Essential Biodiversity Variables: Integrating In-Situ Observations and Remote Sensing Through Modeling
- 4.1k Downloads
Essential biodiversity variables (EBVs) are designed to support the detection and quantification of biodiversity change and to define priorities in biodiversity monitoring. Unlike most primary observations of biodiversity phenomena, EBV products should provide information readily available to produce policy-relevant biodiversity indicators, ideally at multiple spatial scales, from global to subnational. This information is typically complex to produce from a single set of data or type of observation, thus requiring approaches that integrate multiple sources of in situ and remote sensing (RS) data. Here we present an up-to-date EBV concept for biodiversity data integration and discuss the critical components of workflows for EBV production. We argue that open and reproducible workflows for data integration are critical to ensure traceability and reproducibility so that each EBV endures and can be updated as novel biodiversity models are adopted, new observation systems become available, and new data sets are incorporated. Fulfilling the EBV vision requires strengthening efforts to mobilize massive amounts of in situ biodiversity data that are not yet publicly available and taking full advantage of emerging RS technologies, novel biodiversity models, and informatics infrastructures, in alignment with the development of a globally coordinated system for biodiversity monitoring.
Which facets of biodiversity are changing, and what is the magnitude and direction of these changes? How is biodiversity responding to the variety of human pressures? Are the management policies put into place effective to tackle the impact of those pressures? While the scientific community has been addressing these questions for decades, the information gap in biodiversity science remains a major obstacle for reducing the large uncertainties associated with answering those questions. Technological advances, collection of data by an increasing number of scientists and volunteer citizens, and increased access to Earth observations (EO) should help reduce this gap. Yet quantitative information is still limited, as has been its ability to inform important international commitments such as the Aichi Biodiversity Targets in response to the global biodiversity crisis (Tittensor et al. 2014). Data collection and monitoring protocols are often adopted by scientists, public administrations, and environmental organizations with no effective international coordination, and there is no consensus on adopting priority metrics to quantify biodiversity change. While strengthening efforts to reduce the multiple biases present in biodiversity data remains critical (including spatial, temporal, and taxonomic biases, among others; Meyer et al. 2016; Proença et al. 2017), parallel efforts are needed to consolidate data from in-situ and remote sensing (RS) EO so as to increase their usability and information value.
The concept of essential biodiversity variables (EBVs) was proposed in 2013 as a framework to prioritize, integrate, and consolidate biodiversity observations and monitoring programs worldwide (Pereira et al. 2013). Since then, EBVs have gained acceptance among scientists, along with the interest and endorsement of the policy-making community, including the Convention on Biological Diversity (e.g., Decision XI/3 in UNEP/CBD/COP/11/35) and the Intergovernmental Science-Policy Platform on Biodiversity and Ecosystem Services (IPBES). By providing an integrative framework for quantifying biodiversity change in time, EBVs also hold great potential for advancing research on biodiversity and responses to pressures and conservation actions. However, the concept is still evolving, and divergent viewpoints have emerged on what actually constitutes an EBV. Here we discuss recent progress in defining an operational EBV framework and the importance of this framework for biodiversity data integration. We start with discussing key attributes of EBVs. We then describe recent conceptual developments in support of their implementation. Finally, we illustrate the role of biodiversity models as a cornerstone for integrating data obtained from in-situ and satellite RS EO to support global assessments of biodiversity change and as a critical component of a global biodiversity monitoring system (Geller et al., Chap. 20).
18.2 The EBV Framework
18.2.1 Definition of Essential Biodiversity Variables
EBVs are defined as a minimum set of complementary measurements needed to detect and document biodiversity change across all levels of biodiversity, from genes to species and ecosystems (Pereira et al. 2013). EBVs are part of a larger family of Essential Variables (EVs) that was first conceptualized by the climate community with the Essential Climate Variables (Box 18.1).
Like all EVs, EBVs must meet the criteria of feasibility, cost-effectiveness, and scientific and policy relevance. Additional characteristics that might be specific to the EBVs are generalization (to the best extent possible) across terrestrial, marine, and freshwater realms and scalability. Importantly, the EBVs evolved from initially covering multiple aspects of the Driver-Pressure-State-Impact-Response (DPSIR) framework to focusing exclusively on biological state variables (i.e., EBVs describe the condition or the status of a particular biological entity). This is not to say that nonbiological variables are irrelevant for EBVs. On the contrary, some of these variables, such as temperature, fire occurrence, or elevation, may be extremely important (e.g., as covariates in biodiversity models); however, they do not constitute EBVs themselves. Furthermore, EBVs can be analyzed in relation to other variables to attribute biodiversity change to specific pressures and drivers (Pereira et al. 2012), to predict how different biodiversity metrics might behave with different scenarios of change (Kim et al. 2018), and to assess the effectiveness of management policies for biodiversity and ecosystem services (Geijzendorffer et al. 2016).
Box 18.1 Essential Variables
Essential variables (EVs) emerged from the need for openly available data sets with transparent production processes that offer an appropriate spatial and temporal coverage to allow their use in policy- and decision-making (Bojinski et al. 2014). As a result, EVs are meant to allow the development of indicators that can support dynamic users’ needs while being resilient to changing and/or evolving observation systems (Reyers et al. 2017). From a pool of candidate variables, both science and technology will determine which are feasible, cost-effective, and, most importantly, relevant, and thus essential (Bojinski et al. 2014). In practice, although EVs can be interpreted and adapted differently among disciplines, the process of their development and endorsement remains similar, with a community of practice that self-organizes to provide both the scientific foundation (research, data, monitoring) and technical guidance to produce those EVs.
EVs were first adopted by the climate community as the Essential Climate Variables (ECVs) in the early 1990s, to respond to the needs of Parties of the United Nations Framework Convention on Climate Change and the Intergovernmental Panel on Climate Change, but the concept has since been expanded to go beyond climate science, including with the Essential Biodiversity Variables (EBVs) and the Essential Ocean Variables (EOVs, Miloslavich et al. 2018). While there is value in increasingly expanding the concept to other domains, a coordinated approach within disciplines to define and prioritize the EVs and avoid the duplication of efforts is currently being discussed within the Group on Earth Observations (GEO). One example is the joint effort by the Marine Biodiversity Observation Network of the Group on Earth Observations Biodiversity Observation Network (GEO BON) and the Global Ocean Observing System (GOOS) of the Intergovernmental Oceanographic Commission (IOC) to streamline the marine observations that underpin the EBVs and EOVs (Muller-Karger et al. 2018b). The discussion on EVs is also permeating other domains, such as agriculture, health, and disaster risk reduction (Reyers et al. 2017).
18.2.2 A Space-Time-Biology Cube
The data structure of an EBV can be described as a hypercube and has analogy to a multidimensional data array in computer programming. The first two dimensions of the hypercube are space (latitude and longitude) and time, while the third dimension represents biological entities (Fig. 18.1). The latter dimension can, for instance, describe taxonomy in a species-centered EBV (see below), and values will inform the presence/absence or population abundance (e.g., Kissling et al. 2018a). Unlike the Essential Climate Variables (ECVs), the biological dimension of the EBVs makes them especially challenging in terms of developing the conceptual framework and producing the EBV data products. For ecosystem-level EBVs, this dimension can also inform ecosystem structure metrics (e.g., extent of different habitat types) or functions (e.g., primary productivity) in the time-space coordinates. The hypercube thus provides an intuitive representation of the EBV concept and at the same time has a direct translation in data computing language that suits implementation. Other EBVs are also more challenging to represent with three dimensions, even more so when considering that their value is likely to change depending on the spatial scale and extent, as is the case for the community spatial turnover.
18.2.3 Six EBV Classes
Each EBV measures a particular attribute (property) of a given entity (object). EBVs are grouped into six broad classes based on similarities and differences in the attributes and entities they address (Fig. 18.2). These classes are sets of variables describing the structure, composition, and function of biodiversity across its hierarchical levels (Noss 1990). The entity addressed by an EBV can be of two broad types, distinguished by the approach used to define the set of organisms forming this entity.
In the first approach, entities are formed by grouping organisms primarily on the basis of their species identity. In other words, EBVs of this broad type measure particular attributes of species—i.e., genetic diversity within a species in the case of the Genetic Composition Class; distribution and abundance of a species in the Species Populations Class; and traits of a species in the Species Traits Class.
The second approach to forming entities involves grouping organisms primarily on the basis of where they occur. EBVs of this broad type measure collective attributes of the entire ecosystem formed by all of the organisms occurring within a defined area (most typically an individual cell within a regular grid)—i.e., structural attributes of the ecosystem in the case of the Ecosystem Structure Class; functional attributes of the ecosystem in the Ecosystem Function Class; and various dimensions of compositional diversity (e.g., taxonomic, genetic/phylogenetic, functional) of organisms occurring within the ecosystem in the Community Composition Class.
The relationships between these six EBV classes is depicted in Fig. 18.2. A few key aspects of this overall typology are worth noting. First, the two broad approaches to defining the entity addressed by an EBV, species-focused and ecosystem-focused, essentially work with the same pool of individual organisms but view these organisms from two different perspectives—one grouping organisms according to species identity and the other according to location. While the entity employed in species-focused EBVs will typically be defined primarily on the basis of species identity, this could in some instances be qualified to focus, for example, on the population of a species occurring in a particular area. Likewise, ecosystem-focused EBVs might, in some instances, focus on measuring collective attributes of a particular subset of organisms occurring in an ecosystem rather than all organisms, with this subset defined in terms of taxonomy (e.g., all birds) or any other trait of interest (e.g., all pollinators). Finally, it is important to caution against directly equating the species-focused versus ecosystem-focused typology with major sources of in-situ versus RS observation. Many different sources and types of data can, and should, contribute to the population of EBVs across this entire framework. Any given EBV class can typically be populated using data from multiple sources of in-situ and remote-sensing observation, and any given source will typically contribute data to more than one EBV class. For example, EBVs in the Community Composition Class could be populated with data both from RS of compositional diversity (e.g., Morsdorf et al., Chap. 4) and from aggregation of in-situ species observations and models (e.g., Pinto-Ledezma and Cavender-Bares, Chap. 9), with the latter also contributing data simultaneously to the Species Populations Class.
18.3 Production Workflows for EBVs
The estimation of EBV information products typically involves multiple levels of data integration, from the collection of raw observations to the production of a final, consistent information set that provides comparable measurements in space and time. Data integration procedures need to be customized for almost every EBV, since they need to accommodate highly diverse biological quantities that are often specific to a particular EBV. Designing open, consistent, and fully reproducible workflows is key to support the full operationalization process, from data collection to publication of an EBV product that is ready to use for multiple science and policy purposes.
18.3.1 The Need for Open EBV Workflows
Workflows are defined as precise descriptions of data processing from one analytical step to another in a formal language. In recent years a multiplication of biodiversity data availability, novel analytical capabilities, and virtual infrastructures have laid the foundations for producing better integrated and more detailed information for measuring biodiversity change (e.g., Jetz et al. 2012; Hansen et al. 2013). However, the increasing variety of analytical procedures and project-specific designs also means that analytical standards are difficult to establish (Borregaard and Hart 2016). Open workflows benefit the preservation of processing steps and support data interoperability and the automation of biological and environmental data integration (e.g., via virtual biodiversity e-infrastructures; La Salle et al. 2016). These workflows require provenance of derived products to be also recorded so others can understand the relationships among data, processing, and results (Michener and Jones 2012) and thus facilitate product updating as new data and better processing algorithms become available. All these aspects are critical in the EBV framework since the production of EBVs depends on large research collaborations built on the basis of knowledge transfer and open access to data and production protocols.
At present, fully operational workflows that facilitate the automated and widespread production of EBVs are missing. However, recent efforts have identified critical steps and bottlenecks for the definition of workflows in support of the production of specific EBVs.
18.3.2 From Data Collection to Biodiversity Models
Generic workflows have been outlined so far for the production of a few species-centered EBVs, including species distributions, population abundances, and species traits (Kissling et al. 2018a, b). For example, 11 steps have been identified to build spatially continuous and temporally consistent EBV products for species distributions, from the integration of multiple data sources, including traditional direct species observations collected in many different ways, automated records from sensor networks—such as camera traps and sound detection—and emerging uses of satellite remote sensing (RS) for detecting species (Kissling et al. 2018a). These workflows pay special attention to the integration among in-situ observations and RS data. Other approaches may use in-situ observations only as ground-truth data, while the rest of the process is dominated by image processing (e.g., mapping vegetation cover; Hansen et al. 2013). However, traceability of the ground-truth sampling and processing remains equally important and therefore also applies to the entire process similar principles of annotation, uncertainty reporting, and conformance with data management guidelines (see below).
Standardization of primary biodiversity observations. At the core of the EBV concept is the aggregation of primary observations from multiple sources into a harmonized product that provides more comprehensive and richer information than each individual data set. Before this aggregation can take place, primary data must be curated, standardized, and annotated with appropriate metadata that record characteristics such as location, time, measurement units, and, ideally, sampling designs, collection procedures, and data quality control procedures (Rüegg et al. 2014). For example, for Species Populations EBVs, harmonized observations would consist of sets of species occurrence and abundance data expressed in appropriate units (such as species occupancies and number of individuals per unit area, respectively) complemented with metadata in appropriate standards such as the “Darwin Core Standard” with the “Event Core” extension (Wieczorek et al. 2012), which makes it possible to capture monitoring protocols and sampling efforts together with the data (https://www.gbif.org/darwin-core). Full documentation of sampling events using adequate metadata standards not only is critical for facilitating reuse of data by secondary users but also provides important information for quantifying the associated uncertainty and eventually applying correction techniques in subsequent steps. In practice, for a decade or so, the critical importance of annotating data with standard metadata has guided data management practices (e.g., in the context of long-term ecological research networks; Michener et al. 2011). However, poor data practices that ignore the annotation of metadata or that fail to adopt interoperable formats are still common for many biodiversity data sets, including those accessible through public data archives of scientific journals (Roche et al. 2015). These deficiencies constitute a major bottleneck for building EBVs (Hugo et al. 2017).
Primary data aggregation. A second set of steps leads to the production of consolidated data products that typically conform to all or most of the following characteristics: They contain consistent biological quantities expressed in the same measurement unit; other relevant biological attributes have been checked and harmonized (e.g., into a harmonized taxonomy or a consistent typology of traits or of ecosystem types); spatial and temporal references are matched; and data uncertainties have been quantified. Standardized observations need to be checked at this stage using quality control (QC) mechanisms that are documented transparently (Rüegg et al. 2014), for example, looking at outliers to ensure data quality. Collation of data in support of user requirements will ideally be automated using virtual infrastructures that are able to map the different (standardized) data sets with metadata into fully interoperable formats (Hugo et al. 2017). As detailed in Kissling et al. (2018b), an excellent example of this for the Species Traits EBVs is the Global Plant Phenology Data Portal (https://www.plantphenology.org), a platform that integrates phenology observations from three different networks using disparate data frameworks (Stucky et al. 2018). Key for this integration was the design of a new “Plant Phenology Ontology” that was able to provide a semantic framework as a basis to overcome interoperability problems produced by network-specific terminologies for data recording. Finally, data integration needs to deal with, and report on, uncertainties resulting from errors that may propagate throughout the different EBV production steps, including uncertain geographic locations of in-situ data, heterogeneous sampling methods and efforts (Proença et al. 2017), and measurement errors.
Model-based estimation. Final EBV products ideally provide continuous information in space and at different time periods so biodiversity change can be measured throughout the entire spatial domain. This is the case for EBVs that can be directly estimated using algorithms applied to satellite RS imagery with complete area coverage. On the contrary, for many EBVs that are primarily estimated from in-situ data, an additional level of integration is required to overcome the sparsity of data. Biodiversity models provide this level of integration by combining the strengths of in-situ observations and state-of-the-art RS products based on correlative or deductive approaches (Jetz et al. 2012; Ferrier et al. 2017). For instance, species distribution models are often based on a correlative relationship between environmental variables and the probability of the occurrence of a species. These models are calibrated or trained using species occurrence and sometimes absence data as response variables and environmental variables as predictors. The probability of occurrence of a species can be spatially interpolated between the observation points because environmental variables are available as continuous surfaces (i.e., wall-to-wall), which are themselves generated from models using in-situ and EO data. In deductive habitat modeling, expert-based assessment of the habitat preference and environmental constraints of species is used to refine the potential species distribution. When habitat predictors are available in high resolution, this makes it possible to go from coarse potential species distributions to fine-grain species distributions because species also respond more locally to habitat variables than to, for instance, climate (Triviño et al. 2011; Martins et al. 2014). Other EBVs can also be projected with models that integrate in-situ observations with RS data and other environmental data. Community composition variables such as the beta diversity between two sites can be projected from climate and other variables using generalized dissimilarity models (Ferrier et al. 2007), while alpha and gamma diversity can be projected from land-use using the countryside species-area model (Pereira and Borda-de-Água 2013). Hence, environmental predictors derived from RS constitute the backbone of higher-resolution EBV products that are consistent in space and time. However, it is important to note that such model-based EBVs provide information that is fundamentally different from the aggregated data sets described in the preceding steps and that while it improves the spatial and temporal coverage of the data set, it also introduces additional uncertainties that need to be documented.
Massive integration of biodiversity data based on the EBV framework and workflows requires implementation via interoperable informatics infrastructures (Hugo et al. 2017). Projects aligned with the mission and concepts of EBVs, such as Map of Life (www.mol.org) or the Biogeographic Infrastructure for Large-scaled Biodiversity Indicators (BILBI) (Hoskins et al. 2018), already constitute a proof of concept of the potential of virtual infrastructures for developing a biodiversity-modeling framework that delivers global information from multi-sourced EO data integration. While the technological implementation of these infrastructures should not constitute a major limitation, redoubled efforts are needed, first, on making the large amounts of in-situ data being collected available and interoperable and, second, on developing and adapting biodiversity models that are able to ingest massive and novel sources of data, both in-situ (e.g., eDNA data) and RS (e.g., imaging spectroscopy).
18.3.3 Access Principles
In addition, GEO BON is developing an “Essential Biodiversity Variables Portal” that supports this process and enhances accessibility to EBV products. Open distribution of these products is complemented by reporting on their compliance with a set of “EBV Minimum Information Standards”. Besides ensuring good data management practices, these information standards aim to provide a guideline for the standardized description of EBV products. The purpose is to ensure consistent information about the EBV hypercube (i.e., the attributes of space, time, biological entity, and uncertainties) among the different EBV classes so that final users can easily access the relevant information (e.g., when searching for suitable EBVs for specific indicators).
18.4 Seamless Integration of Past Trends to Future Scenarios Using EBVs
Recently, a set of EBVs was historically reconstructed and projected into the future in an inter-model comparison study carried out by the Expert Group on Scenarios and Models of the Intergovernmental Platform on Biodiversity and Ecosystem Services (Kim et al. 2018). Species distribution, community composition, ecosystem function variables, and ecosystem services variables were reconstructed since 1900 and projected to 2050 globally, at a 0.5° resolution, using harmonized land-use data sets developed for the shared-socioeconomic pathways and climate data sets for the relative concentration pathway scenarios. In this exercise, a space-for-time substitution was used in the biodiversity models. In other words, no explicit time series biodiversity data were used to calibrate the models. Instead, current spatial patterns of biodiversity and drivers were used to infer how biodiversity changes over time when driver variables change. A future challenge for biodiversity modelers is to use biodiversity time series to fully model biodiversity across space and time (Ferrier et al. 2017).
18.5 Concluding Remarks
Since EBVs were first defined, there have been significant advances in the consolidation of the framework, substantial conceptual work on implementation, and increasing enthusiasm about their many potential applications in biodiversity science and policy. Now the scientific community needs to face the challenge of delivering EBV products and workflows that provide estimates of changes for the main facets of biodiversity and support our understanding of the driving mechanisms and the consequences of such changes. There are important opportunities for mobilizing primary data offered by the open-access movement, which continue to permeate the biodiversity community. These include public institutions responsible for promoting scientific and technological advancement. Data gaps will be covered by combining technological development with appropriate biodiversity models. For example, spaceborne sensors such as the Global Ecosystem Dynamics Investigation (GEDI) Lidar launched in 2018 are providing unprecedented global coverage in vertical measurements of vegetation and topography and will most likely support model-based integration of information for biodiversity variables in unforeseen ways.
Fulfilling the EBV vision requires renewed efforts, first, in continued scientific and technological support for the mobilization of in-situ data and for designing more comprehensive and better coordinated monitoring schemes and, second, in the implementation of workflows and interoperable infrastructures that support wall-to-wall integration of biodiversity data. GEO BON as a network defined at multiple levels, from scientific to institutional and infrastructure support, is instrumental for this endeavor (Hugo et al. 2017; Navarro et al. 2017). Key priorities are the implementation of mechanisms that enhance data mobilization as exemplified by the Darwin Event Core; a common understanding between the biodiversity research community and the space agencies of the processes to develop the technology required for detecting biodiversity change (Paganini et al. 2016); global informatics infrastructure support that meets the requirements for operationalizing EBVs (Hardisty et al. 2019); and broad scientific cooperation in implementing and enhancing biodiversity models that integrate all types of Earth observations.
- Bush A, Sollmann R, Wilting A, Bohmann K, Cole B, Balzter H, Martius C, Zlinszky A, Calvignac-Spencer S, Cobbold CA, Dawson TP, Emerson BC, Ferrier S, Gilbert MTP, Herold M, Jones L, Leendertz FH, Matthews L, Millington JDA, Olson JR, Ovaskainen O, Raffaelli D, Reeve R, Rödel M-O, Rodgers TW, Snape S, Visseren-Hamakers I, Vogler AP, White PCL, Wooster MJ, Yu DW (2017) Connecting earth observation to high-throughput biodiversity data. Nat Ecol Evol 1:0176CrossRefGoogle Scholar
- ConnectinGEO (2015) Deliverable D2.2 EVs current status in different communities and way to move forward. CREAFGoogle Scholar
- Geijzendorffer IR, Regan EC, Pereira HM, Brotons L, Brummitt N, Gavish Y, Haase P, Martin CS, Mihoub J-B, Secades C, Schmeller DS, Stoll S, Wetzel FT, Walters M (2016) Bridging the gap between biodiversity data and policy reporting needs: an essential biodiversity variables perspective. J Appl Ecol 53:1341–1350CrossRefGoogle Scholar
- GEO BON (2015) Global biodiversity change indicators: model-based integration of remote-sensing & in situ observations that enables dynamic updates and transparency at low cost. GEO BON Secretariat, LeipzigGoogle Scholar
- Haase P, Tonkin JD, Stoll S, Burkhard B, Frenzel M, Geijzendorffer IR, Häuser C, Klotz S, Kühn I, McDowell WH, Mirtl M, Müller F, Musche M, Penner J, Zacharias S, Schmeller DS (2018) The next generation of site-based long-term ecological monitoring: linking essential biodiversity variables and ecosystem integrity. Sci Total Environ 613–614:1376–1384CrossRefGoogle Scholar
- Hardisty AR, Michener WK, Agosti D, Alonso García E, Bastin L, Belbin L, Bowser A, Buttigieg PL, Canhos DAL, Egloff W, De Giovanni R, Figueira R, Groom Q, Guralnick RP, Hobern D, Hugo W, Koureas D, Ji L, Los W, Manuel J, Manset D, Poelen J, Saarenmaa H, Schigel D, Uhlir PF, Kissling WD (2019) The Bari manifesto: an interoperability framework for essential biodiversity variables. Eco Inform 49:22–31CrossRefGoogle Scholar
- Hoskins AJ, Harwood TD, Ware C, Williams KJ, Perry JJ, Ota N, Croft JR, Yeates DK, Jetz W, Golebiewski M, Purvis A, Ferrier S (2018) Supporting global biodiversity assessment through high-resolution macroecological modelling: Methodological underpinnings of the BILBI frameworkGoogle Scholar
- Kim H, Rosa IMD, Alkemade R, Leadley P, Hurtt G, Popp A, van Vuuren DP, Anthoni P, Arneth A, Baisero D, Caton E, Chaplin-Kramer R, Chini L, De Palma A, Di Fulvio F, Di Marco M, Espinoza F, Ferrier S, Fujimori S, Gonzalez RE, Gueguen M, Guerra C, Harfoot M, Harwood TD, Hasegawa T, Haverd V, Havlík P, Hellweg S, Hill SLL, Hirata A, Hoskins AJ, Janse JH, Jetz W, Johnson JA, Krause A, Leclère D, Martins IS, Matsui T, Merow C, Obersteiner M, Ohashi H, Poulter B, Purvis A, Quesada B, Rondinini C, Schipper A, Sharp R, Takahashi K, Thuiller W, Titeux N, Visconti P, Ware C, Wolf F, Pereira HM (2018) A protocol for an intercomparison of biodiversity and ecosystem services models using harmonized land-use and climate scenarios. Geosci Model Dev Discuss:1–37Google Scholar
- Kissling WD, Ahumada JA, Bowser A, Fernandez M, Fernández N, García EA, Guralnick RP, Isaac NJB, Kelling S, Los W, McRae L, Mihoub J-B, Obst M, Santamaria M, Skidmore AK, Williams KJ, Agosti D, Amariles D, Arvanitidis C, Bastin L, De Leo F, Egloff W, Elith J, Hobern D, Martin D, Pereira HM, Pesole G, Peterseil J, Saarenmaa H, Schigel D, Schmeller DS, Segata N, Turak E, Uhlir PF, Wee B, Hardisty AR (2018a) Building essential biodiversity variables (EBVs) of species distribution and abundance at a global scale: building global EBVs. Biol Rev 93:600–625CrossRefGoogle Scholar
- Kissling WD, Walls R, Bowser A, Jones MO, Kattge J, Agosti D, Amengual J, Basset A, van Bodegom PM, Cornelissen JHC, Denny EG, Deudero S, Egloff W, Elmendorf SC, Alonso García E, Jones KD, Jones OR, Lavorel S, Lear D, Navarro LM, Pawar S, Pirzl R, Rüger N, Sal S, Salguero-Gómez R, Schigel D, Schulz K-S, Skidmore A, Guralnick RP (2018b) Towards global data products of essential biodiversity variables on species traits. Nat Ecol Evol 2:1531–1540CrossRefGoogle Scholar
- Miloslavich P, Bax NJ, Simmons SE, Klein E, Appeltans W, Aburto-Oropeza O, Garcia MA, Batten SD, Benedetti-Cecchi L, Checkley DM, Chiba S, Duffy JE, Dunn DC, Fischer A, Gunn J, Kudela R, Marsac F, Muller-Karger FE, Obura D, Shin Y-J (2018) Essential Ocean variables for global sustained observations of biodiversity and ecosystem changes. Glob Chang Biol 24:2416–2433CrossRefGoogle Scholar
- Muller-Karger FE, Hestir E, Ade C, Turpie K, Roberts DA, Siegel D, Miller RJ, Humm D, Izenberg N, Keller M, Morgan F, Frouin R, Dekker AG, Gardner R, Goodman J, Schaeffer B, Franz BA, Pahlevan N, Mannino AG, Concha JA, Ackleson SG, Cavanaugh KC, Romanou A, Tzortziou M, Boss ES, Pavlick R, Freeman A, Rousseaux CS, Dunne J, Long MC, Klein E, McKinley GA, Goes J, Letelier R, Kavanaugh M, Roffer M, Bracher A, Arrigo KR, Dierssen H, Zhang X, Davis FW, Best B, Guralnick R, Moisan J, Sosik HM, Kudela R, Mouw CB, Barnard AH, Palacios S, Roesler C, Drakou EG, Appeltans W, Jetz W (2018a) Satellite sensor requirements for monitoring essential biodiversity variables of coastal ecosystems. Ecol Appl 28:749–760CrossRefGoogle Scholar
- Muller-Karger FE, Miloslavich P, Bax NJ, Simmons S, Costello MJ, Sousa Pinto I, Canonico G, Turner W, Gill M, Montes E, Best BD, Pearlman J, Halpin P, Dunn D, Benson A, Martin CS, Weatherdon LV, Appeltans W, Provoost P, Klein E, Kelble CR, Miller RJ, Chavez FP, Iken K, Chiba S, Obura D, Navarro LM, Pereira HM, Allain V, Batten S, Benedetti-Checchi L, Duffy JE, Kudela RM, Rebelo L-M, Shin Y, Geller G (2018b) Advancing marine biological observations and data requirements of the complementary essential ocean variables (EOVs) and essential biodiversity variables (EBVs) frameworks. Front Mar Sci 5:211CrossRefGoogle Scholar
- Navarro LM, Fernández N, Guerra C, Guralnick R, Kissling WD, Londoño MC, Muller-Karger F, Turak E, Balvanera P, Costello MJ, Delavaud A, El Serafy G, Ferrier S, Geijzendorffer I, Geller GN, Jetz W, Kim E-S, Kim H, Martin CS, McGeoch MA, Mwampamba TH, Nel JL, Nicholson E, Pettorelli N, Schaepman ME, Skidmore A, Sousa Pinto I, Vergara S, Vihervaara P, Xu H, Yahara T, Gill M, Pereira HM (2017) Monitoring biodiversity change through effective global coordination. Curr Opin Environ Sustain 29:158–169CrossRefGoogle Scholar
- Pereira HM, Borda-de-Água L (2013) Modeling biodiversity dynamics in countryside and native habitats. In: Encyclopedia of biodiversity. Elsevier, San Diego, pp 321–328Google Scholar
- Pereira HM, Ferrier S, Walters M, Geller GN, Jongman RHG, Scholes RJ, Bruford MW, Brummitt N, Butchart SHM, Cardoso AC, Coops NC, Dulloo E, Faith DP, Freyhof J, Gregory RD, Heip C, Hoft R, Hurtt G, Jetz W, Karp DS, McGeoch MA, Obura D, Onoda Y, Pettorelli N, Reyers B, Sayre R, Scharlemann JPW, Stuart SN, Turak E, Walpole M, Wegmann M (2013) Essential biodiversity variables. Science 339:277–278CrossRefGoogle Scholar
- Proença V, Martin LJ, Pereira HM, Fernandez M, McRae L, Belnap J, Böhm M, Brummitt N, García-Moreno J, Gregory RD, Honrado JP, Jürgens N, Opige M, Schmeller DS, Tiago P, van Swaay CAM (2017) Global biodiversity monitoring: from data sources to essential biodiversity variables. Biol Conserv 213:256–263CrossRefGoogle Scholar
- Tittensor DP, Walpole M, Hill SLL, Boyce DG, Britten GL, Burgess ND, Butchart SHM, Leadley PW, Regan EC, Alkemade R, Baumung R, Bellard C, Bouwman L, Bowles-Newark NJ, Chenery AM, Cheung WWL, Christensen V, Cooper HD, Crowther AR, Dixon MJR, Galli A, Gaveau V, Gregory RD, Gutierrez NL, Hirsch TL, Hoft R, Januchowski-Hartley SR, Karmann M, Krug CB, Leverington FJ, Loh J, Lojenga RK, Malsch K, Marques A, Morgan DHW, Mumby PJ, Newbold T, Noonan-Mooney K, Pagad SN, Parks BC, Pereira HM, Robertson T, Rondinini C, Santini L, Scharlemann JPW, Schindler S, Sumaila UR, Teh LSL, van Kolck J, Visconti P, Ye Y (2014) A mid-term analysis of progress toward international biodiversity targets. Science 346:241–244CrossRefGoogle Scholar
Open Access This chapter is licensed under the terms of the Creative Commons Attribution 4.0 International License (http://creativecommons.org/licenses/by/4.0/), which permits use, sharing, adaptation, distribution and reproduction in any medium or format, as long as you give appropriate credit to the original author(s) and the source, provide a link to the Creative Commons license and indicate if changes were made.
The images or other third party material in this chapter are included in the chapter's Creative Commons license, unless indicated otherwise in a credit line to the material. If material is not included in the chapter's Creative Commons license and your intended use is not permitted by statutory regulation or exceeds the permitted use, you will need to obtain permission directly from the copyright holder.