- Open Access
Where did they not go? Considerations for generating pseudo-absences for telemetry-based habitat models
Movement Ecology volume 9, Article number: 5 (2021)
Habitat suitability models give insight into the ecological drivers of species distributions and are increasingly common in management and conservation planning. Telemetry data can be used in habitat models to describe where animals were present, however this requires the use of presence-only modeling approaches or the generation of ‘pseudo-absences’ to simulate locations where animals did not go. To highlight considerations for generating pseudo-absences for telemetry-based habitat models, we explored how different methods of pseudo-absence generation affect model performance across species’ movement strategies, model types, and environments.
We built habitat models for marine and terrestrial case studies, Northeast Pacific blue whales (Balaenoptera musculus) and African elephants (Loxodonta africana). We tested four pseudo-absence generation methods commonly used in telemetry-based habitat models: (1) background sampling; (2) sampling within a buffer zone around presence locations; (3) correlated random walks beginning at the tag release location; (4) reverse correlated random walks beginning at the last tag location. Habitat models were built using generalised linear mixed models, generalised additive mixed models, and boosted regression trees.
We found that the separation in environmental niche space between presences and pseudo-absences was the single most important driver of model explanatory power and predictive skill. This result was consistent across marine and terrestrial habitats, two species with vastly different movement syndromes, and three different model types. The best-performing pseudo-absence method depended on which created the greatest environmental separation: background sampling for blue whales and reverse correlated random walks for elephants. However, despite the fact that models with greater environmental separation performed better according to traditional predictive skill metrics, they did not always produce biologically realistic spatial predictions relative to known distributions.
Habitat model performance may be positively biased in cases where pseudo-absences are sampled from environments that are dissimilar to presences. This emphasizes the need to carefully consider spatial extent of the sampling domain and environmental heterogeneity of pseudo-absence samples when developing habitat models, and highlights the importance of scrutinizing spatial predictions to ensure that habitat models are biologically realistic and fit for modeling objectives.
Animal telemetry has revolutionized our understanding of animal movement and habitat use in both marine and terrestrial environments [29, 35]. Telemetry data have allowed for the exploration of behavioural and environmental drivers of animal space use, habitat selection, and migration [4, 39, 43, 49], and enabled the identification of important biological hotspots to inform conservation and management [14, 32, 55]. Animal telemetry data can also be used as inputs to habitat models (also known as ‘species distribution models’), to predict patterns of distribution or resource selection across space and time based on a species’ preference for particular characteristics of the environment . However, a fundamental challenge of using telemetry data in habitat models is that they are presence-only, and thus cannot be used to infer environmental drivers in areas where animals were absent. To address this, a variety of techniques exist to generate data representing where animals could have gone but did not go (i.e. ‘pseudo-absences’, e.g. ). However, the relative performances of different pseudo-absence generation methods have not yet been assessed for telemetry-based habitat models. Furthermore, the literature lacks an evaluation of the relative utility of pseudo-absence methods between marine and terrestrial systems, where differences in the scales of habitat heterogeneity may influence model outcomes.
Approaches for generating pseudo-absences range from simple (e.g., background sampling, [46, 54]) to complex [e.g., biased sampling, [9, 41]]. Background sampling is the most commonly used approach, which involves randomly sampling the entire study area or habitat extent to produce absences that represent a broad range of characteristics [37, 38, 46]. While background sampling is the backbone of presence-only modeling techniques such as Maxent , it does not consider how animals actually move through space and treats all areas and habitats as being equally accessible. To address this issue, approaches that explicitly incorporate information on animal movement have been developed, such as buffer sampling (analogous to ‘step selection’ [7, 19, 60]. This approach treats habitat selection as a series of step-by-step decisions, with pseudo-absences randomly sampled within a predetermined step-length from each presence location. A third approach is to create pseudo-absences that have the same autocorrelation structure as actual tracks using correlated random walks (CRWs) [1, 30, 31, 42, 67]. CRWs recreate movement patterns using sampled step-lengths and turn angles from interpolated animal tracks, in order to realistically simulate the movement characteristics of study species. CRWs can also be generated in reverse (reverse CRWs) to control for biases generated by non-random animal tagging locations .
In order to highlight key considerations for generating pseudo-absences for habitat models built from telemetry data, the effects and biases of pseudo-absence generation methods need to be explored across species’ movement strategies, model types, and environments. Here we examine pseudo-absence generation methods using two mobile megafauna, the blue whale (Balaenoptera musculus) and African elephant (Loxodonta africana). These two species forage near the base of the food web, yet inhabit completely different physical environments and employ different movement strategies [2, 8, 61]. In the Northeast Pacific, blue whales undertake basin-scale migrations from breeding to foraging grounds, while in Etosha National Park, Namibia, elephants move nomadically within the park boundaries. For each species, we compare the effects of four different pseudo-absence generation techniques (background sampling, buffer sampling, CRW and reverse CRW) on habitat model performance. We compare results across three model types commonly applied to telemetry data (generalised linear mixed models, generalised additive mixed models and boosted regression trees) to test if the relative performance of different pseudo-absence generation methods was robust across different model types.
We explored two previously published mega-vertebrate tracking datasets for Northeast Pacific blue whales and African elephants (Fig. 1). The blue whale data contained 10,664 daily locations in the eastern North Pacific, representing 104 ARGOS-tracked blue whales tracked between 1998 and 2009. This dataset has been studied extensively to identify critical habitat , understand patterns and drivers of migration [2, 8], and guide spatial management strategies [4, 30]. In this study, we examined foraging habitat selection by blue whales when resident in the central California Current System (CCS; 2,240,000 km2), excluding migratory behavior through Mexican waters and presumed breeding behavior in the southern end of their range. The elephant dataset contained 40,273 locations taken every 6 h from 14 GPS-collared elephants in Etosha National Park, Namibia (EtNP; 22,900 km2) between 2008 and 2014. These data have previously been used to explore animal movement syndromes  and drivers of habitat use .
We selected six out of twelve potential environmental variables for blue whales that have previously been shown to be important drivers of habitat use during migration and foraging [4, 30, 52]: sea surface temperature, the spatial variability of sea surface temperature (an index of frontal activity), sea level anomaly, chlorophyll-a, oxygen concentration at 100 m depth, and bathymetry (Table S1). For elephants, we selected three variables that have been shown to most strongly influence elephant movement in the study area (Table S1, ): distance to the nearest road, multiannual mean normalized difference vegetation index (NDVI), and distance to the nearest water source. The two study systems, the CCS and EtNP, have vastly different patterns of environmental dynamism. The CCS has strong seasonal upwelling driving cool, productive nearshore waters , with offshore waters characterized by ephemeral features like fronts and eddies that can shift at daily to weekly timescales . In contrast, EtNP experiences more gradual seasonal variation in temperature and rainfall . Accordingly, the environmental variables selected for modelling mirror this dynamism: dynamic variables for the CCS were acquired at a daily or monthly resolution, whereas EtNP variables were either static or long-term averages (in the case of NDVI).
We compared four methods of pseudo-absence generation that represent different assumptions about where animals could be distributed relative to observed tracks: ‘background sampling’, where random locations are sampled across the entire domain; ‘buffer sampling’, where random locations are sampled within a certain distance from each presence location; and ‘correlated random walks’ (CRW) and ‘reverse CRWs’, where tracks are simulated from given start or end points respectively, based on observed step lengths and turn angles. We outline each method below, and illustrate key concepts in Fig. 1.
Background sampling is designed to capture the full range of conditions under which species could be found, assuming they were distributed randomly across the environment. Habitat models are then used to contrast characteristics of preferred habitat where species are more likely to be observed, with this completely random distribution . This approach is adapted from systematic survey design ( and references therein), where individual presences are not assumed to be autocorrelated . Thus, even when applied to tracking data where each presence location depends on the one preceding it, background sampling of pseudoabsences incorporates no information or assumptions regarding characteristics of animal movement, such as distance traveled or direction of movement.
Buffer sampling for habitat modeling was originally used to minimize pseudo-absence overlap with presences, by sampling points outside a certain radius around each presence . However, more recent approaches use buffers to restrict the sampling domain to areas accessible by the animal, by sampling from within a given radius around a presence [10, 24]. For tracking data, buffer size has been determined based on the mean or median step-length (e.g. distance traveled between two positions over a set time interval), irrespective of direction . Resource selection functions use buffer sampling at each step to estimate the relative probability of selecting a specific parcel of habitat, relative to others that were equally accessible at that movement step .
CRWs and reverse CRWs sample the paired distribution of distance and turn angle from the empirical movement distributions in order to simulate realistic tracks (e.g. [1, 30]). CRWs have been used to create potential trajectories that animals could have taken based on measured movement parameters such as distance traveled and turning angle between consecutive locations . CRWs have been implemented particularly when animals are wide ranging and can access areas far from the original tagging location . In theory, CRWs offer the ability to create absences that best reflect the spatial and temporal auto-correlation of the actual tracks. Further, when there are implicit drivers of directionality or seasonality (e.g. movement away from competing colonies, or migration through less desirable habitat to reach more favorable habitat), entire CRW tracks can be selected that appropriately recreate important features of original tracks, such as the maximum displacement, or the mean angle of travel [30, 63]. Reverse CRWs have been introduced to address the issue of biases in tagging locations, recreating movement from the last known location and simulating backwards in time to the original tagging date .
We used a common sampling extent for all generation methods for each species based on the maximum extent of their tracks: for blue whales, a bounding box from 32° to 45° N and − 140° to − 115° W within the CCS; and for elephants the fenced boundary of EtNP (Fig. 1). For each pseudo-absence method, we generated a 1:1 ratio of pseudo-absences to presences to maintain consistency across models.
For background sampling, pseudo-absences were drawn randomly from within the domain for each species. For buffer sampling, we used the mode step length to create a radius of 100 km (whales) and 10 km (elephants) around each presence point, and randomly sampled one absence within each buffer zone. For CRWs, we randomly sampled a paired distance and turn angle from the observed distributions. Points were generated consecutively, starting from the locations where animals were tagged, until the number of pseudo-absences equaled the number of presences. The reverse CRW used the same approach but instead moved backwards in time from the last recorded position of the tag.
We selected three commonly used statistical correlative models to test how model type influenced the relative performance of the pseudo-absence generation methods. We selected generalised linear mixed models (GLMMs), which are parametric and estimate linear species-environment relationships; generalised additive mixed models (GAMMs) which are semi-parametric and use smoothers to represent non-linear species-environment relationships; and boosted regression trees (BRTs) which are non-parametric and use boosting to determine optimal partitioning of variance. For both GLMMs and GAMMs, we used the gamm function in the ‘mgcv’ R package  and included individual tag identification as a random effect. For GAMMs, we used a thin-plate spline smoother with knots set to 5 per variable. BRTs were fit using the gbm.fixed function in the ‘dismo’ R package  with a learning rate of 0.005, a bag fraction of 0.75, tree complexity of 5, and 2000 trees (following ).
We evaluated model performance holistically across three dimensions: explanatory power, predictive skill, and biological realism. Explanatory power indicates a model’s ability to explain the variability in a given dataset, and was evaluated using % explained deviance (R2). Predictive skill indicates a model’s ability to correctly predict species presence or absence on novel data, and was evaluated with Area Under the Receiver Operating Characteristic Curve (AUC) and True Skill Statistic (TSS, ). As independent validation data do not exist at the scale of the original data, we tested predictive skill using three cross-validation approaches: the first used 100% of the data for both model training and testing. The second used randomly subsampled 75% of the data to train models, with the remaining 25% used to test models. Third, we also trained models on 11 of 12 months, and withheld a single month (twelve times) for testing for the dynamic blue whale models. As the terrestrial predictors for elephants were static or climatological averages, we were unable to test a temporal leave-one-out approach. We present the 100% training and testing results so that inferences were consistent across validation approaches.
Previous work has identified that habitat model performance will increase as environmental dissimilarity between presences and absences increases . We explored this phenomenon by using density plots to qualitatively evaluate the environmental dissimilarity between presences and pseudo-absences generated by the four methods. Additionally, we quantified the statistical independence of the environmental niches of the presences and pseudo-absences for each variable and species using Bhattacharayya’s coefficient . To determine the effect of environmental dissimilarity on model performance, we used linear regression to test relationships between Bhattacharyya’s coefficient and model predictive skill (AUC) for the three most important predictor variables for each species.
Finally,  recommended supplementing evaluations of model performance with evaluations of biological realism based on expert opinion and published literature. Following this advice, we qualitatively evaluated the ability of the models to predict realistic patterns of species distributions by assessing spatial prediction maps using expert knowledge. Specifically, we considered spatial predictions biologically realistic for blue whales if they predicted inshore habitat along the coast and reproduced the known blue whale hotspot in the Southern California Bight during summer months [12, 18, 36]; we considered spatial predictions biologically realistic for elephants if they avoided predictions in the large salt pan in the northeast corner of EtNP and preferred areas closer to roads, water, and fences . We also quantified the ability of models to capture where blue whales and elephants are present and putatively absent by calculating mean predicted values at known presences and pseudo-absences, respectively.
Spatial and environmental separation of pseudo-absences and presences
Blue whale presences were clustered adjacent to the California coastline, with highest densities in the Southern California Bight (Fig. 1). Elephant presences were clustered in the southern portion of EtNP, and no presences were located within the large salt pan in the northeast corner of the park (Fig. 1). There was similar spatial separation between pseudo-absences and presences across the four generation methods for both species (Fig. 1). Background sampling - which randomly sampled pseudo-absences across the study area - resulted in the greatest spatial contrast between pseudo-absences and presences, with pseudo-absences sampled in offshore regions of the CCS, and in the salt pan and northern extent of EtNP (Fig. 1). Buffer sampling - which sampled pseudo-absences within 100 km and 10 km of blue whale and elephant presences, respectively, resulted in the lowest spatial contrast between pseudo-absences and presences, while CRW and reverse CRW resulted in intermediate spatial contrast (Fig. 1).
The separation of environmental variables between presence and pseudo-absence locations were similar to the spatial contrasts among pseudo-absence generation methods (Fig. 2). For blue whales, background sampling had the greatest environmental separation between presences and pseudo-absences for all variables, largely due to the preference of tracked animals for the nearshore 200 m depth contour and the strong onshore-offshore environmental gradients that were sampled by the pseudo-absences (Fig. 2a-d). For example, sea surface temperature had a single peak at 28 °C for background sampling, compared to double peaks around 28 °C and 16 °C in the presence data, CRW, reverse CRW, and buffer sampling (Fig. 2a). All pseudo-absence methods sampled deeper, more oxygenated waters with lower chlorophyll concentrations compared to the blue whale presences (Fig. 2b-d). The elephants showed less environmental separation between pseudo-absences and presences compared to blue whales, and fewer differences in separation among pseudo-absence methods (Fig. 2e-g). For elephants, buffer sampling resulted in the greatest environmental overlap between pseudo-absences and presences for the three predictor variables, whereas reverse CRW sampling had the lowest overlap with presences. Pseudo-absence methods generally sampled areas that were further from roads and water, and with lower NDVI values compared to where elephants were present (Fig. 2e-g). For both species, habitat model response curves highlighted how unique the environmental data range of background sampling was compared to the other pseudo-absence methods (Fig. S1).
Blue whale model performance was strongly driven by pseudo-absence type, with models built using background sampling having the best explanatory power, predictive skill, and ability to capture where blue whales are present (Table 1). CRWs were best able to capture where blue whales were absent (mean prediction at pseudo-absences). In contrast, elephant model performance was predominantly influenced by model type, with BRTs having the best explanatory power, predictive skill, and ability to capture where elephants were absent regardless of pseudo-absence type. This pattern of BRTs performing best was also apparent in blue whales, but to a lesser extent due to the large effect of pseudo-absence type (Table 1). Following BRTs, GAMMs outperformed GLMMs in terms of explanatory power and predictive skill for both species.
Environmental similarity between presences and pseudo-absences (Bhattacharyya’s coefficient) had a significant negative relationship (p < 0.05) with model predictive skill (AUC) for each model type and species (Fig. 3). That is, as the environments sampled by pseudo-absences became more similar to presence locations, model performance decreased. This pattern was also reflected in the relationship between Bhattacharyya’s coefficient and both TSS and R2 values (Table 1). The lowest Bhattacharyya’s coefficient (highest environmental separation) was found in blue whale background sampling, which also had the highest R2, AUC, and TSS values across all models and both species. Conversely, the highest Bhattacharyya’s coefficient (lowest environmental separation) was found in the elephant buffer sampling, which also had the lowest R2, AUC, and TSS values across all models and species (Table 1, Tables S1, S2). These results provide evidence that model explanatory power and predictive skill is strongly related to environmental separation between presences and absences, regardless of species or habitat model type.
Spatial predictions of species distributions showed divergent results across pseudo-absence generations methods and model types. For blue whales, background sampling predicted more uniformly suitable habitat on the continental shelf, whereas other pseudo-absence methods predicted higher inshore use. CRWs and reverse CRWs were best able to reproduce the known blue whale hotspot in the Southern California Bight during summer months [12, 18, 36]. In general, there was more consistency in spatial predictions among model types than among pseudo-absence generation methods (Fig. 4). For elephants, spatial differences among both pseudo-absence methods and model types were minimal, with all (except GAMM with buffer) reproducing low habitat selection inside the large salt pan in the northeast of the park (Fig. 5). The BRT model with highest predictive skill was reverse CRW, while background sampling was able to highlight areas of low habitat preference in the northern extent of the EtNP that matched patterns in the tracking data to a greater degree than the other sampling methods and model types (Fig. 5). Elephant BRTs captured fine-scale patterns of habitat use across pseudo-absence types, while GLMMs and GAMMs predicted smoother and more homogeneous distributions (Fig. 5).
A critical component of habitat modeling for presence-only data like animal telemetry is selecting pseudo-absence points that provide insight into how habitat selected by animals differs from the range of available habitat . Here we explored the performance of pseudo-absence generation techniques across species, study systems, and model types to help inform best practices for telemetry-based habitat modeling. We found that the environmental separation between presences and pseudo-absences was an important driver of model explanatory power and predictive skill - a result that held true across marine and terrestrial habitats, two species with different movement syndromes (migratory vs. nomadic), and three different model types. However, greater environmental separation between presences and pseudo-absences did not necessarily lead to greater biological realism in spatial predictions, highlighting the importance of using multiple inferences to evaluate model performance. Model performance metrics may be positively biased in cases where pseudo-absences are sampled from dissimilar habitats relative to those used by the study species, without a concurrent increase in the model’s ability to make accurate predictions of habitat use. This emphasizes the need to carefully consider the spatial extent of the sampling domain and environmental separation between presences and sampled pseudo-absences when developing habitat models.
Previous studies have demonstrated that model performance is influenced by study area extent and the proportion of this extent occupied by species, such that species that occupy small extents of a large study area are better predicted than species that occupy large extents of small study areas [44, 45, 62]. Separation in environmental niche space may dominate any differences between pseudo-absence generation approaches. For example,  found CRWs were less successful than background sampling. However, the study used CRWs only within the species’ domain and background sampling from outside the species’ domain to understand habitat use. Thus the separation between environmental conditions in the two sampling extents likely dominates any difference between pseudo-absence approach. Sampling across broad spatial and environmental gradients can be useful for identifying patterns of presence and absence and result in increased model performance, but may not be the most appropriate approach for understanding finer scale patterns of movement and habitat selection, highlighting the need to identify ecological questions and applications prior to modeling.
The four pseudo-absence methods differed in their ability to describe patterns in elephant and blue whale distributions, including correctly differentiating areas where species were probably present from areas where they were probably absent (e.g. offshore CCS, and in the Etosha salt pan). We assessed biological realism of our spatial predictions (Figs. 4 and 5) and found that the most biologically realistic models were not always those that performed best according to traditional model performance metrics. For example, blue whale background sampling had the highest predictive performance, but failed to identify the gradient between off-shelf absence and near-shore suitability where blue whales frequently occur. Background sampling tended to overestimate suitable habitat, and was therefore the most inaccurate at capturing areas where whales were absent (Table 1). In comparison, CRW sampling was more biologically realistic and better at capturing blue whale absence within the CCS domain despite this sampling approach resulting in models with poorer predictive performance and out of sample testing. Boosted regression tree models based on CRW and reverse CRW had anomalously high offshore habitat predictions where blue whales were rarely present even with strong realism nearshore, indicating these models would not be a good candidate for extrapolation .
The tradeoff between model skill and biological realism has practical implications for habitat modeling, where modellers should decide a priori on a model’s purpose and whether the ultimate goal is to better predict species presence or absence (e.g. . We advise caution when comparing model performance across multiple studies that may be driven by different management goals or that use different underlying data, modeling types, or pseudo-absence generation approaches. For example, a blue whale habitat modeling application that aims to conservatively identify all areas where whales might be present in order to afford them maximum spatial protection could benefit from using the background method, whereas an application that seeks to identify areas where whales are most likely not in direct contact with human activities outside areas of core habitat use might benefit from the CRW approach. Ultimately, which pseudo-absence method is best for a given goal will depend to a large extent on what environmental range it is sampling compared to presences. Johnson  describes four orders of resource selection that animals may exhibit, ranging from coarse to fine spatial scales: a species’ geographic range (1st order); an area within the geographic range (e.g. a home range; 2nd order); an area within the home range (3rd order); and a specific site or resource within the selected area (4th order; ). We propose similar attention should be paid to the modeling or management aim to inform the pseudo-absence selection approach (see Table 2). Ultimately, ensemble approaches may be worth exploring to gain inference across model differences  or among data types and modeling approaches .
We found consistent rankings among the three habitat model types (GLMMs < GAMMs < BRTs) based on explanatory power and predictive skill. These patterns held across species despite differences among the pseudo-absence methods. For elephants in particular, model type had a larger impact on model results compared to the pseudo-absence method. This importance of model type for elephants may be a function of the static nature of the habitat model, where variation in elephant presence (locations every 6 h) was not as well explained by the environmental covariates and resulted in models with non-linear functions (BRTs and GAMMs) performing better than linear models (GLMMs). Further, the ability of BRTs to best predict elephant presence was likely a function of the sharp step-wise transitions in the response curves (e.g. recursive binary splits) that can best describe habitat preferences near discrete features such as water holes and roads.
Comprehensive comparisons of habitat model approaches exist elsewhere in the literature [11, 17, 23, 50], thus we explored the interaction between model type and pseudo-absence method to provide practical recommendations. We found that selection of the optimal pseudo-absence method varied based on the questions being asked of the model, on the animals’ movement syndromes , and on the width of environmental niche space sampled by presences and generated pseudo-absences. Single habitat models and single approaches towards model validation may be sufficient for exploring ecological inference, but when models are used for management or conservation purposes such as spatial planning, multiple approaches and validation metrics should be considered to ensure the robustness of design and implementation [4, 6, 48, 58]. Taken holistically, model purpose is of utmost importance when choosing pseudo-absence generation method and model type to ensure that predictions are tuned to scales of animal movement and management need.
Maximizing predictive skill while maintaining biological realism is a key part of developing habitat models that optimize spatial protections for species while minimizing uncertainty and opportunity costs of erroneous predictions. Scientists have placed a lot of faith in quantitative metrics for evaluating predictive skill, but high performing models still may not be accurately addressing the research question at scale [27, 45]. Decisions such as choosing the most appropriate modeling framework for a given data structure and deciding how to represent absences can impact the robustness of models built for conservation and management applications. For this reason, careful consideration of model purpose and rigorous assessment of the robustness and accuracy of spatial predictions in relation to these decisions are important steps towards an improved understanding of the drivers of animal movement, predictions of habitat for use in spatial planning, and assessments of risk of human-wildlife conflicts.
Availability of data and materials
The animal movement datasets used in the current study have been previously published and are available from the corresponding data holders (Bailey, Tsalyuk) on reasonable request. Blue whale data are also available on gtopp.org with elephant data available via Movebank: https://doi.org/10.5441/001/1.3nj3qj45. All code for use by this paper is available at https://github.com/elhazen/PA-paper, https://doi.org/10.5281/zenodo.4453501.
Area Under the receiver operating characteristic Curve
Boosted Regression Tree
California Current System
Correlated random walk
Etosha National Park
Generalised Additive Mixed Model
Generalised Linear Mixed Model
True Skill Statistic
Aarts G, MacKenzie M, McConnell B, Fedak M, Matthiopoulos J. Estimating space-use and habitat preference from wildlife telemetry data. Ecography. 2008;31:140–60.
Abrahms B, Hazen EL, Aikens EO, Savoca MS, Goldbogen JA, Bograd SJ, Jacox MG, Irvine LM, Palacios DM, Mate BR. Memory and resource tracking drive blue whale migrations. Proc Natl Acad Sci. 2019a;116:5582–7.
Abrahms B, Seidel DP, Dougherty E, Hazen EL, Bograd SJ, Wilson AM, McNutt JW, Costa DP, Blake S, Brashares JS. Suite of simple metrics reveals common movement syndromes across vertebrate taxa. Mov Ecol. 2017;5:12.
Abrahms B, Welch H, Brodie S, Jacox MG, Becker EA, Bograd SJ, Irvine LM, Palacios DM, Mate BR, Hazen EL. Dynamic ensemble models to predict distributions and anthropogenic risk exposure for highly mobile species. Divers Distrib. 2019b;25(8):1182–93.
Allouche O, Tsoar A, Kadmon R. Assessing the accuracy of species distribution models: prevalence, kappa and the true skill statistic (TSS). J Appl Ecol. 2006;43:1223–32.
Araújo M, New M. Ensemble forecasting of species distributions. Trends Ecol Evol. 2007;22:42–7.
Avgar T, Potts JR, Lewis MA, Boyce MS. Integrated step selection analysis: bridging the gap between resource selection and animal movement. Methods Ecol Evol. 2016;7:619–30.
Bailey H, Mate B, Irvine L, Palacios DM, Bograd SJ, Costa DP. Blue whale behavior in the eastern North Pacific inferred from state-space model analysis of satellite tracks. Endanger Species Res. 2009;10:93–106.
Barbet-Massin M, Jiguet F, Albert CH, Thuiller W. Selecting pseudo-absences for species distribution models: how, where and how many? Methods Ecol Evol. 2012;3:327–38.
Barve N, Barve V, Jiménez-Valverde A, Lira-Noriega A, Maher SP, Peterson AT, Soberón J, Villalobos F. The crucial role of the accessible area in ecological niche modeling and species distribution modeling. Ecol Model. 2011;222:1810–9.
Becker EA, Carretta JV, Forney KA, Barlow J, Brodie S, Hoopes R, Jacox MG, Maxwell SM, Redfern JV, Sisson NB. Performance evaluation of cetacean species distribution models developed using generalized additive models and boosted regression trees. Ecol Evol. 2020;10(12):5759–84.
Becker EA, Forney KA, Ferguson MC, Barlow J, Redfern JV. Predictive modeling of cetacean densities in the California current ecosystem based on summer/fall ship surveys in 1991-2008. NOAA Technical Memorandum, NMFS-SWFSC. 2012;499.
Bhattacharyya A. On a measure of divergence between two statistical populations defined by their probability distributions. Bull Calcutta Math Soc. 1943;35:99–109.
Block B, Jonsen I, Jorgensen S, Winship A, Shaffer SA, Bograd S, Hazen E, Foley D, Breed G, Harrison A-L. Tracking apex marine predator movements in a dynamic ocean. Nature. 2011;475:86–90.
Bograd SJ, Leising AW, Hazen EL. Oceanographic Drivers. In: Mooney H, Zavaleta E, editors. Ecosystems of California – A Source Book. Oakland: University of California Press; 2016. p. 95–101.
Boyce M. Scale for resource selection functions. Divers Distrib. 2006;12:269–76.
Brodie S, Jacox MG, Bograd SJ, Welch H, Dewar H, Scales KL, Maxwell SM, Briscoe DM, Edwards CA, Crowder LB. Integrating dynamic subsurface habitat metrics into species distribution models. Front Mar Sci. 2018;5:219.
Calambokidis J, Steiger GH, Curtice C, Harrison J, Ferguson MC, Becker E, DeAngelis M, Van Parijs SM. 4. Biologically important areas for selected cetaceans within US waters–west coast region. Aquat Mamm. 2015;41:39–53.
Chapman D, Pescott OL, Roy HE, Tanner R. Improving species distribution models for invasive non-native species with biologically informed pseudo-absence selection. J Biogeogr. 2019;46:1029–40.
Checkley D, Barth J. Patterns and processes in the California current system. Prog Oceanogr. 2009.
Chefaoui RM, Lobo JM. Assessing the effects of pseudo-absences on predictive distribution model performance. Ecol Model. 2008;210:478–86.
Dickson BG, Jenness JS, Beier P. Influence of vegetation, topography, and roads on cougar movement in southern California. J Wildl Manag. 2005;69:264–76.
Elith J, Graham C, Anderson R, Dudík M. Novel methods improve prediction of species’ distributions from occurrence data. Ecography. 2006;29:129–51.
Elith J, Kearney M, Phillips S. The art of modelling range-shifting species. Methods Ecol Evol. 2010;1:330–42.
Elith J, Leathwick JR. Species distribution models: ecological explanation and prediction across space and time. Annu Rev Ecol Evol Syst. 2009;40:677–97.
Elith J, Leathwick JR, Hastie T. A working guide to boosted regression trees. J Anim Ecol. 2008;77:802–13.
Fourcade Y, Besnard AG, Secondi J. Paintings predict the distribution of species, or the challenge of selecting environmental predictors and evaluation statistics. Glob Ecol Biogeogr. 2018;27:245–56.
Guillera-Arroita G, Lahoz-Monfort JJ, Elith J, Gordon A, Kujala H, Lentini PE, McCarthy MA, Tingley R, Wintle BA. Is my species distribution model fit for purpose? Matching data and models to applications. Glob Ecol Biogeogr. 2015;24:276–92.
Harcourt R, Martins Sequeira AM, Zhang X, Rouquet F, Komatsu K, Heupel M, McMahon CR, Whoriskey FG, Meekan M, Carroll G. Animal-borne telemetry: an integral component of the ocean observing toolkit. Front Mar Sci. 2019;6:326.
Hazen EL, Palacios DM, Forney KA, Howell EA, Becker E, Hoover AL, Irvine L, DeAngelis M, Bograd SJ, Mate BR, Bailey H. WhaleWatch: a dynamic management tool for predicting blue whale density in the California current. J Appl Ecol. 2017;54:1415–28.
Hazen EL, Scales KL, Maxwell SM, Briscoe DK, Welch H, Bograd SJ, Bailey H, Benson SR, Eguchi T, Dewar H, Kohin S, Costa DP, Crowder LB, Lewison RL. A dynamic ocean management tool to reduce bycatch and support sustainable fisheries. Sci Adv. 2018;4(5):eaar3001.
Hindell MA, Reisinger RR, Ropert-Coudert Y, Hückstädt LA, Trathan PN, Bornemann H, Charrassin J-B, Chown SL, Costa DP, Danis B. Tracking of marine predators to protect Southern Ocean ecosystems. Nature. 2020;580:87–92.
Hirzel AH, Helfer V, Metral F. Assessing habitat-suitability models with a virtual species. Ecol Model. 2001;145:111–21.
Humphries GRW, Huettmann F, Nevitt GA, Deal C, Atkinson D. Species distribution modeling of storm-petrels (Oceanodroma furcata and O. leucorhoa) in the North Pacific and the role of dimethyl sulfide. Polar Biol. 2012;35:1669–80.
Hussey NE, Kessel ST, Aarestrup K, Cooke SJ, Cowley PD, Fisk AT, Harcourt RG, Holland KN, Iverson SJ, Kocik JF. Aquatic animal telemetry: a panoramic window into the underwater world. Science. 2015;348:1255642.
Irvine LM, Mate BR, Winsor MH, Palacios DM, Bograd SJ, Costa DP, Bailey H. Spatial and temporal occurrence of blue whales off the US west coast, with implications for management. PLoS One. 2014;9:e102959.
Iturbide M, Bedia J, Gutiérrez JM. Background sampling and transferability of species distribution model ensembles under climate change. Glob Planet Chang. 2018;166:19–29.
Iturbide M, Bedia J, Herrera S, del Hierro O, Pinto M, Gutiérrez JM. A framework for species distribution modelling with improved pseudo-absence generation. Ecol Model. 2015;312:166–74.
Jesmer BR, Merkle JA, Goheen JR, Aikens EO, Beck JL, Courtemanch AB, Hurley MA, McWhirter DE, Miyasaki HM, Monteith KL. Is ungulate migration culturally transmitted? Evidence of social learning from translocated animals. Science. 2018;361:1023–5.
Johnson DH. The comparison of usage andavailability measurements for evaluating resource preference. Ecology. 1980;61:65–71.
Johnson DS, Thomas DL, Ver Hoef JM, Christ A. A general framework for the analysis of animal resource selection from telemetry data. Biometrics. 2008;64:968–76.
Kareiva P, Shigesada N. Analyzing insect movement as a correlated random walk. Oecologia. 1983;56:234–8.
Kays R, Crofoot MC, Jetz W, Wikelski M. Terrestrial animal tracking as an eye on life and planet. Science. 2015;348:aaa2478.
Lobo J, Jiménez-Valverde A, Hortal J. The uncertain nature of absences and their importance in species distribution modelling. Ecography. 2010;33(1):103–14.
Lobo J, Jiménez-Valverde A, Real R. AUC: a misleading measure of the performance of predictive distribution models. Glob Ecol Biogeogr. 2008;17(2):145–51.
Manly B, McDonald L, Thomas DL, McDonald TL, Erickson WP. Resource selection by animals: statistical design and analysis for field studies: Springer Science & Business Media; 2007.
Mannocci L, Boustany AM, Roberts JJ, Palacios DM, Dunn DC, Halpin PN, Viehman S, Moxley J, Cleary J, Bailey H. Temporal resolutions in species distribution models of highly mobile marine animals: Recommendations for ecologists and managers. Divers Distrib. 2017;23:1098–109.
Mason C, Alderman R, McGowan J, Possingham HP, Hobday AJ, Sumner M, Shaw J. Telemetry reveals existing marine protected areas are worse than random for protecting the foraging habitat of threatened shy albatross (Thalassarche cauta). Divers Distrib. 2018;24:1744–55.
Nathan R, Getz WM, Revilla E, Holyoak M, Kadmon R, Saltz D, Smouse PE. A movement ecology paradigm for unifying organismal movement research. Proc Natl Acad Sci. 2008;105:19052–9.
Norberg A, Abrego N, Blanchet FG, Adler FR, Anderson BJ, Anttila J, Araújo MB, Dallas T, Dunson D, Elith J. A comprehensive evaluation of predictive performance of 33 species distribution models at species and community levels. Ecol Monogr. 2019;89:e01370.
O’Toole M, Queiroz N, Humphries NE, Sims DW, Sequeira AMM. Quantifying effects of tracking data bias on species distribution models. Methods Ecol Evol. 2021;12(1):170–81.
Palacios DM, Bailey H, Becker EA, Bograd SJ, DeAngelis ML, Forney KA, Hazen EL, Irvine LM, Mate BR. Ecological correlates of blue whale movement behavior and its predictability in the California current ecosystem during the summer-fall feeding season. Mov Ecol. 2019;7:26.
Pérez-Jorge S, Tobeña M, Prieto R, Vandeperre F, Calmettes B, Lehodey P, Silva MA. Environmental drivers of large-scale movements of baleen whales in the mid-North Atlantic Ocean. Divers Distrib. 2020;6:683–98.
Phillips SJ, Dudík M, Elith J, Graham CH, Lehmann A, Leathwick J, Ferrier S. Sample selection bias and presence-only distribution models: implications for background and pseudo-absence data. Ecol Appl. 2009;19:181–97.
Queiroz N, Humphries NE, Couto A, Vedor M, Da Costa I, Sequeira AM, Mucientes G, Santos AM, Abascal FJ, Abercrombie DL. Global spatial risk assessment of sharks under the footprint of fisheries. Nature. 2019;572:461–6.
Raymond B, Lea MA, Patterson T, Andrews-Goff V, Sharples R, Charrassin JB, Cottin M, Emmerson L, Gales N, Gales R. Important marine habitat off east Antarctica revealed by two decades of multi-species predator tracking. Ecography. 2015;38:121–9.
Roberts JJ, Best BD, Mannocci L, Fujioka E, Halpin PN, Palka DL, Garrison LP, Mullin KD, Cole TV, Khan CB. Habitat-based cetacean density models for the US Atlantic and Gulf of Mexico. Sci Rep. 2016;6:22615.
Scales KL, Hazen EL, Maxwell SM, Dewar H, Kohin S, Jacox MG, Edwards CA, Briscoe DK, Crowder LB, Lewison RL, Bograd SJ. Fit to predict? Eco-informatics for predicting the catchability of a pelagic fish in near real-time. Ecol Appl. 2017;27(8):2313–29.
Stockwell D. The GARP modelling system: problems and solutions to automated spatial prediction. Int J Geogr Inf Sci. 1999;13:143–58.
Thurfjell H, Ciuti S, Boyce MS. Applications of step-selection functions in ecology and conservation. Mov Ecol. 2014;2:4.
Tsalyuk M, Kilian W, Reineking B, Getz WM. Temporal variation in resource selection of African elephants follows long-term variability in resource availability. Ecol Monogr. 2019;89:e01348.
Warren DL, Matzke NJ, Iglesias TL. Evaluating presence-only species distribution models with discrimination accuracy is uninformative for many applications. J Biogeogr. 2020;47:167–80.
Willis-Norton E, Hazen EL, Fossette S, Shillinger G, Rykaczewski RR, Foley DG, Dunne JP, Bograd SJ. Climate change impacts on leatherback turtle pelagic habitat in the Southeast Pacific. Deep-Sea Res II Top Stud Oceanogr. 2015;113:260–7.
Wood S. Generalized additive models: an introduction with R. Boca Raton, Florida: Chapman & Hall / CRC press; 2006. p. 385.
Woodman SM, Forney KA, Becker EA, DeAngelis ML, Hazen EL, Palacios DM, Redfern JV. Esdm: a tool for creating and exploring ensembles of predictions from species distribution and abundance models. Methods Ecol Evol. 2019;10:1923–33.
Yates KL, Bouchet PJ, Caley MJ, Mengersen K, Randin CF, Parnell S, Fielding AH, Bamford AJ, Ban S, Barbosa AM. Outstanding challenges in the transferability of ecological models. Trends Ecol Evol. 2018;33:790–802.
Žydelis R, Lewison RL, Shaffer SA, Moore JE, Boustany AM, Roberts JJ, Sims M, Dunn DC, Best BD, Tremblay Y. Dynamic habitat models: using telemetry data to project fisheries bycatch. Proc R Soc Lond B Biol Sci. 2011;278:3191–200.
This project built upon modeling efforts for blue whales led by Helen Bailey, Ladd Irvine, and Daniel Palacios and elephant movement led by Miriam Tsyaluk and Wayne Getz. We thank the many people who assisted with field efforts and tagging efforts. The work would not have been possible without the field efforts of Oregon State’s Marine Mammal Institute, and Miriam Tsalyuk, Wayne Getz, and the Etosha Ecological Institute, permitting for marine mammal research by NOAA, permitting for elephant research by Namibian Ministry of Environment and Tourism (MET). We thank Elizabeth Becker, Tommy Clay, and Nerea Lezama Ochoa for useful comments that helped improve the manuscript. Sponsors did not have a role in planning, executing, or writing this research.
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Summary of environmental predictors used in species distribution modelling for blue whale and elephant case studies. Spatial resolution is in decimal degrees. Table S2. Validation metrics for spatial and temporal hold-out approaches. Temporal hold-out not available for the average elephant model as predictor variables are not dynamically measured. Figure S1. Partial response curves for the two most important covariates in the blue whale (a-d) and elephant (e-h) habitat suitability models. Response curves for GAMMS (left panels; A, B, E, F), and BRTs (right panels; C, D, G, H) are shown for the four pseudo-absences generation techniques (Background in red, Buffer in gray, CRW in green, Reverse CRW in blue).
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Hazen, E.L., Abrahms, B., Brodie, S. et al. Where did they not go? Considerations for generating pseudo-absences for telemetry-based habitat models. Mov Ecol 9, 5 (2021). https://doi.org/10.1186/s40462-021-00240-2