-threatened, and consequently expose a greater range of discord than revealed by Brito et al. (2010).
The overall level of agreement (0 difference in assessment rank) is particularly driven by agreement on assessment of species that are Least Concern; such assessments make-up 42% (962/2301) of all the agreement assessment pairs. A two-tailed Fisher’s exact test (p < 0.0001) demonstrates then when the IUCN-RL assessment is Least Concern, the RRL assessment has a significant association with this assessment. So, for Least Concern assessments, agreement between IUCN-RL and RRL assessments is significantly better than random. This is unsurprising—it is relatively easier to agree on species which are not at risk of extinction. But even hidden within the assignment of ‘Threatened’ statuses there is disagreement, namely that 19.3% or 873 of our assessment pairs disagree in terms of what exact category of threat is assigned to particular species e.g.VU versus EN, EN versus CR, or VU versus CR (similar to that shown by Rivers et al. 2014). Our data shows a positive skew towards RRL assigning a greater extinction risk to species, than the corresponding IUCN-RL assessment (Fig. 8a).
Generally this positive skew fits null expectation as, due to reasons of geographic scale, the most common explanation is that a species is much more likely to become regionally extinct than to become globally extinct. However there are two more troubling aspects to these analyses of level of agreement. Firstly, when just endemic species are considered, the overall pattern remains largely similar with a similar positive skew (Fig. 8e). More than half (1314/2623, 50.1%) of the endemics-only data present some form of assessment disagreement albeit typically only one rank of threat status up or down (Fig. 8e). Procedural factors and differences in assessment protocol may therefore be a major contributor, perhaps including a national bias towards overvaluing culturally important plants, political interference to elevate or reduce threat status, application of different assessment protocols, misapplication or alteration of IUCN protocols, and taxonomic disagreement. Second, although the overall skew is towards the positive, there are a large number of disagreements, which fall to the negative i.e. the RRL assign a lower risk of extinction to species than the corresponding IUCN-RL assessment. But it is logically impossible for a species to be Near Threatened or Vulnerable nationally and Extinct globally. These ‘negative’ tail disagreements are the more dangerous in terms of species conservation, because most species conservation efforts are delivered locally or regionally, and so an underestimation of extinction risk by RRL may undermine these conservation efforts. However here, our comparisons and analyses provide a useful tool for targeting interventions, as a way of prioritizing species re-evaluation for which one of the assessments, either Regional or IUCN-RL, might be in need of updating an accurate.
Observed differences in assessment have different causes
Likely to form the bulk of the differences between IUCN-RL and RRL is the simple fact that regional extinction is inherently more likely than global extinction. In the case of the 3 species which have the maximal (7) difference in assessment possible, it is unsurprising to find that the countries lie at the extremities of the species range (Brito et al. 2010). For assessments of Cyperus glaber (1), Ranunculus ophioglossifolium (2), and Ulex europaeus (3) the IUCN-RL has them all as Least Concern, whilst at the regional level they have all been assessed as ‘Extinct’ (1) by a Croatian NL, (2) by an Israeli NL, and (3) by a Norwegian NL. For these species it is clear that they are geographically widespread species and the difference in assessment merely reflects regional extinction at the edge of the native species range, rather than global extinction.
Real change in extinction risk occurring in the time elapsed between two assessments. In our pool of data we have some assessment pairs in which one assessment may be published up to 30 years after the other assessment for the same species (incidentally in all three of these maximal instances the assessment stays the same [Least Concern] between the two assessments). In the intervening time between assessments it is conceivable that the extinction risk of a species may genuinely change rank and thus difference in assessment could be purely down to just time elapsed between assessments. The statistical modeling demonstrates that time elapsed is only weakly predictive of difference in assessment. To add a complication, time elapsed also increases the likelihood of the taxon circumscription being revised, so time elapsed is co-correlated and not independent of issues owing to taxonomic change. Examination of assessment pairs that are separated in publication date by 5 years of less (e.g. Fig. 8f), show a similar trend to the overall data (Fig. 8a).
Differences owing to changes in our understanding of the circumscription of taxa. In 1998, a global IUCN-RL assessment for Chrysophyllum claraense was published assessing it as Critically Endangered. The Plant List v1.1 treats Chrysophyllum claraense as a synonym of Chrysophyllum oliviforme What was assessed in 1998 under C. claraense by IUCN-RL is no longer considered a discrete separate taxon worthy of its own species-rank name. That taxon is considered a synonym of Chrysophyllum oliviforme and this species is regionally assessed as Least Concern by the Cuba Red List (Berazain Iturralde et al. 2005). As our analyses show, changes to the circumscription of taxa that affect conservation status are relatively rare (Fig. 8a, b). Most synonyms are orthographic or nomenclatural synonyms that do not change the circumscription of the taxon, unlike taxonomic synonyms which do change taxon circumscription (sensu Remsen 2016).
Possible local rediscoveries, reflected in local assessments, that have not yet filtered back to global assessment processes. There are a noticeably large number of taxa (830) for which the RRL assessment is much less threatened than the global IUCN-RL assessment. Of particular interest, four species, namely Adiantum lianxianense, Melicope haleakalae, Chrysophyllum januariense, and Ormosia howii have regional assessments that indicate they are extant and are either Near Threatened or Vulnerable. However, the IUCN-RL has assessed all four species as globally extinct—a difference of unarguable significance. Three of those local assessments are noticeably more recent that their IUCN-RL counterparts which suggests they may have been rediscovered in the wild after the IUCN-RL ‘Extinct’ assessments were made. However, for Melicope haleakalae the publication date of NatureServe’s ‘G2’ assessment and IUCN-RL’s ‘Extinct’ assessment is the same: 1998, suggesting a possible taxonomic error. We note that Melicope haleakalae is listed as a ‘Species of Concern’ but not one that is Extinct (Wood et al. 2016), which suggests that the IUCN-RL assessment is perhaps too pessimistic. These sorts of disagreements need urgent re-evaluation to ensure appropriate conservation action is taken.
We have found that RRL assessments are increasing at a rate much faster than global IUCN-RL assessments of plant species. The collective contribution of RRL is invaluable in terms of broadening the scope of threat assessments and providing much needed depth in certain taxonomic areas such as the bryophytes. The Regional and IUCN assessments are largely complementary in terms of taxonomic and geographic coverage, and there would be much to be gained by combining the work of IUCN-RL and RRL to support subsequent GSPC targets on the in situ and ex situ conservation of plants, which has now happened with the recent release of BGCI ThreatSearch (https://www.bgci.org/threat_search.php). However, comparisons of regional-level and global IUCN-RL assessments of the same species reveal interesting discrepancies in the exact level of extinction risk between assessments, something that could be usefully resolved in specific cases with further investigation. As expected, our data show that RRL tend to report higher risk of extinction relative to global assessments, but more concerning are the great many RRL assessments that report lower extinction risk for species than the global assessments Our analyses serve to highlight these instances and to direct specific efforts for re-assessment. In extreme cases this could lead to official ‘rediscovery’ of species that were previously considered extinct by global assessment groups, but found to be extant by regional assessments. These discrepancies that we highlight, together with the taxonomic and geographic gaps, should help guide focused intervention, ensuring both breadth and depth in the threat assessment coverage of all plant species.
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