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Research Article

A Gap Analysis Methodology for Collecting Crop Genepools: A Case Study with Phaseolus Beans

  • Julián Ramírez-Villegas mail,

    j.r.villegas@cgiar.org

    Affiliation: Decision and Policy Analysis Program, International Center for Tropical Agriculture (CIAT), Cali, Colombia

    X
  • Colin Khoury,

    Affiliation: Global Crop Diversity Trust, Rome, Italy

    X
  • Andy Jarvis,

    Affiliations: Decision and Policy Analysis Program, International Center for Tropical Agriculture (CIAT), Cali, Colombia, Adaptation to Progressive Climate Change, Challenge Program on Climate Change, Agriculture and Food Security (CCAFS), Copenhagen, Denmark, Bioversity International, Regional Office for the Americas, Cali, Colombia

    X
  • Daniel Gabriel Debouck,

    Affiliation: Genetic Resources Unit, International Center for Tropical Agriculture (CIAT), Cali, Colombia

    X
  • Luigi Guarino

    Affiliation: Global Crop Diversity Trust, Rome, Italy

    X
  • Published: October 20, 2010
  • DOI: 10.1371/journal.pone.0013497

Abstract

Background

The wild relatives of crops represent a major source of valuable traits for crop improvement. These resources are threatened by habitat destruction, land use changes, and other factors, requiring their urgent collection and long-term availability for research and breeding from ex situ collections. We propose a method to identify gaps in ex situ collections (i.e. gap analysis) of crop wild relatives as a means to guide efficient and effective collecting activities.

Methodology/Principal Findings

The methodology prioritizes among taxa based on a combination of sampling, geographic, and environmental gaps. We apply the gap analysis methodology to wild taxa of the Phaseolus genepool. Of 85 taxa, 48 (56.5%) are assigned high priority for collecting due to lack of, or under-representation, in genebanks, 17 taxa are given medium priority for collecting, 15 low priority, and 5 species are assessed as adequately represented in ex situ collections. Gap “hotspots”, representing priority target areas for collecting, are concentrated in central Mexico, although the narrow endemic nature of a suite of priority species adds a number of specific additional regions to spatial collecting priorities.

Conclusions/Significance

Results of the gap analysis method mostly align very well with expert opinion of gaps in ex situ collections, with only a few exceptions. A more detailed prioritization of taxa and geographic areas for collection can be achieved by including in the analysis predictive threat factors, such as climate change or habitat destruction, or by adding additional prioritization filters, such as the degree of relatedness to cultivated species (i.e. ease of use in crop breeding). Furthermore, results for multiple crop genepools may be overlaid, which would allow a global analysis of gaps in ex situ collections of the world's plant genetic resources.

Introduction

Crop wild relatives (CWR) are wild plant species sharing relatively recent common ancestry with cultivated plants. CWR typically possess wide diversity, much of it not found in the crop, and this diversity may be introgressed into the crop by plant breeders, with the ease of transfer of genes generally dependent on the degree of relatedness between the wild species and the domesticate [1], [2]. Wild relatives have provided to crops traits such as pest and disease resistance, tolerance to abiotic stresses, increased yield, male sterility, and quality, increasing the value and sustainability of banana, barley, beans, cassava, chickpea, lettuce, maize, oats, pearl millet, potatoes, rice, sugar cane, sunflower, tomato, and wheat production, among others. In the past 20 years, there has been a steady increase in the rate of release of cultivars containing genes from CWR, and their contribution should only increase as the development of molecular technologies makes identification and utilization of diverse germplasm more efficient [2][5].

Plant breeders obtain CWR material from genebanks. However, major gaps in the genetic diversity of important crop genepools remain to be filled in ex situ germplasm collections. These gaps are particularly evident for non-cereal crops (e.g. legumes, roots and tubers, vegetables), and for wild and weedy forms [6][8]. Maxted and Kell [7] estimated that 94% of European CWR species are completely missing from ex situ collections. At the same time, habitat destruction, invasive species, urbanization, and the shift from traditional to industrial agricultural practices, among other factors, continue to threaten PGR, and climate change is projected to impose further pressures on both wild and agricultural ecosystems [9][15].

Clearly, much collecting of CWR diversity is still required. Unfortunately international efforts in collecting plant genetic resources in general have been in decline in recent decades [16]. The recent coming into force of the International Treaty on Plant Genetic Resources for Food and Agriculture is, however, expected to provide impetus for the development of an integrated, effective, efficient, global approach to conserving PGR. The development of strategic planning approaches will be necessary to prioritize PGR for collecting as part of such a rational global system.

Gap analysis refers to a systematic method of analyzing the degree of conservation of taxa, in order to identify those locations, taxa, and particular traits (adaptations) un- or under- secured in conservation systems [17]. Nabhan [18] identified four ways by which gap analysis techniques may lead to better collecting and conservation: targeting localities where sets of species absent from existing collections can be obtained with least effort and cost; determining which areas are ‘under-collected’ or ‘over-collected’ for germplasm relative to the known distribution of a taxon; locating which regions have the greatest or most dissimilar species richness compared with other regions; and outlining the ecological amplitudes of each species so that a wider representation of the ecotypes or genetically adapted populations of each can be sampled.

Geographic Information Systems (GIS) technologies have enabled a better understanding of species distributions and of the representativeness of germplasm collections, and have contributed to conservation planning of wild species, CWR, and domesticates [17][28]. Pioneering the use of these tools in conservation, Jones et al. [25] successfully predicted the location of populations of wild common bean (Phaseolus vulgaris), based on climatic suitability. Significant developments have occurred in recent years in the application of GIS to PGR conservation planning, including the development and validation of various approaches to niche modeling, new analysis tools and extensions, and better access to geographic information, results and approaches [29].

We propose here a gap analysis method designed to inform planning of germplasm collecting for ex situ conservation, based upon available information resources, using GIS. The distributions of ex situ collections are compared to GIS-modeled taxon distributions based on both herbarium and genebank data. The gross total number of germplasm accessions, as well as the distribution (geographical and environmental) of those accessions, are compared against modeled distributions in order to identify gaps in ex situ conservation coverage. These results form the basis for a prioritization of taxa across the genepool for collecting, and the identification of the highest priority locations (i.e. diverse and under-represented areas) for the most efficient and effective collecting, in order to further enhance ex situ holdings. Our model genepool is Phaseolus.

The genus Phaseolus originated in the tropics and subtropics of the New World, and contains up to 81 species and 34 infraspecific taxa [2], [30][32], having undergone a series of revisions, notably in association with members of Vigna, which have included splitting some species into new genera (e.g. Strophostyles, Dysolobium, Macroptilium, Minkelersia and Alepidocalyx) [27]. The main centers of diversity for the genus are in wide Mesoamerica (from southern USA, Mexico, and Central America down to Panama), the northern Andean region (Colombia to northern Peru), and the central Andes (northern Peru, Bolivia to northwest Argentina). Of these, the Mesoamerican centre is the richest in species [30], [32][34].

Phaseolus has five domesticated species, each a result of an independent domestication process: P. vulgaris L.- common bean; P. lunatus L.- lima bean; P. coccineus L.- runner bean; P. acutifolius A. Gray - tepary bean; and P. dumosus Macfady - year bean. The genus has been cultivated for over 7000 years, and each of the cultivated species has distinct ecological adaptations [35]. Common bean is the world's most important legume for food production and security, and represents 50% of the grain legumes consumed worldwide, reaching primary importance in the staple diet of over 500 million people, especially for its protein content [31], [36]. Common bean is now grown on over 27 million hectares globally, producing over 20 million tons [37].

Diversity in Phaseolus in relation to the cultivated species is organized into genepools based on phylogenetic relationships [38], [39]. The primary genepool of cultivated species includes both cultivars and wild populations, hybrids of which are generally fully fertile with no major reproductive barriers. P. vulgaris also allows a measure of interspecific hybridization with species in its secondary genepool. P. lunatus and P. acutifolius appear less capable of gene exchange with related species [40].

Like many important food crops, cultivars of common bean have a narrow genetic base, attributable to the genetic bottleneck accompanying the domestication process, stringent quality requirements in the market, limited past use of exotic germplasm in breeding, and conservative breeding programs for the crop [2]. Interspecific and wide intraspecific crossing have been useful strategies for crop improvement, but given the still limited genetic base, more along these lines is needed. Useful alleles for many agronomic traits deficient in common bean cultivars, including resistance to storage insects, leafhoppers, ascochyta blight, common bacterial blight, white mold, bean common mosaic virus, rust, drought, and soil fertility problems, as well as early maturity, adaptation to higher latitudes, upright plant type, pod quality, and seed yield have been identified in wild common bean and species in the secondary and tertiary genepools, and utilized in breeding programs [2], [41][43]. Wild common bean has also contributed high protein digestibility [44] and nodulation [45] traits. Despite the increasing utilization of CWR in common bean breeding, Singh [2] estimated as much as 90% of the genetic variability available in the primary genepool and related species as under- or not utilized. Widening of genetic diversity in the other Phaseolus crop species may also prove important. The domestication of tepary bean involved a severe genetic bottleneck event, leading to a particularly low level of genetic diversity in the crop [46][48].

Close to 250 ex situ germplasm collections of Phaseolus, holding approximately 260,000 accessions, have been established worldwide [16]. The vast majority of these accessions are of common bean, with much smaller collections of the other cultivated species, and a small percentage of wild species. The largest collections of CWR of Phaseolus are held in the international collection managed by the Consultative Group on International Agricultural Research (CGIAR), with close to 2000 accessions [49], and in the United States National Genetic Resources Program, with close to 500 accessions) [50].

Methods

An eight-step gap analysis process is presented, which attempts to evaluate conservation deficiencies at three different levels: (1) taxonomic, (2) geographic and (3) environmental. The aim is to define the extent to which current genebank holdings represent total genetic diversity within a genepool. We apply the protocol to all the wild members of the genus Phaseolus.

Based upon the average of overall taxonomic, geographic, and environmental coverage factors, the method produces a table outlining the high, medium and low priority species for collecting. From this table, potential collecting areas for high priority species may be highlighted, and overlapping high priority regions for the collection of multiple taxa identified. In detail, the method is as follows:

1. Determination of target taxa, delineation of target area and harvesting of occurrence data:

This involves five steps:

  1. Identification of the target cultivated species.
  2. Taxonomical review of all CWR related to the cultivated species, and analysis of relatedness to the domesticated species using the concept established by Maxted et al. [51].
  3. Creation of a database containing as many records as possible both of genebank accessions and herbarium specimens, along with (when available) their respective passport data, specifically the names of the places of collection and coordinates (i.e. latitude and longitude). Samples listed as weedy or cultivated are not included in the database.
  4. Cross-check, verification, and correction of geographic references (coordinates) through thorough review of data and use of verification tools such as BioGeomancer (www.biogeomancer.org) [52], Google Earth, and high detail physical maps of localities, and strict selection only of verified geo-referenced samples for distribution modeling, as the quality of location data strongly affects the performance of niche modeling techniques [53].
  5. Determine target area for the gap analysis: based upon the native (wild) distribution of the target taxa. Depending on the genepool, the area can range from a small region within a country to the entire world.

2. Determination of sampling deficiencies at the taxon level

A gross representativeness of genebank accessions for each taxon is calculated using the ‘sampling representativeness score’ (SRS, Eqn. 1), comparing total germplasm accessions to herbarium records. (Eqn. 1)

SRS is calculated as the number of germplasm samples (GS) divided by the total number of samples, i.e. the sum of germplasm plus herbarium samples (HS), regardless of whether samples contain location data. SRS therefore permits a general estimation of adequacy of germplasm holdings of each taxon based upon all available data. In the case that a taxon has no genebank samples, it is listed as a “high priority species” for collecting by setting the FPS (see step 7 below) to 0.

In the rare case that for a particular taxon there is obviously deficient herbarium sample data in comparison to germplasm records, the analysis should eliminate SRS as an input for that taxon, as its inclusion would overestimate adequacy of conservation. Mapping of herbarium samples and genebank accessions can be performed (e.g. using DIVA-GIS (version 7.1.70) [29], [54]) in order to provide a general geographic assessment of the available data.

3. Create potential distribution models for taxa

Potential distributions of taxa are calculated using the maximum entropy (Maxent) model [55], with a set of bioclimatic variables and species presence data as inputs. We do not consider the total number of samples with coordinates but the number of different populations represented by those samples (unique locations) [55][58]. We use Maxent due to its precision and confidence when predicting species distributions [55][62]. Default features are used in Maxent, in which complexity of the models (represented by the number of terms and the type of interactions between environmental variables) depend upon the number of input data points [55], [59]. Background points for model training equal 10,000 random points over the distributional range of the genepool in order to avoid overfitting [63], [64].

As the Maxent distribution is generally broader than the real distribution of the species, the modeled distribution is further refined by selecting only known native areas and high probability zones, which generally are defined as the most climatically suitable for the taxon, thus avoiding over-estimation of the realized niche [63], [65]. The potential distribution is limited to the native area reported in the literature and then thresholded using the ROC (receiver operating characteristic) curve plot-based approach (point on the ROC curve [sensitivity vs. 1-specificity] which has the shortest distance to the top-left corner [0,1] in the ROC plot) [55], [59], [66]. We use this threshold as it provides a decent omission rate, is taxon-specific and shows better performance than other thresholds when predicting potential presence [66]. We call this thresholded modeled distribution the “potential distribution coverage”.

Based on the above, for each taxon, we report three model performance metrics: (1) the 25-fold average area under the ROC curve (AUC) [55], [61], [64], [66] of test data (ATAUC), (2) the standard deviation of the test AUC of the 25 different folds (STAUC), and (3) the proportion of the potential distribution coverage with standard deviation above 0.15 (ASD15). Maxent models with ATAUC above 0.7 [66], STAUC below 0.15, and ASD15 below 10% can be considered “accurate and stable” and are thus used in further calculations. We use three measures of model accuracy as the use of AUC alone might mislead the interpretation given the sensitivity of this measure to spatial autocorrelation [67], [68].

For those taxa for which the Maxent model training fails or is inaccurate or unstable, we assign a priority to the taxa using the following criteria:

  1. As with step (2), taxa with no genebank samples are listed as “high priority species” for collecting by setting the FPS (see step 5 below) to 0.
  2. Taxa with genebank samples but no herbarium samples with verified location data are listed as “high priority species” for collecting, as more data are needed in order to perform the analysis. Taxa with such paucity of herbarium records are likely to also have limited germplasm conserved, and are therefore very likely to be “high priority species”. However, these taxa might differ from taxa in (3a) since they already have at least one genebank accession, which certainly permits some type of analyses (e.g. genetic diversity). These taxa are thus differentiated from taxa in (3a) by a flag in the final priorities table (see results).
  3. Taxa with genebank samples and one or more herbarium samples with verified location data are assessed using the area of the convex hull around all known populations (unique locations) of the taxon in lieu of potential distribution coverage. We use the convex hull since, particularly for taxa with very limited occurrence data; it provides a polygon resembling the type of area produced by the Maxent distribution model.

At this point, the potential distribution coverage for all taxa (for which a niche model is possible) may be mapped together in order to display the distribution of the genus, and a richness map along with an uncertainty map (i.e. maximum standard deviation of probabilities among the species that are present in each pixel) for the genepool may be calculated from the results.

4. Geographic coverage assessment

The adequacy of geographic coverage of genebank accessions is calculated as a ‘geographic representativeness score’ (GRS, Eqn. 2), assessed by comparing the taxon potential distribution coverage with the genebank samples geographic coverage, modeled using the ‘circular area statistic with a 50 km radius’ (CA50) value [29]. (Eqn. 2)

GRS is thus the geographic coverage of germplasm collections (GCG) divided by the potential distribution coverage of the taxon under analysis (PDC). The higher the GRS, the higher the representativeness of genebank collections in relation to the potential distribution of the taxon.

5. Determination of environmental gaps

The adequacy of environmental coverage of genebank accessions is calculated as an ‘environmental representativeness score’ (ERS, Eqn. 3), assessed by comparing the germplasm samples in relation to the full environmental range of the modeled taxon distribution. The same set of climatic layers used for developing the potential distribution coverage are standardized to have an average of zero and a standard deviation of 1 in order to perform a principal components analysis. The first two of these spatially explicit components (which normally account for more than 70% of the spatial variability) are reclassified into twenty equal classes.(Eqn. 3)

For these two principal components (i = 2), ERS is calculated as the environmental coverage (i.e. number of different classes) of germplasm collections (EC) divided by the potential environmental coverage of the taxon under analysis (PED), times the weight (w) of the principal component (weights of the two components are re-scaled so that the sum of their weights is 1). If the total variation explained by the first two components is too small (i.e. less than 70%), additional components can be included in the analysis, and should be weighted accordingly.

6. Rarity of each species based on environmental variables determination

All records for the genepool (i.e. GS + HS for all taxa combined) are plotted against a specific environmental variable or linear combination of variables (i.e. vector or principal component) to identify taxa with records falling in rare environmental classes (i.e. extremes of the distribution). We assume that the frequency of the data presents a normal distribution and ‘environmentally rare’ taxa are those located in sites where extreme environmental conditions are found (tails of the distribution - 5th [NSP5] and 95th [NSP95] percentiles). A numeric value (environmentally rare taxa score, ERTS, Eqn. 4) is calculated for each taxon as the number of populations in rare environments divided by the total number of populations of that taxon. (Eqn. 4)

As this step of the gap analysis should be conducted only when there is sufficient data for all the taxa under analysis in order to avoid bias in the results (an abundant number of populations so that a histogram can be calculated), usually it will not be included in the overall assessment. We suggest that this step can be usefully included for the assessment of a specific subset of well-sampled species.

7. Numeric assessment to determine the priority of collecting for ex situ conservation for each taxa

All level-specific representativeness scores (SRS, GRS, ERS, and if possible ERTS) are averaged with equal weight to obtain a final score of prioritization of species. The ‘final priority score’ (FPS), is then used to classify taxa according to the following ranges: (1) as high priority species if the FPS is between 0 and 3, (2) as medium priority species if the FPS is between 3.01 and 5, (3) as low priority species if the FPS is between 5.01 and 7.5, and (4) as well conserved species (no need for further collection) if the FPS is between 7.51 and 10. All taxa flagged as high priority in steps (2) and (3) are included in the list of high priority taxa to be further collected.

8. Prioritization of geographic areas for collecting germplasm

The potential collection zones for each high priority species are identified separately and then combined to highlight those zones where gaps for multiple species overlap (“collection gap richness”). This is done through the following steps:

  1. Identify un-collected zones for each taxon by comparing the potential distribution coverage with the current geographic coverage of germplasm collections (CA50). Areas where the taxon is potentially present but already sampled are dismissed at this stage; the remaining areas are highlighted as uncollected.
  2. Four products treating all mappable high priority taxa are finally produced: (1) individual maps showing potential collecting zones of all high priority taxa, (2) a map of collection gap richness: the number of different taxa that can be collected in each 2.5 arc-minutes (~5 km at the Equator) grid cell, (3) a map showing the maximum standard deviation of high priority taxa (derived from the 25-fold Maxent model training procedure) in each pixel, and (4) a map of the maximum distance of each pixel to the nearest accession (this calculation is done taxon-by-taxon and then aggregated into a single map output, by calculating the maximum of all ‘high priority taxa’.

Testing the gap analysis methodology

The methodology relies on available data and utilizes modeling tools, and is therefore vulnerable to the quantity and quality of input data and the limitations of the modeling applied. In order to test the quality of the results, we have compared them to expert opinion, as following:

  1. Identify one or more experts on the target taxa (i.e. genepool)
  2. Query the selected expert(s) to provide
    1. A ranking of taxa for importance for conservation: To achieve this, the list of taxon names under analysis is sent to the expert(s), who is asked to provide a rating from 1 to 10 for each taxon (where 1 corresponds to a very high priority [i.e. an incomplete collection], and 10 corresponds to the lowest priority [i.e. a complete collection]), without having seen the results of the gap analysis. The expert is requested to rate taxa strictly on the basis of adequacy of ex situ holdings for the taxon.
    2. The expert is then shown the results of the analysis and is asked to give general comments on the validity of the taxa and geographic prioritizations.
  3. Compare the expert and method-based prioritization of each taxon using the relative difference (RD) between the expert priority score (EPS) and the gap analysis FPS, with respect to the total maximum possible difference [Eqn. 5]

(Eqn. 5)
RD is calculated for each taxon and the number of taxa with very similar ratings (−30<RD<30%), the number of taxa somewhat similar ratings (−50%<RD<50%), and the number of taxa with very different ratings (RD <−70% and RD >70%) are then counted. We also plot the FPS and the EPS in a scattergram and calculate both the Spearman correlation coefficient and the P-value of the Spearman correlation coefficient. With these metrics, we aim to provide a general evaluation of the gap analysis method in identifying high priority taxa in comparison to best available expert knowledge.

Results

1. Determination of target taxa, delineation of the target area and harvesting of occurrence data

We conducted a literature review for the Phaseolus genus [30], [32], [69][71], checked against genepool experts (Debouck) and created a complete list of taxonomically verified species. We used the concept established by Maxted et al. [51], including with equal weight all taxa belonging to taxon groups 1 to 4 of the genepool.

According to a recent revision of the Phaseolus genepool [32], there are 81 species and 34 infra-specific taxa, totaling 115 taxa within the genepool. With various species synonyms and historical revisions [27], [30], [32], specimen identification and data availability issues persist. Although taxonomically verified herbarium specimens provided the bulk of the data used in the analysis, we also rely on the specimen identification performed by the individual holding institutions. Based on the recent history of Phaseolus taxonomy, we made the following changes to the determination of specimens used in the data: Any variant within P. polymorphus Wats. was considered as P. polymorphus, and the same was done for P. coccineus L. and P. leptostachyus Benth. [34]. The variants P. polystachyus subsp. smilacifolius (Pollard) Freytag and P. polystachyus subsp. sinuatus (Nuttall ex Torrey & Gray) Freytag were considered as separated species (P. smilacifolius and P. sinuatus, respectively), and the species P. pyramidalis Freytag and P. palmeri Piper were merged into P. grayanus Woot. & Standl. The only infraspecific taxa that were considered were those of wild teparies (P. acutifolius) and those of P. maculatus, for which there was not enough evidence for merging into single species. For taxa with ongoing taxonomic uncertainty (e.g. P. neglectus Hermann), we followed Debouck [32] and CIAT's Genetic Resources Unit genebank practice. After these modifications, a total of 85 taxa were finally listed, including 81 species and 4 infraspecific taxa.

We gathered data from all known available sources, including primary datasets accessed directly from herbaria and genebanks, as well as online global databases, such as the Global Biodiversity Information Facility (GBIF, www.gbif.org), the System-wide Information Network for Genetic Resources (SINGER, www.singer.cgiar.org) database held by the CGIAR, and the United States Department of Agriculture (USDA) Germplasm Resources Information Network (GRIN, www.ars-grin.gov) database (Table 1).

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Table 1. List of institutions from which data was harvested.

doi:10.1371/journal.pone.0013497.t001

Data were available for all taxa, including the 81 species, 2 subspecies and 2 varieties. The entire dataset was carefully geographically verified and corrected using BioGeomancer, and, when possible, new geographic references (coordinates) were added to the passport data. The final dataset contained 11,442 records, of which 6,926 (60.5%) had coordinates or enough location data to obtain coordinates, and 4,516 (39.5%) samples had no location data or coordinates.

The analysis was based on the native range for the genus throughout the Americas (northeastern United States to northern Argentina, including the Caribbean and the Galapagos Islands) [30], [50]. Records outside the boundaries of the Americas, as well as those listed as weedy or cultivated, were deleted and a final dataset was produced for analysis. The average total number of samples per taxon was 144.8, but data was unevenly distributed. Samples were predominantly concentrated in wild progenitors of domesticated species (i.e. P. acutifolius, P. coccineus, P. dumosus, P. lunatus, P. vulgaris), comprising about 55% of the total records.

Germplasm collections of the Phaseolus genepool are not distributed equally in relation to total herbarium collections (Figure 1). The number of genebank accessions in a 200 km cell ranged from 1 to 273, while that of herbarium collections ranged from 1 to 373. Observable differences in the two maps (gaps) are present in the eastern United States, Costa Rica, Nicaragua, and in the north of Mexico and along its border with United States. Most of the areas in central Mexico are however well sampled and it is possible that species occurring in those areas are adequately conserved. This was also observed in some areas in South America (particularly in the Colombian, Ecuadorian and Peruvian Andes), where a greater proportion of genebank accessions have been collected, potentially indicating a better coverage of taxa in genebanks for populations from these regions.

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Figure 1. Density of sampling (sampling richness) for (A) genebank assessions and (B) herbarium records for Phaseolus.

doi:10.1371/journal.pone.0013497.g001

2. Sampling deficiencies at the taxa level

Of 85 taxa, 35 (41.2%) had no germplasm accessions, 26 taxa (30.6%) had 1–9 accessions, and 24 taxa (28.2%) had 10 or more accessions. From the 85 taxa, 61 (71.8%) taxa presented a SRS below 3, indicating poor representativeness of the number of genebank accessions in relation to herbarium collections, whilst 16 taxa (18.8%) showed SRS between 3.01 and 5, 4 (4.7%) between 5.01 and 7.5, and 4 (4.7%) greater than 7.5.

The total representativeness (only in terms of the total number of samples, Figure 2 –intermittent line) is above the average representativeness of germplasm collections (continuous line), signifying that on average, species are likely to have fewer genebank accessions than herbarium specimens. P. vulgaris, P. acutifolius and P. lunatus appear well conserved in relation to both the gross number of accessions (compared to other taxa), and in proportion to their respective number of herbarium records.

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Figure 2. Number of genebank accessions versus all samples (genebank accessions plus herbarium specimen records).

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3. Potential distribution models for taxa

We used high-resolution global climatic datasets developed by Hijmans et al. [72]. WorldClim includes monthly data at 30 arc-seconds resolution (approximately 1 km near the Equator) for total precipitation, and mean, maximum and minimum temperatures. Using such monthly datasets, 19 bioclimatic variables have been derived [73], representing average yearly climates, stressful and extreme conditions, and interannual seasonality (Table 2).

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Table 2. List of derived bioclimatic variables used in the analysis.

doi:10.1371/journal.pone.0013497.t002

We downloaded WorldClim data at 30 arc-seconds, calculated the bioclimatic indices and aggregated the 30 arc-seconds datasets to 2.5 arc-minutes using a bilinear interpolation in order to reduce the computational time and data storage needs. Although most of the bioclimatic indices used to develop the niche models are highly correlated (particularly in the tropics), we used the complete set of 19 bioclimatic variables in Table 2 because (1) they are useful to provide the best possible description of the climatic requirements of species during a single average year, (2) these correlations might not hold in space and time, (3) the alternative approach of dropping some variables leads to underestimation of distributions and poor performance of Maxent [62], (4) the alternative approach of reducing the set of variables to a subset of orthogonal vectors [60] might lead to loss of valuable climatic information and tends to complicate the interpretation of results of the application of the niche model, and (5) the Maxent model prevents over-fitting due to the use of a set of correlated environmental predictors by assigning weights based on the relative importance of the variable to the model [55], [59], [61].

The geographic distributions of 51 out of the 85 taxa were considered sufficiently accurate and stable to be mapped. Potential distribution coverage was estimated via the convex hull method for 3 additional taxa (P. marechalii, P. salicifolius, and P. rotundatus). Therefore, a total of 54 taxa were assessed further.

The genus was modeled to occur from the northern border of the United States through Central America, and along the Andean chain into northern Argentina (Figure 3a). Potential taxon richness ranged from 1 to 23 taxa per grid cell. Taxon diversity hotspots were mainly found in southern and western Mexico and in the southern United States, as well as some highland areas of Guatemala, Honduras and Costa Rica, where 6 to 11 taxa are potentially distributed in a single 5 km pixel.

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Figure 3. Species distributions and uncertainties.

(A) Taxon richness for Phaseolus based upon potential area of distribution of all taxa, (B) modeling uncertainties as maximum standard deviations among all modeled taxa.

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Uncertainties in modeling distributional range calculated by the maximum standard deviation among any possible class (i.e. taxon) varied from 0 to 0.32 (Figure 3b), with the vast majority of the potential distribution coverage of the genus presenting a modeling uncertainty below 10%, and only very few areas presenting more than 15% variation in predicted probabilities. High uncertainty areas do not coincide with high diversity areas, confirming the reliability of the Maxent algorithm in predicting the geographic distributions of our set of taxa. These small spots are located in southwestern Mexico along the very western edge of Nayarit (municipalities of El Nayar, Rosamorada, Tepic), along the borders of Guerrero and Oaxaca, in northern Oaxaca, and in northeastern Michoacán. Despite the observed uncertainties, these areas with more than 15% variability among predictions account to less than 10% of the total potential distribution coverage of the genus.

4. Geographic coverage assessment

The comparison between the CA50 and the size of the potential distribution showed that there are 30 taxa out of the 54 assessed (55.6%) with GRS below 3.01 (less than 30% of representativity in terms of geographic coverage), 12 taxa (22.2%) with GRS between 3.01 and 5, 4 taxa (7.1%) with GRS between 5.01 and 7.5, and 8 taxa (14.8%) with GRS greater than 7.5. The great majority of taxa have germplasm collections covering a geographic range considerably smaller than the potential geographic area in which the taxon is distributed (Figure 4), thus indicating the need for further collecting in order to fill geographic gaps.

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Figure 4. Geographic coverage of genebank accessions against total potential distribution coverage of taxa.

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The average representativeness line (intermittent line) is above the complete representativeness line (continuous line), indicating that the representativeness of germplasm collections in comparison to the total potential distribution coverage is low on average, and relatively high only for a few species (namely the wild progenitors P. vulgaris, P. coccineus, P. acutifolius and P. lunatus).

5. Determination of environmental gaps

The principal components analysis showed that the first two components explained up to 81.5% of the total spatial variability among the Phaseolus genepool target area (61.2 and 20.3% for PC1 and PC2 respectively). Re-scaling of these two components' weights resulted in a weight of 75.03% for PC1 and 24.97% for PC2. Out of the 54 modeled taxa, 10 (18.5%) presented ERS below 3.01, indicating a significantly low environmental representativeness (i.e. less than 30%) in germplasm collections; 7 (13%) taxa presented an ERS between 3.01 and 5; 7 taxa (13%) between 5.01 and 7.5; and 30 taxa (55.6%) above 7.5. Notably, environmental representativeness of genebank accessions was found to predominantly fit in the two extreme classes (below 30% and above 75%) for most of the taxa.

P. vulgaris and P. lunatus showed the highest coverage of potential environmental range, with 8 and 14 respectively out of the 20 classes along PC1, and 8 and 16 classes along PC2 (Figure 5). Germplasm representativeness of these environmental classes is for both species significantly high (90% or more representativeness in both classes). For wild P. vulgaris, among other cases (Figure 5), we found the environmental distribution of genebank accessions to be broader than the environmental distribution of the potential distribution coverage, which may be explained as an artifact given the use of the ROC-plot based threshold for binning the species distributions (i.e. the omission rate), the native area (i.e. one or two small localities where the taxon occurs might not be reported in literature), or the use of the CA50 around germplasm locations, which might enlarge the range towards unsuitable habitats, particularly where the landscape changes rapidly (e.g. topographically diverse regions, such as the Andes). A broad range of adaptation to climatic conditions may be covered by current germplasm collections, but it should be noted that small environmental gaps remain even for these well-sampled species.

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Figure 5. Coverage of genebank accessions versus potential environmental area for modeled species for the first (left) and second (right) principal components.

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6. Rarity of each species

Rarity of species was not included in the analysis since there were significant sampling biases that would lead to inaccurate results. In order to produce accurate results, the weight of the ERTS was finally established at 0.05, which is practically irrelevant and thus the step was dropped. If a subset of species with reliable sampling were to be analyzed separately (e.g. the five wild progenitors of the domesticated species), however, the ERTS could be calculated and weighted equally with the other scores when calculating the FPS.

7. Numeric assessment to determine the priority of collecting for ex situ conservation for each taxon

Out of the 85 taxa under analysis, 48 (56.5%) are either under-represented or not represented in any way in genebanks and therefore flagged as HPS for collecting (Table 3, Table S1). Of these taxa, 35 had no germplasm accessions, and 11 are listed as HPS due to the average of gross representativeness, geographic, and environmental gaps (FPS below 3.01). A further 2 taxa (P. sinuatus and P. altimontanus) couldn't be assessed due to uncertainties in the modeling and the data, and are included as HPS due to the need for collecting in order to provide adequate data for a gap analysis.

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Table 3. List of taxa and available data included in the analysis (see Table S1 for full details).

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Medium priority for further collecting was given to 17 taxa (20%), 15 taxa (17.7%) were given low priority, and only 5 taxa (P. macrolepis, P. marechalii, P. pachyrrhizoides, P. xanthotrichus and P. vulgaris) were assessed as well represented in ex situ collections.

8. Prioritization of geographic areas for collecting germplasm

36 priority taxa (i.e. those flagged as high priority and with sufficient location data) were mapped together, along with standard deviations on predicted Maxent probabilities (aggregated for all the taxa using the maximum value) and distances to the nearest population (also aggregated) (Figure 6). Potential collection sites have a richness of up to 7 taxa per grid (Figure 6a). Zones where gaps in ex situ collections for many Phaseolus taxa overlap are concentrated in central-western Mexico, with an extension along the Sierra Madre Occidental north to Sonora.

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Figure 6. Prioritization results.

(A) Zones where gaps in ex situ collections for multiple taxa overlap (collecting gap richness) for high priority species, (B) modeling uncertainties as standard deviations among high priority modeled taxa, (C) collecting uncertainties as maximum geographic distance to nearest known population.

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Andean environments where Phaseolus species are likely distributed appear in general to be adequately represented in genebanks for most of the species. Note that the narrow endemic nature of many of the under- or un-sampled taxa results in a need for very finely targeted collection trips to specific regions outside of the gap richness areas identified, for example to collect from populations of P. carteri, P. novoleonensis, and P. plagiocylix in isolated regions of Mexico, and P. mollis in South America.

The maximum modeling uncertainty (given by the maximum standard deviation of the 25 folds per taxon) was slightly greater than 15% in a very small area (dark blue spot in western Nayarit, Figure 6b). Interestingly, modeling uncertainties of high priority taxa had a maximum of 19%, significantly lower than uncertainties of the whole set of taxa under analysis (Figure 3b), strengthening confidence in results regarding high priority taxa. The distance to verified populations (Figure 6c) was greatest (i.e. uncertainty) in northwestern Mexico (southern Sonora, northern Sinaloa, and southwestern Chihuahua). The areas identified in these uncertainty analyses are least likely to contain target species.

Comparison with expert opinion

The expert authority for Phaseolus was Daniel G. Debouck (DGD), head of the Genetic Resources Unit at the International Center for Tropical Agriculture (CIAT), author and co-author of numerous publications on Phaseolus, including a survey of the Phaseolus genepool in North and Central America [30], who has participated in many collecting missions for the genus throughout the Americas and has extensive expertise in taxonomy (including research at 67 different herbaria in the last 32 years), ecogeographic distributions, and level of in situ and ex situ conservation of the genepool.

DGD did not assess 4 taxa: P. maculatus, and P. acutifolius since he considered it enough to assess the subspecies and/or variants, and P. trifidus and P. opacus, since he considered them as doubtful taxa. All figures below are thus based on the total number of taxa assessed by DGD (81). Further taxonomic analyses of these species are needed in order to inform conservation priorities.

In comparison to expert opinion, the gap analysis approach tended to underestimate priority for collecting in a considerable number of cases (30.9% of the taxa); however, scores for 28 taxa (34.6%) did align with expert opinion (with 0 as score for 24 of these). For 51 taxa (63%), the method and DGD agreed on the priority class, and from the remaining proportion, the difference was of one single class. In addition, the relative difference (RD) varied from −50% to 72.2% and the maximum difference between our approach and the expert's concept was around 7 units in the priority scale of 10 units. Moreover, 87.7% of the validated taxa (81) presented differences lower than 30% or greater than −30%, and only 2 taxa presented more than a 50% or less than −50% difference (P. salicifolius with 7.2 in EPS and 0 in FPS, P. marechalii with 8.3 in EPS and 3 in FPS). Only P. salicifolius was found to have more than 70% difference between EPS and FPS (Figure 7a).

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Figure 7. Validation results.

(A) Frequency distribution of the relative difference [RD] and (B) linear trend between Final Priority Score (FPS) and Expert Priority Score (EPS) (the red dotted line indicates a 95% confidence interval).

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The linear trend between EPS and FPS has a Spearman correlation coefficient of 0.79 (p<0.0001, n = 79). However, as previously stated, the gap analysis approach tends to underestimate the priorities compared to expert opinion (average underestimation is −10.7%, Figure 7b).

A number of taxa fall far from the linear trend (i.e. P. neglectus, P. albiflorus, P. salicifolius and P. pachyrrhizoides). Whilst for P. pachyrrhizoides this is due to a very high accuracy (ERS and FPS are equal) in comparison with the propagating error in the regression line (i.e. the underestimation error), differences for other taxa generally result from lack of geographic data for a robust gap analysis, likely taxonomic misidentifications in records, and/or difficulty in eliminating duplicates in records (e.g. P. neglectus, P. albiflorus).

For species such as P. xanthotrichus and P. oligospermus, the gap analysis approach indicated little need for further collection, as germplasm has been collected throughout the most of the region of recorded herbarium collections and environments occupied by those collections. However, expert knowledge on other areas of distribution of the species, under-recorded in online herbarium data, gave the species higher priority on the EPS.

Discussion

Success of the gap analysis method in identifying priority taxonomic, geographic, and environmental gaps is directly dependent on the quality of input data and robustness of the modeling based upon the data. In this section we discuss uncertainties and limitations concerning the method:

a. Input data availability, bias and certainty

The quality of the input geographic information (i.e. climatic and occurrence data) directly affects the performance of species distributions models [53], [57], [58], [60], [62], [74]. Geographic data for specimens is generally less than optimal and is unevenly distributed across taxa, due to the bias of collecting activities toward particular species or locations, a historically insufficient prioritization of recording and maintaining of geographic data, lack of high quality absence data for species, and limited accessibility of stored data for some collections. Many regions of the world remain un- or under-sampled, particularly highly inaccessible areas, and those chronically affected by war or civil strife.

Recently described and/or under-studied taxa, such as P. acinaciformis, P. juquilensis, P. longiplacentifer, P. persistentus, P. scrobiculatifolius, P. teulensis, P. albiviolaceus, P. leptophyllus, P. lignosus, P. scabrellus, and P. sinuatus, may require further taxonomic clarification, and are generally in need of further collecting, and characterization of the collected populations, in order to clarify identification and facilitate accurate prioritization.

Infraspecific taxa (variants and subspecies), such as those of P. maculatus and P. acutifolius, may also be incompletely treated in the analysis due to data constraints. There are several records of these species that remain undetermined at the infraspecific level. Due to overlapping ranges of distribution for various infraspecific taxa, unassigned records cannot be easily differentiated based on collection location. In the gap analysis we have therefore assessed both the species level and the infraspecific taxa.

More germplasm of Phaseolus may be conserved worldwide than the accession data used in this analysis indicate, as the data from some genebanks was not accessible. We assume that, with few exceptions, the accessions whose data was not accessible are also generally inaccessible to crop breeders and researchers worldwide. Areas where these collections were made may not represent a gap for the particular holding collection, yet they are effectively a very real gap for rest of the global community.

Duplication between and within institutes might inflate the numbers of unique records for some of the taxa, leading to bias in the prioritization results. The use of different numbering systems, and lack of tracking of former records, leads to an overestimation of samples held, and difficulty in identifying duplicates, perhaps especially for the most commonly exchanged species (e.g. wild progenitors). For Phaseolus, we found that large differences can exist between the number of records and of actual populations both for genebanks (up to 83.1%) and herbaria (up to 87.5%). The data preparation phase of the analysis involved a thorough identification of duplicates in order to avoid inflation of numbers of records and therefore biases in prioritization. Further, the geographic representativeness score (GRS) takes distinctness/uniqueness of populations into account indirectly, and the environmental representativeness score (ERS) addresses the issue by illuminating gaps in the abiotic adaptations of the sampled material (i.e. number of different climatic environments covered by the conserved material).

Location data constraints may also limit the taxa for which the method may be applied, as well as lead to an underestimation of taxon distributions. From the 45 different data sources, 24 (53.3%) had more records without location data than with location data, and only 9 (20%) of the sources presented all of their records with coordinates or with detailed location data (Table 1). For genebanks, 71.1% of the data presented reliable location data and 28.9% had either no location data or location data were unreliable, whilst for herbaria, 70.2% of the data presented coordinates and 29.8% did not present any useful location data.

Additional data, such as absence of the taxon, would certainly improve model-training by increasing the model's ability to discriminate between presence and absence areas. These data are unfortunately not available in conventional genetic resources databases [59], [75]. Future collecting should be planned with an eye to the improvement of gap analysis approaches and should thus consider a more systematic recording of absences, geo-referencing all records, and making widely accessible data from all available germplasm and herbarium samples. These actions will improve the performance of species distribution models and any conclusions drawn from them.

b. Ability of the species distribution model used (i.e. Maxent) to adequately predict the potential and realized niche of taxa

The Maxent modeling technique was chosen for its ability to handle sample bias and spatial autocorrelation of species data [57], [58], [64] so as to provide high confidence species distributions models even given limited or biased location data. Maxent is an algorithm known to reliably predict the potential niches of species, and has been tested by several authors under a wide range of conditions and configurations (e.g. 55, 61, 57–58, 63–65, among others); although we note that some reports [68], [76][77] consider niche modeling techniques misleading and of limited use in certain contexts. As the robustness of Maxent is considered in the publications listed above, we do not provide a full analysis here.

We used the average test-data AUC, which showed that 52 species distribution models were reliable (i.e. accurate and stable, Table S1). Using the current configuration, the AUC statistic is not likely to be biased by the pseudo-absences range [63]. Discrimination between presence and absence sites was therefore considerably positive for most of the taxa (~70%). Particularly good was the performance of taxon distribution models with more than 40 data points.

Moreover, the uncertainties associated with the application of a probabilistic model such as Maxent and depicted by the 25-fold cross-validated models for each of the taxa indicated that standard deviations among predictions ranged from 0 to 0.19. Collecting priorities are more uncertain in limited areas (e.g. along the western coast of Mexico), but are relatively robust across the vast majority of the distributional range of the genepool.

However, there was a set of taxa (those marked with + in Table 3) for which we were not able to develop species distributions models due to either lack of samples or to the distribution of those samples. These species could benefit from other approaches, such as Bayesian techniques [78], which are able to develop probability surfaces even from a single point. Here we did not include these additional approaches, given the uncertainties involved with these models. We rather use specimen data (i.e. herbarium sampling points) to depict areas where these species can be potentially collected.

c. Geographic collecting priorities

To analyze the validity of geographic gap results, we have calculated the stability (standard deviation) of the Maxent models and have also provided the distance to the nearest population within the collection zone (Figure 6).

Additional analyses, including threat level, can be incorporated into the methodology in order to refine conservation priorities. Possible threats that could lead to genetic erosion in wild species populations include fires, grazing pressure, invasive species, deforestation, habitat modification and degradation, urbanization, and climate change, among others [5]. Accession-level genetic data may also serve as an input in order to identify gaps in genetic diversity. Additional environmental data, such as soil type, may further define potential distributions of species. These additional inputs are currently only rarely available at high detail over large geographic areas or for all taxa in a genepool, but this may improve with the ongoing development of GIS and decreasing costs of genotyping. Taxon-specific knowledge may also be used to refine or weight priorities, giving some species higher importance in the final result (e.g. focusing on specific traits of interest, adjusting to phytosanitary/noxious weed constraints, recognizing legal constraints to access, prioritizing in order to capitalize on appropriate seasonal collecting windows, etc.)

In our approach, we include all wild relatives of the crop without regard to relatedness to cultivated species, weighting them equally, with the assumption that a wide range of taxa are potentially useful to provide genes for crop improvement [11], recognizing the lack of data on relatedness. Information on relatedness and threat level can be added to the prioritization exercise by experts with specific interests or familiar with local conditions.

When this is done for Phaseolus the following gaps are highlighted. Collecting a few (1–5) populations is needed for 35 taxa that currently have no genebank samples conserved. Out of the five wild progenitors of the domesticated species, P. vulgaris and P. dumosus have been relatively well sampled, and only small gaps remain to be filled. Briefly, gaps for wild P. vulgaris are present in: Oaxaca, El Salvador, Panama, western Andes of Venezuela, northern central Bolivia, and San Luis in Argentina. For wild P. dumosus: eastern Chiapas and Alta Verapaz in Guatemala. For the remaining three progenitors, the gaps are substantially more important. For P. acutifolius: Sonora, Chihuahua, many spots in western Mexico and in Guerrero. For P. coccineus: Chihuahua down to Guatemala. For P. lunatus, gaps exist throughout the very large range (from the Revillagigedo Islands, Baja California Sur and Sinaloa to Puerto Rico, and down to Salta and Formosa in Argentina.

Regarding the secondary genepool of each of the five cultigens: for common bean, runner bean, and year bean, additional collecting is needed for P. albescens, P. costaricensis, and P. persistentus (if placement into Sect. Phaseoli is confirmed). For tepary, collecting is needed for P. parvifolius (all across its range from Chihuahua down into Guatemala). For Lima bean, concerted effort is required because few (if any) accessions are available for taxa within Section Paniculati, as well as P. maculatus, P. novoleonensis, P. reticulatus, P. ritensis, and P. venosus within Section Coriacei.

For the remaining Phaseolus species (not highly related to any cultigen given molecular evidence available today), a few accessions exist for taxa such as P. chiapasanus, P. esperanzae, P. pluriflorus, and P. micranthus. Remaining species are in need of further collecting in order to secure germplasm ex situ.

d. Comparison with expert knowledge

The method performed well as compared with expert knowledge on the Phaseolus genepool, 81.2% of the taxa presenting differences between −30% and 30%, and only one taxon with a difference of more than 70% between EPS and FPS. We note that although the expert will often refine the analysis by adding further insight and by qualifying data, the gap analysis also holds the potential to highlight taxonomic, geographic, and environmental gaps previously unknown to the expert.

In order to provide a more robust test, multiple experts could be consulted. As GIS approaches continue to expand and improve, a more comprehensive validation procedure may be performed with a network of experts, facilitated through an online portal.

Expert intervention within the gap analysis method is especially critical during (1) thorough taxonomical review of the genepool, including variants and/or subspecies changes according to the latest studies, (2) the full evaluation and georeferencing of locality names in the dataset, and (3) the further refining and correction of priorities when a data availability issue is detected.

Expert taxonomic knowledge will of course also be vital in the actual field collecting, especially for understudied species (e.g. P. albinervus, P. leptophyllus, and P. purpusii). This has proven to be important in this genus, as numerous new species have been identified only during germplasm collecting missions (e.g. P. altimontanus, P. costaricensis, P. novoleonensis, P. persistentus, P. rotundatus, and P. talamancensis).

Conclusion and final remarks

This study proposes a method for the rational prioritization of taxa within a genepool for collection for ex situ conservation, using Phaseolus as a model. The method builds upon the standard comparison of herbarium samples with genebank accessions via gap analysis [17], yet aims to address sampling biases by modeling species distributions with a robust algorithm, and refining these distributions using two different criteria. Furthermore, the method identifies priorities based not only on taxonomic and geographic gaps, but also environmental gaps. Priority locations for sampling of gaps result, as well as gap richness models contributing to the identification of collection locations for maximum efficiency. The results cover the four target outcomes of gap analysis identified by Nabhan [18]. Collecting for ex situ conservation should prioritize the resulting taxa, including those not or under-sampled ex situ, as well as geographic and environmental gaps in the distribution of taxa with some degree of germplasm currently conserved.

We found 48 high priority taxa (56.5%) (Table 3, Table S1), 35 (41.1% of total) of these not recorded as represented ex situ by even a single accession. Acknowledging that the results for a number of these species may potentially be affected by data availability constraints, in the most optimistic case, around half of the taxa in the genepool are highly under-represented in ex situ conservation. There is therefore a clear need for further collecting in order to cover the full range of taxonomic, geographic and environmental diversity.

The greatest priority regions for further collecting are located in northern Central America (i.e. Mexico and Guatemala), with a maximum potential sampling richness of 7 species per 5 km cell. However, there are a number of species that require individually targeted efforts in other areas (e.g. P. mollis, in the Galapagos Islands).

Additional criteria, such as threats to taxa, and degree of relatedness of taxa to cultivated species, may also be included in the analysis, when data is sufficiently available. In order to include a more complete picture of conservation, the method should ideally be coupled with in situ gap analysis results [e.g. 15], i.e. comparison of distributions with the extent of protected areas. In general, the high priority taxa identified in the analysis are likely to be those also most highly prioritized for in situ conservation, although this was not explored in the current analysis.

The method is applicable to any set of related taxa, given adequate geographic data and a thorough taxonomic and geographic referencing process. Genepools whose taxonomy has not received sufficient attention (e.g. Oryza in the Americas), or which have not been well sampled for herbarium specimens, will present particular challenges in producing reliable results. As each genepool is different, the analysis must be adapted according to data availability, and tested against expert knowledge, preferably repeatedly. Once the method has been applied to a number of crop genepools, the prioritization of taxa and “gap richness” mapping may be applied for these genepools together, potentially facilitating the identification of priority regions (“plant genetic resource gap megacenters”) for the efficient and effective collecting of CWR diversity on a global scale.

Supporting Information

Table S1.

Complete set of metrics used for the assessment of species distributions and ex-situ conservation status. Prioritization of taxa is done as follows: HPS: High priority species, MPS: Medium priority species, LPS: Low priority species, NFCR: No further urgent conservation required. FPS indicates the result of the method proposed in this paper, and EPS indicates the prioritization given by expert knowledge (based on Daniel G. Debouck's expertise in Phaseolus). +Indicates that the taxon had no genebank accessions and no herbarium samples with coordinates or location data; ++indicates a taxon for which a Maxent model was not possible and for which 0-few genebank accessions were available; #indicates a taxon with some genebank accessions but no or limited herbarium samples with coordinates or location data. These taxa are listed as HPS for further collecting in order to inform the gap analysis.

doi:10.1371/journal.pone.0013497.s001

(0.03 MB XLS)

Acknowledgments

The authors thank Nora Patricia Castaneda, from the International Center for Tropical Agriculture (CIAT), for providing inputs to very preliminary versions of the analyses presented here, as well as Silvia Castano, Ovidio Rivera and Carlos Nagles, from the International Center for Tropical Agriculture (CIAT) for aiding in some of the georreferencing work. We also thank the two anonymous reviewers for their useful inputs.

Author Contributions

Conceived and designed the experiments: JRV AJ. Performed the experiments: JRV. Analyzed the data: JRV CK DGD. Contributed reagents/materials/analysis tools: JRV CK AJ DGD LG. Wrote the paper: JRV CK AJ LG. Created the first version of the methodology: JRV. Provided a great deal of input for corrections to issues highlighted by other authors: CK. Provided substantial scientific background: AJ LG. Led to intense discussions and provided critical data for the enhancement of the paper: DGD.

References

  1. 1. Harlan JR, de Wet JMJ (1971) Toward a Rational Classification of Cultivated Plants. Taxon 20(4): 509–517.
  2. 2. Singh SP (2001) Broadening the Genetic Base of Common Bean Cultivars: A Review. Crop Science 41: 1659–1675.
  3. 3. Hajjar R, Hodgkin T (2007) The use of wild relatives in crop improvement: A survey of developments over the last 20 years. Euphytica 156: 1–13.
  4. 4. Prescott-Allen C, Prescott-Allen R (1986) The First Resource: Wild Species in the North American Economy. Yale University, New Haven.
  5. 5. Tanksley SD, McCouch SR (1997) Seed Banks and Molecular Maps: Unlocking Genetic Potential from the Wild. Science 277(5329) (August22): 1063–1066. doi:10.1126/science.277.5329.1063.
  6. 6. Food and Agriculture Organization of the United Nations (FAO) (1997) State of the World's Plant Genetic Resources for Food and Agriculture. Rome, Italy. Available: http://apps3.fao.org/wiews/wiewspage.jsp​?i_l=EN&show=SOW1.
  7. 7. Maxted N, Kell S (2009) Establishment of a global network for the in situ conservation of crop wild relatives: status and needs. Rome, Italy: FAO Commission on Genetic Resources for Food and Agriculture.
  8. 8. Khoury C, Laliberté B, Guarino L (2010) Trends in ex situ conservation of plant genetic resources: a review of global crop and regional conservation strategies. Genetic Resources and Crop Evolution 57(4): 625–639. doi:10.1007/s10722-010-9534-z.
  9. 9. Intergovernmental Panel on Climate Change (2007) Geneva: IPCC Fourth Assessment Report: Climate Change 2007, IPCC.
  10. 10. Hawkins B, Sharrock S, Havens K (2008) Plants and Climate Change: which future? Richmond, UK: Botanic Gardens and Conservation International. 98 p.
  11. 11. Challinor AJ, Wheeler TR, Craufurd PQ, Ferro CAT, Stephenson DB (2007) Adaptation of crops to climate change through genotypic responses to mean and extreme temperatures. Agriculture, Ecosystems and Environment 119: 190–204.
  12. 12. Brooks TM, Mittermeier RA, da Fonseca GAB, Gerlach J, Hoffmann M, et al. (2006) Global Biodiversity Conservation Priorities. Science 313(5783) (July7): 58–61. doi:10.1126/science.1127609.
  13. 13. Thuiller W, Lavorel S, Araújo MB, Sykes MT, Prentice IC (2005) Climate change threats to plant diversity in Europe. Proceedings of the National Academy of Sciences 102(23): 8245.
  14. 14. Meilleur BA, Hodgkin T (2004) In situ conservation of crop wild relatives: status and trends. Biodiversity and Conservation 13(4): 663–684. doi:10.1023/B:BIOC.0000011719.03230.17.
  15. 15. Burke MB, Lobell DB, Guarino L (2009) Shifts in African crop climates by 2050, and the implications for crop improvement and genetic resources conservation. Global Environmental Change 19(3) (8): 317–325. doi:10.1016/j.gloenvcha.2009.04.003.
  16. 16. Food and Agriculture Organization of the United Nations (FAO) (2009) Second report on the state of the world's plant genetic resources for food and agriculture (draft), Rome. Available: ftp://ftp.fao.org/docrep/fao/meeting/017​/ak528e.pdf.
  17. 17. Maxted N, Dulloo E, Ford-Lloyd BV, Iriondo JM, Jarvis A (2008) Gap analysis: a tool for complementary genetic conservation assessment. Diversity and Distributions 14(6): 1018–1030.
  18. 18. Nabhan GP (1990) Wild Phaseolus Ecogeography in the Sierra Madre Occidental, Mexico: Areographic techniques for targeting and conserving species diversity. Systematic and Ecogeographic Studies on Crop Genepools 5. International Board of Plant Genetic Resources (IBPGR).
  19. 19. Graham C, Hijmans RJ (2006) A comparison of methods for mapping species range and species richness. Global Ecology and Biogeography 15: 578–587.
  20. 20. Hijmans RJ, Spooner DM, Salas AR, Guarino L, de la Cruz J (2002) Atlas of Wild Potatoes. Rome, Italy: International Plant Genetic Resources Institute.
  21. 21. Hijmans RJ, Spooner D (2001) Geographic distribution of wild potato species. American Journal of Botany 88: 2101–2112.
  22. 22. Jarvis A, Ferguson M, Williams D, Guarino L, Jones P, et al. (2003) Biogeography of wild Arachis: Assessing conservation status and setting future priorities. Crop Science 43: 1100–1108.
  23. 23. Jarvis A, Guarino L, Williams D, Williams K, Hyman G (2002) Spatial analysis of wild peanut distributions and the implications for plant genetic resource conservation. Plant Genetic Resources Newsletter 131: 29–35.
  24. 24. Jarvis A, Yeaman S, Guarino L, Tohme J (2005) The role of geographic analysis in locating, understanding, and using plant genetic diversity. In: Zimmer E, editor. Elsevier, New York: Molecular Evolution: Producing the Biochemical Data, Part B.. pp. 279–298.
  25. 25. Jones PB, Beebe SE, Tohme J, Galwey NW (1997) The use of geographical information systems in biodiversity exploration and conservation. Biodiversity Conservation 6: 947–958.
  26. 26. Lobo Burle M, Torres Cordeiro CM, Fonseca JR, Martins Palhares de Melo L A, de Belem das Neves Alves R, et al. (2003) Characterization of germplasm according to environmental conditions at the collecting site using GIS- two case studies from Brazil. Plant Genetic Resources Newsletter 135: 1–11.
  27. 27. Maxted N, Mabuza-Dlamini P, Moss H, Padulosi S, Jarvis A, et al. (2004) An Ecogeographic Study: African Vigna. Rome: International Plant Genetic Resources Institute.
  28. 28. Parthasarathy U, Saji KV, Jayarajan K, Parthasarathy VA (2006) Biodiversity of Piper in South India – application of GIS and cluster analysis. Current Science. 91. (5).
  29. 29. Hijmans RJ, Guarino L, Cruz M, Rojas E (2001) Computer tools for spatial analysis of plant genetic resources data: 1. DIVA-GIS. Plant Genetic Resources Newsletter 127: 15–19.
  30. 30. Freytag GF, Debouck DG (2002) Taxonomy, Distribution, and Ecology of the Genus Phaseolus in North America, Mexico and Central America. Botanical Research Institute, Fort Worth.
  31. 31. Gepts P (2001) Phaseolus vulgaris (Beans). In Encyclopedia of Genetics.Academic Press. 1444–1445.
  32. 32. Debouck DG (2009) Cahiers de Phaséologie – Synonymie. International Center for Tropical Agriculture, CIAT. Available: http://isa.ciat.cgiar.org/urg/urgweb_fol​der/files/unitfiles/CahiersdePhaseologie​Synonymie.pdf [Accessed: 10 November 2009].
  33. 33. Delgado-Salinas A (1985) Systematics of the genus Phaseolus (Leguminosae) in North and Central America. Ph.D. 363: Texas, USA: Thesis, Univ. of Texas, Austin.
  34. 34. Debouck DG (2000) Biodiversity, Ecology, and Genetic Resources of Phaseolus Beans- Seven Answered and Unanswered Questions. In: Oono K, editor. Wild Legumes. pp. 95–123. Ministry of Agriculture, Forestry and Fisheries, and National Institute of Agrobiological Resources, Tsukuba, Ibaraki, Japan.
  35. 35. Debouck DG, Smartt J (1995) Beans. In: Smartt J, Simmonds N W, editors. Evolution of Crop Plants. Singapore: Longman Scientific and Technical. pp. 287–294.
  36. 36. McClean P, Gepts P, Kami J (2004) Genomics and Genetic Diversity in Common Bean. In: Wilson R, Stalker HT, Brummer EC, editors. Legume Crop Genomics. AOCS, Champaign. pp. 60–82.
  37. 37. Food and Agriculture Organization of the United Nations (FAOSTAT). (2009) Available: http://faostat.fao.org/site/339/default.​aspx.
  38. 38. Smartt J (1981) Gene Pools in Phaseolus and Vigna Cultigens. Euphytica 30: 445–449.
  39. 39. Singh RJ, Jauhar P (2005) Genetic Resources, chromosome engineering, and crop improvement: Grain Legumes, Volume 1.CRC Press. 390.
  40. 40. Debouck DG (1999) Diversity in Phaseolus species in relation to the common bean. Chapter 2. In: Singh SP, editor, Common bean improvement in the twenty-first century.Dordrecht, Holland: Kluwer Academic Publishers. 25–52.
  41. 41. Acosta-Gallegos JA, Kelly JD, Gepts P (2007) Prebreeding in Common Bean and Use of Genetic Diversity from Wild Germplasm. Crop Science. 47, no.. (12): pp. S-44–S-59. doi:10.2135/cropsci2007.04.0008IPBS.
  42. 42. Delgado-Salinas A, Turley T, Richman A, Lavin M (1999) Phylogenetic analysis of the cultivated and wild species of Phaseolus (Fabaceae). Systematic Botany 24: 438–460.
  43. 43. Kornegay J, Cardona C (1991) Breeding for insect resistance. In: van Schoonhaven A, Voysest O, editors. Common Beans: Wallingford: Research for Crop Improvement. CAB International. pp. 619–41.
  44. 44. Shelley-Dessert KC, Bliss FA van Schoonhaven A, Voysest O, editors. (1991) Genetic improvement in food quality factors.Common Beans: Wallingford: Research for Crop Improvement. CAB International. 649–71.
  45. 45. Kipe-Nolt JA, Montealegre CM, Tohme J (1992) Restriction of nodulation by the broad host range Rhizobium tropici strain CIAT899 in wild accessions of Phaseolus vulgaris. New phytol 120: 489–94.
  46. 46. Schinkel C, Gepts P (1988) Phaseolin diversity in the tepary bean Phaseolus acutifolius A Gray. Plant Breeding 101: 292–301.
  47. 47. Garvin FD, Weeden N (1994) Isozyme evidence supporting a simple geographic origin for domesticated tepary bean. Crop Science 34: 1390–1395.
  48. 48. Munoz LC, Duque MC, Debouck DG, Blair MW (2006) Taxonomy of tepary bean and wild relatives as determined by amplified fragment length polymorphism (AFLP) markers. Crop Science 46: 1744–1754.
  49. 49. The Consultative Group on International Agricultural Research (CGIAR), System-wide Information network for Genetic Resources (SINGER) (2009) Available: http://singer.grinfo.net/.
  50. 50. USDA, ARS, National Genetic Resources Program (NGRP) (2009) Germplasm Resources Information Network - (GRIN) [Online Database]. National Germplasm Resources Laboratory, Beltsville, Maryland. Available: http://www.ars-grin.gov/cgi-bin/npgs/htm​l/index.pl.
  51. 51. Maxted N, Ford-Lloyd BV, Jury SL, Kell SP, Scholten MA (2006) Towards a definition of a crop wild relative. Biodiversity and Conservation 15(8): 2673–2685.
  52. 52. Guralnick RP, Wieczorek J, Beaman R, Hijmans RJ, the BioGeomancer Working Group (2006) Biogeomancer: Automated Georreferencing to Map the World's Biodiversity Data. PLoS Biology 4(11): 1908–1909.
  53. 53. Graham C, Elith J, Hijmans RJ, Guisan A, Peterson AT, et al. (2008) The influence of spatial errors in species occurrence data used in distribution models. Journal of Applied Ecology 45: 239–247.
  54. 54. Hijmans RJ, Guarino L, Jarvis A, O'Brien R, Mathur P, et al. (2005b) DIVA-GIS version 5.2 manual. Available: http://www.diva-gis.org/Materials.htm.
  55. 55. Phillips SJ, Anderson RP, Schapire RE (2006) Maximum entropy modeling of species geographic distributions. Ecological Modelling 190: 231–259.
  56. 56. Hernandez PA, Graham CH, Master LL, Albert DL (2006) The effect of sample size and species characteristics on performance of different species distribution modeling methods. Ecography 29: 773–785.
  57. 57. Loiselle BA, Jorgensen PM, Consiglio T, Jimenez I, Blake JG, et al. (2008) Predicting species distributions from herbarium collections: does climate bias in collection sampling influence model outcomes? Journal of Biogeography 35(1): 105–116.
  58. 58. Costa GC, Nogueira C, Machado RB, Colli GR (2010) Sampling bias and the use of ecological niche modeling in conservation planning: a field evaluation in a biodiversity hotspot. Biodiversity Conservation 19: 883–899.
  59. 59. Phillips SJ, Dudik M (2008) Modeling of Species Distributions with Maxent: New Extensions and Comprehensive Evaluation. Ecography 31: 161–175.
  60. 60. Dormann CF (2006) Promising the future? Global change projections of species distributions. Basic Applied Ecology 8: 387–397.
  61. 61. Elith J, Graham CH, Anderson RP, Dudik M, Ferrier S, et al. (2006) Novel methods improve prediction of species' distributions from occurrence data. Ecography 29: 129–151.
  62. 62. Hijmans RJ, Graham C (2006) The ability of climate envelope models to predict the effect of climate change on species distributions. Global Change Biology 12: 2272–2281.
  63. 63. VanDerWal J, Shoo LP, Graham CH, Williams SE (2009) Selecting pseudo-absence data for presence-only distribution modeling: How far should you stray from what you know? Ecological Modeling 220: 589–594.
  64. 64. Phillips SJ (2008) Transferability, sample selection bias and background data in presence-only modeling: a response to Peterson, et al. (2007). Ecography 31: 272–278.
  65. 65. Smolik MG, Dullinger S, Essl F, Kleinbauer I, Leitner M, et al. (2010) Integrating species distribution models and interacting particle systems to predict the spread of an invasive alien plant. Journal of Biogeography 37(3): 411–422. doi:10.1111/j.1365-2699.2009.02227.x.
  66. 66. Liu C, Berry PM, Dawson TP, Pearson RG (2005) Selecting thresholds of occurrence in the prediction of species distributions. Ecography 28: 385–393.
  67. 67. Veloz SD (2009) Spatially autocorrelated sampling falsely inflates measures of accuracy for presence-only niche models. Journal of Biogeography 36: 2290–2299.
  68. 68. Lobo JM, Jiménez-Valverde A, Real R (2008) AUC: a misleading measure of the performance of predictive distribution models. Global Ecology and Biogeography 17(2): 145–151.
  69. 69. Salcedo CJ, Arroyave JA, Toro O, Debouck DG (2006) Phaseolus novoleonensis, a new species (Leguminosae, Phaseolinae) from the Sierra Madre Oriental, Nuevo León, Mexico. Novon 16(1): 106–112.
  70. 70. Delgado-Salinas A, Carr WR (2007) Phaseolus texensis (Leguminosae: Phaseolinae): A new species from the Edwards Plateau of Central Texas. Lundellia 10: 11–17.
  71. 71. Salcedo CJ, Lépiz RI, Castañeda NA, Ocampo CN, Debouck DG (2009) Additional Observations about Phaseolus rotundatus (Fabaceae), An Endemic Bean Species from Western Mexico. Journal of the Botanical Research Institute of Texas 3(2): 751–762.
  72. 72. Hijmans RJ, Cameron SE, Parra JL, Jones PG, Jarvis A (2005) Very high resolution interpolated climate surfaces for global land areas. International Journal of Climatology 25: 1965–1978.
  73. 73. Busby JR (1991) BIOCLIM – a bioclimatic analysis and prediction system. In: Margules CR, Austin MP, editors. Nature conservation: cost effective biological surveys and data analysis. Canberra, Australia: Commonwealth Scientific and Industrial Research Organisation (CSIRO). pp. 64–68.
  74. 74. Wisz MS, Hijmans RJ, Li J, Peterson AT, Graham CH, et al. (2008) Effects of sample size on the performance of species distribution models. Diversity and Distributions 14: 763–773.
  75. 75. Lobo JM, Jimenez-Valverde A, Hortal J (2010) The uncertain nature of absences and their importance in species distribution modeling. Ecography 33: 103–114.
  76. 76. Jimenez-Valverde A, Lobo JM, Hortal J (2008) Not as good as they seem: the importance of concepts in species distribution modelling. Diversity and Distributions 14: 885–890.
  77. 77. Fitzpatrick MC, Hargrove WW (2009) The projection of species distribution models and the problem of non-analog climate. Biodiversity Conservation 18: 2255–2261.
  78. 78. Termansen M, McClean CJ, Preston CD (2006) The use of genetic algorithms and Bayesian classification to model species distributions. Ecological Modelling 192: 410–424.