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Modelling Dolphin Distribution to Inform Future Spatial Conservation Decisions in a Marine Protected Area

Scientific Reportsvolume 8, Article number: 15659 (2018) | Download Citation


As marine predators experience increasing anthropogenic pressures, there is an urgent need to understand their distribution and their drivers to inform spatial conservation planning. We used an ensemble modelling approach to investigate the spatio-temporal distribution of southern Australian bottlenose dolphins (Tursiops cf. australis) in relation to a variety of ecogeographical and anthropogenic variables in Coffin Bay, Thorny Passage Marine Park, South Australia. Further, we evaluated the overlap between current spatial management measures and important dolphin habitat. Dolphins showed no distinct seasonal shifts in distribution patterns. Models of the entire study area indicate that zones of high probability of dolphin occurrence were located mainly within the inner area of Coffin Bay. In the inner area, zones with high probability of dolphin occurrence were associated with shallow waters (2–4 m and 7–10 m) and located within 1,000 m from land and 2,500 m from oyster farms. The multi-modal response curve of depth in the models likely shows how the different dolphin communities in Coffin Bay occupy different embayments characterized by distinct depth patterns. The majority of areas of high (>0.6) probability of dolphin occurrence are outside sanctuary zones where multiple human activities are allowed. The inner area of Coffin Bay is an important area of year-round habitat suitability for dolphins. Our results can inform future spatial conservation decisions and improve protection of important dolphin habitat.


Information on how different environmental and anthropogenic variables affect the distribution of species is fundamental for understanding their ecology and guiding spatial conservation planning1,2. The presence and distribution of marine top predators, such as dolphins, has been linked to a variety of abiotic and biotic factors, which are usually linked to the distribution of their prey, predators and conspecifics3. Human activities such as boating, fishing activities and aquaculture can affect dolphin behaviour and ultimately also influence their distribution patterns4,5,6. Species distribution models (SDM) provide a useful analytical framework to investigate the environmental and anthropogenic factors affecting species distribution1,2,7. Such information can help elucidate which areas constitute important habitat for a species and where potential conflicts with human activities may occur8.

In the marine environment, coastal ecosystems are the most heavily impacted by human activities9. Marine top predators such as whales and dolphins are particularly susceptible to human stressors because of their life-history traits (i.e. late maturity, low reproductive rate and long life span10) and some of the most at risk species occur in coastal areas. Several coastal dolphin populations, especially those with high levels of site fidelity and restricted ranging patterns, are at risk due to pressures such as habitat degradation and loss, by-catch, prey depletion, tourism, pollution, among others11,12,13,14,15,16. The decline of dolphins’ numbers due to anthropogenic disturbances can be reverted if areas of high abundance and suitable habitats are identified, and appropriate spatial conservation planning and management measures (including enforcement) are established to diminish anthropogenic impacts within those areas17,18,19.

Australia has the world’s largest representative network of marine parks covering 3.3 million km2 (36%) of its marine environment. Despite this protection, the waters surrounding Australia’s coastline are increasingly threatened by human activities and several areas across northern, western and southern Australia have been identified as global hotspots of marine mammal extinction risk20. Furthermore, few studies have focused on investigating whether Australia’s marine protected areas are adequately protecting marine mammals21. In South Australia (SA), increasing coastal zone development, coastal pollution, aquaculture and fishery interactions, threaten the viability of dolphin populations22,23,24,25. Our understanding of the magnitude of these problems and ability to provide effective management solutions to them is hindered by the lack of spatially explicit data on dolphin distribution and anthropogenic threats. There is an urgent need for this information as zoning of all SA’s marine parks is schedule for review in 2022, and there is strong commitment from wildlife agencies to ensure that the marine planning process includes the conservation needs of marine top predators such as dolphins.

The bottlenose dolphin (Tursiops sp.) is a cosmopolitan marine top predator, extensively distributed in temperate and tropical waters around the world. Currently there are two widely accepted species within the genus, the common bottlenose dolphin (T. truncatus) and the Indo-Pacific bottlenose dolphin (T. aduncus). T. truncatus is considered by the IUCN Red List of Threatened Species as Least Concern26, while T. aduncus is classified as Data Deficient27. Recently, a potential new species was described for coastal waters of southern Australia, the Burrunan dolphin (Tursiops australis)28. The taxonomy of this putative new species is still contentious29,30, therefore we refer to them here as southern Australian bottlenose dolphins (Tursiops cf. australis) or SABD. SABD appear to form small, resident and genetically differentiated populations31, and population structuring may be occurring at small spatial scales in relation to environmental factors (e.g. location of oceanographic front32). So far, six populations of SABD have been identified spread over ~2500 km of coastline based on molecular markers28,31,33,34. These populations are exposed to different environmental conditions and anthropogenic activities, but little is known about how these may influence their distribution patterns. Studies in Gulf Saint Vincent, SA, showed that the distribution patterns of SABD are influenced by a variety of ecogeographic variables, likely linked to prey distribution and availability, such as bare sand habitat in the Port River estuary and Barker Inlet35, and water depth, benthic habitat type and slope along Adelaide’s metropolitan coast36. Both studies identified priority areas for dolphin conservation along SA’s coast and highlighted the need for future studies to evaluate the influence of human activities (e.g. vessel traffic, fishing, and ports) on dolphin distribution.

The largest population of SABD (n = 306, 95% CI: 291–323) studied to date inhabits Coffin Bay, a small embayment (263 km2) located within the Thorny Passage Marine Park, Eyre Peninsula, SA37. Coffin Bay is an heterogeneous ecosystem with two distinctive areas, the outer area, which is exposed to the oceanographic conditions of the Southern Ocean, and the inner area, which is a shallow inverse estuary consisting of a variety of habitats across several interconnected embayments38,39. The inner area sustains a high density of dolphins (1.57–1.7 individuals/km2), most of them residents, likely favoured by the high biological productivity and the apparent low predation risk in this area37,40. The status of these dolphins, i.e. whether the population size is stable or not, is unknown37. About 6% of Coffin Bay waters are currently classified as sanctuary zones (i.e. areas of high conservation value where only low-impact recreation activities are allowed, but motorized water sports and fishing are prohibited), while the rest of the bay is zoned as a multiple use marine park where several human activities are allowed (e.g., boating, oyster aquaculture, recreational fishing41,42). The local human population around Coffin Bay is relatively small (c.a. 500 people) but increases to c.a. 4,000 people during the peak tourist season (end-December to February, and Easter)43. The main human activities occurring in Coffin Bay waters that could have detrimental effects to the local dolphin population are aquaculture and vessel traffic43. The inner area of Coffin Bay is home to SA’s leading Pacific oyster aquaculture industry with several areas designated for farming (Fig. 1). Furthermore, the bay attracts substantial power boating activity, particularly during the summer and Easter tourism seasons, including recreational fishing, fishing charters, and cruises for sightseeing and to see and taste oysters in the farms, and to a smaller degree, for dolphin watching43. Elsewhere, shellfish aquaculture has been associated with dolphins’ habitat loss because of a decrease in occurrence and distribution of dolphins in areas around farms44,45,46,47. Vessel traffic is also known to affect dolphins’ behaviour in the short-term48,49,50, can cause injuries or death due to collisions51, and could lead to population declines or abandonment of habitat in the long term6,52. Despite the importance of Coffin Bay for SABD, the current lack of information about their distribution patterns in relation to environmental conditions and human activities hampers the identification of important habitats and the potential impacts of these threats. Understanding how aquaculture and vessel traffic may affect dolphins’ distribution patterns is crucial for improving future decision-making regarding the zoning of multiple-use MPAs in SA.

Figure 1
Figure 1

Location of Coffin Bay within the Thorny Passage Marine Park, Eyre Peninsula, South Australia. Study area showing the zig-zag transect layout (Survey routes A and B) used to cover the outer and the inner areas of Coffin Bay, oyster farms and sanctuary zones. Colours as indicated in the legend represent the different types of benthic habitats (Database provided by the Department of Environment, Water and Natural Resources, South Australian Government).

In this study, we used an ensemble of SDMs53 to assess the spatio-temporal distribution of SABD in relation to a variety of ecogeographical and anthropogenic variables in Coffin Bay, SA. The aim was to identify areas of high probability of dolphin occurrence, gain insights into the habitat requirements of the species and evaluate the relevance of the current sanctuary zones to the protection of dolphins within this MPA. The results improve our understanding of the spatial ecology of the species, illustrate the importance of considering both environmental as well as anthropogenic factors in SDMs, and support future spatial conservation planning in southern Australia.


Between September 2013 and October 2015, we encountered 620 groups of dolphins (587 and 33 in the inner and outer areas, respectively) over 144 days of surveys. Survey effort and number of dolphin groups sighted varied between seasons, and between the inner and the outer areas of Coffin Bay (Supplementary Appendix 1, Table S1 and Fig. S1). Overall, the highest survey effort and number of dolphin sightings occurred within the inner area (Supplementary Appendix 1, Table S1 and Fig. S1).

Dolphin occurrence across Coffin Bay

When considering data across the entire study area and study period, collinearity was detected between distance to farm and distance to sanctuary zone (r = 0.92), and depth and distance to land (r = 0.72). After running ‘vifstep’, distance to farm and to land were discarded from modelling. Thus, the remaining explanatory variables included in SDMs for the whole study area were habitat type, distance to sanctuary zones, and water depth (Table 1). Single SDMs performance varied from moderate to excellent (AUC median = 0.88; range: 0.79–0.93), and ensemble models (AUC = 0.90) had better performance than most single SDMs (Fig. 2). The most important variable in all single SDMs was distance to sanctuary zone, followed by water depth (Table 1). The probability of dolphin occurrence was higher in areas between 500 and 5,000 m from sanctuary zones, and where water depth was shallower than 15 m, with peaks in dolphin occurrence at water depths of 2–4 m and 7–10 m (Supplementary Appendix 2, Fig. S4). These ranges of distance to sanctuary zones and water depth are characteristic of the inner area only (Supplementary Appendix 1, Fig. S2). Accordingly, the ensemble model of the whole study area predicted high dolphin presence mainly within the inner area of Coffin Bay (Fig. 3). Similarly, seasonal models indicated that the most important predictor of dolphin presence was distance to sanctuary zone (or distance to farm), and predicted areas of high probability of dolphin in the inner area (see Appendix 4).

Table 1 Importance of ecogeographical and anthropogenic variables used in SDMs of SABD (Tursiops cf. australis) for the whole study area and for the inner area of Coffin Bay: GAM = generalised additive model; GBM = generalised boosted model; CTA = classification tree analysis; RF = random forest; and MaxEnt = maximum entropy. Variable importance is presented as the mean value over the 10 runs of each single modelling algorithm, and as the mean of means amongst them. Explanatory variables of greatest influence (values closest to one) are highlighted in bold. (NOTE: Values are presented only for those non-correlated variables included in each model).
Figure 2
Figure 2

Performance of species distribution models built with datasets of the entire study area (left) and the inner area (right) of Coffin Bay. Box-plots for the model accuracy (AUC: area under the curve of the receiver operating characteristics plot) of the 10 cross-validation runs of each modelling algorithm (GAM: generalised additive model; GBM: generalised boosted model; CTA: classification tree analysis; RF: random forest; and MaxEnt: maximum entropy), and dotted line indicating the predictive performance (AUC) of ensemble models for each dataset. Values of AUC ≥ 0.7 indicate that the model predictive performance is moderate to excellent.

Figure 3
Figure 3

Ensemble model of SABD (Tursiops cf. australis) probability of occurrence in Coffin Bay for the overall study period (September 2013 – October 2015). The coloured shading, as detailed in the legend, represents probability of dolphin occurrence.

Dolphin occurrence in inner area

We found no collinearity between the explanatory variables considered for SDMs of the inner area (r < 0.26 and VIF < 1.3 for all combinations of variables), thus all variables were retained for analysis. Single SDMs performance varied from moderate to excellent (AUC median = 0.80; range: 0.72–0.86), and ensemble models outperformed all single SDMs (AUC = 0.86; Fig. 2). The most important variable affecting the distribution of dolphins in the inner area over the entire study period was water depth, followed by distance to oyster farms and to land (Table 1). The probability of dolphin occurrence was higher in areas deeper than 2 m, within a distance of 2,500 m from oyster farms, and within 1,000 m from land (Supplementary Appendix 2, Fig. S5). The ensemble model predicted high dolphin presence mainly in the north-west part of Port Douglas Bay, in some parts of Mount Dutton Bay, and the western part of Kellidie Bay (Fig. 4a).

Figure 4
Figure 4

Ensemble models of SABD (Tursiops cf. australis) probability of occurrence in the inner area of Coffin Bay for: (a) over the entire study period; (b) spring; (c) summer; (d) autumn; and (d) winter. Colours as shown in the legend indicate the probability of occurrence of dolphins.

Seasonal dolphin occurrence in inner area

Collinearity was found between water visibility and depth in every season (r > 0.74). After running ‘vifcor’, water visibility was discarded from seasonal models. In autumn, pH and salinity also showed high collinearity (r = −0.74), and thus salinity was discarded from the models after running ‘vifstep’ (Table 2). Single seasonal SDMs of the inner area showed poor (AUC < 0.7) to moderate performance (0.7 ≤ AUC < 0.9) (Supplementary Appendix 3, Fig. S6), thus some models were excluded from ensembles. The ensemble models outperformed all single SDMs in every season (Supplementary Appendix 3, Fig. S6). Most seasonal SDMs identified water depth as the most important variable, followed by distance to land (Table 2); which is concordant with results of overall models for the inner area (Table 1). Exceptions included two algorithms for spring and three for autumn that had distance to land as the most important variable, and two algorithms for summer that identified pH as an important variable (Table 2). Response curves of SDMs showed variability among SDMs (see examples in Supplementary Appendix 3, Fig. S7). Among seasonal ensemble predictions, summer exhibited the lowest probability of dolphin presence (Fig. 4b–e). In summer, the highest probabilities of dolphin occurred in the central part of Kellidie Bay, and the northern part of Mount Dutton Bay and the entrance to Little Mount Dutton (Fig. 4c). In the remaining seasons, the highest probability of dolphins were in areas where water depth exceeds 2 m including the western sector of Kellidie Bay, the central part of Mount Dutton Bay and around the farms of Port Douglas Bay (Fig. 4b,d and e).

Table 2 Importance of ecogeographical and anthropogenic variables for SABD (Tursiops cf. australis) in the inner area of Coffin Bay by season, using five types of models: generalised additive model (GAM), generalised boosted model (GBM), classification tree analysis (CTA), random forest (RF) and maximum entropy (MaxEnt). Variable importance is presented as the mean value over the 10 runs of each single modelling algorithm, and as the mean of means amongst them. Explanatory variables of greatest influence (values closest to one) are highlighted in bold. (NOTE: Values are presented only for those non-correlated variables included in each model).

Dolphin occurrence and sanctuary zones

According to ensemble models’ predictions, the probability of dolphin occurrence in sanctuary zones over the whole study period ranged from 0.06 to 0.83 (Fig. 4). Amongst all sanctuaries, the one located in Mount Dutton Bay had the highest probability (mean ± SD = 0.52 ± 0.28) of dolphin occurrence (Fig. 4; Table 3). The seasonal mean probabilities of dolphin occurrence were below 0.5 for all sanctuaries (Table 3).

Table 3 Probability of occurrence of SABD (Tursiops cf. australis) predicted by the inner area’s ensemble models in sanctuary zones (SZ) of Coffin Bay.


Effective management of wildlife populations requires sound knowledge of species distributions and associated threats. Here, we used an ensemble modelling approach to determine the spatio-temporal distribution patterns of SABD in Coffin Bay, a heterogeneous ecosystem located within a multiple use marine park in SA. Ensemble modelling provided a robust approach for evaluating the importance of ecogeographical and anthropogenic factors influencing dolphin distribution patterns, and identifying important areas of dolphin occurrence. Distance to sanctuary zones and water depth were the most important variables influencing dolphins’ probability of occurrence over Coffin Bay. High probability of dolphin occurrence was predicted almost exclusively for the inner area of Coffin Bay, which is consistent with the high density of dolphins recorded for this area37, and indicates that the inner area represents an important habitat for SABD. Models of the inner area showed that dolphins favoured waters greater than 2 m deep, within a distance of 1,000 m from land and 2,500 m from oyster farms. Despite the seasonality in environmental conditions and anthropogenic activities, the most important explanatory variables influencing dolphin distribution were similar across seasons and there were no significant shifts in dolphin distribution patterns. Overall, we found that areas with the highest probability of dolphin presence were located in three different embayments within the inner area: Mount Dutton, Kellidie and Port Douglas. Most areas of highest dolphin probability (>0.6) were located outside sanctuary zones.

Dolphin distribution is influenced by prey distribution and predation risk54,55,56. Therefore, characteristics of the habitat such as water depth, distance to coast, salinity, sea surface temperature, among others, are usually used as proxies of prey availability in SDMs because they are related to oceanographic processes that enhance local productivity e.g.,36,57,58. SABD favoured the waters of the inner area of Coffin Bay. Shallow, sheltered, inverse estuaries, such as the inner area of Coffin Bay, are usually highly productive systems59 that can sustain high densities of fish and top predators like dolphins. The total nutrient loads in the inner area of Coffin Bay are higher than those of outer area60, and it is likely that this enhances the productivity in the former resulting in higher abundance of prey. Several fish and cephalopods known to be part of the diet of bottlenose dolphins in SA61, use Coffin Bay as a nursery and feeding area42. Furthermore, it is likely that differences in predation risk between the inner and outer area of Coffin Bay may also influence dolphin occurrence patterns in the study area. White sharks (Carchharodon carcharias), one of the predators of dolphins along SA’s coast62, can be found close to shore in <5 m depth, but they seem to prefer continental shelf waters <100 m depth63. The shallow waters of the inner area and the narrow connection with the outer area may restrict the use of the former by sharks, thus resulting in lower predation risk in the inner area. To explicitly test these hypotheses, future studies need to incorporate additional variables into SDMs such as chlorophyll a or net primary production, as well as the presence and abundance of prey and predators.

In temperate regions, dolphins can display seasonality in their distribution patterns as they follow changes in prey abundance and availability, which are driven by seasonal changes in water conditions36,64. Although Coffin Bay is exposed to pronounced spatial and temporal variability in environmental conditions (Supplementary Appendix 2, Fig. S3), dolphin distribution patterns showed no major changes with season. This temporal stability in the distribution patterns of SABD indicates year-round habitat suitability in the inner area of Coffin Bay, suggesting that the availability of prey in the inner area is enough to fulfil dolphins needs year round, contrary to what is observed along the Adelaide coast36. The Adelaide metropolitan coast is an open environment, likely less productive than Coffin Bay, where the abundance of SABD varies throughout the year, and individuals show varying levels of site fidelity and residency65.

Apart from ecological factors, the social structure of animal populations can also influence individual patterns of space use66,67,68. Two social communities of SABD (each one with at least 70 individuals) occur in the inner area of Coffin Bay, one in the Port Douglas area and another one in Mount Dutton and Kellidie Bays69. Furthermore, the space use patterns of resident dolphins of the inner area are characterized by strong site fidelity, small representative ranges (<33.5 km2) and restricted movements to a single embayment40. The multi-modal response curves observed for the applied models likely reflect the dolphin community preferences for different embayments within Coffin Bay and their respective characteristics69. The plateau of occurrence probability observed at 2–4 m depth may relate to the dolphin community inhabiting Kellidie and Mount Dutton Bays, where the mean depth of this bays are 2 and 4 m, respectively; and the plateau at 7–10 m may relate to the community occurring in Port Douglas Bay, where depth can reach up to 11 m (Supplementary Appendix 1, Fig. S2b). Thus, the areas of high probability of dolphin occurrence identified here likely reflect the interaction among ecological and social factors.

Anthropogenic activities such as aquaculture and vessel traffic are known to affect dolphin distribution patterns (e.g.,4,5,6). Dolphins’ response to aquaculture activities is variable and complex. Some studies elsewhere showed that dolphins were attracted to areas with aquaculture44,70,71, while others showed that dolphins were less likely to go into areas where aquaculture was occurring, even though farms were located in habitats with characteristics favored by dolphins47. In Coffin Bay, oyster farms are located in shallow areas less than 2 m deep, while dolphins seem to prefer waters greater than 2 m deep. Whether dolphins have been displaced from areas now occupied by oyster farms, since the farms were established, is unknown. In general, shellfish aquaculture is known to increase nitrogen levels into the ecosystem altering local ecology, especially in areas where tidal and other flushing is minimal72. The inner area of Coffin Bay has slow flushing39 and high nutrient loads60. A trophic mass-balance model used to estimate the potential effects of finfish aquaculture in Aranci Bay, Sardinia, Italy, showed increased nutrient loading into aquaculture farm areas, followed by increases in biomass of fish and top predators, such as bottlenose dolphins71. Thus, dolphins favouring areas within 500 to 2,500 m from oyster farms in Coffin Bay is likely in response to higher nutrients and a potential increase in prey abundance in the proximity of farms. Further studies on dolphin diet and prey distribution within the study area are needed to test this hypothesis.

Although the influence of encounter rate of vessels was not as strong as other variables in explaining the distribution of dolphins, response curves showed that the probability of dolphin presence decreased as vessel encounter rates increased (Supplementary Appendix 3, Fig. S7), suggesting that dolphins in Coffin Bay tend to occur in areas with lower vessel traffic. Future behavioural research and long-term monitoring of this population would help elucidate whether dolphins’ behaviour is affected by the presence of oyster farms or vessels, and if management measures are required to prevent potential long-term consequences.

Our findings highlight areas with high probability of dolphins (>0.6) located in three different embayments within the inner area of Coffin Bay (i.e. Kellidie, Mount Dutton and Port Douglas, see Fig. 4a). Sanctuary zones cover areas with low (<0.3) to moderate (0.31–0.6) probability of dolphin’s presence in Kellidie and Port Douglas Bays, and relatively high probability in Mount Dutton Bay. However, in general, areas with the highest probability of dolphin presence are outside the sanctuary zones, in multiple use areas where dolphins are exposed to a variety of anthropogenic threats including vessel traffic, recreational fishing and oyster farming. Dolphins favoured areas close to oyster farms and such proximity can put them under risk of entanglement with aquaculture gear, which may cause injuries or death47,51,70. The farming system used in Coffin Bay uses structures that result in debris washing up on beaches38, including poles, baskets, rubber bands and plastic clips. During this study, four calves were observed swimming with rubber bands entangled around their necks, while two of them were still alive at the end of the study, the remaining two were presumed dead (unpublished data). The expansion of current or the establishment of new oyster farms in Coffin Bay should take into account the areas of high dolphin presence identified here to minimize interactions with aquaculture equipment and potential displacement of dolphins from important habitats.

Marine mammals are considered as ‘species of ecological value’ in the management plan of the Thorny Passage Marine Park73. However, there are no specific management arrangements to protect SABD. The high density of dolphins inhabiting Coffin Bay37, and the findings presented here should encourage the integration of the species into the monitoring program and zoning arrangements of this park. We recommend the areas of high dolphin presence identified here as priority areas for dolphin conservation and for the implementation of vessel traffic, aquaculture and fishing regulations.


Study area

Coffin Bay is part of the Thorny Passage Marine Park, SA (Fig. 1). Coffin Bay’s benthic habitats are mainly seagrass beds, followed by unconsolidated bare substrate, invertebrate community, low profile reef, macroalgae, cobble and medium profile reef (Fig. 1). The bay is divided by a spit of land into an inner (~123 km2) and an outer area (~155 km2), and water exchange between these two areas is restricted through a narrow (2 km) opening39. The inner area is a shallow (mean depth ~2.5 m with tides of approx. 1.3 m) system that consists of several interconnected bays (e.g. Port Douglas, Mount Dutton and Kellidie38,39). This area is considered an inverse estuary because evaporation rates exceeds precipitation during the austral summer resulting in hypersaline waters; while in winter salinity is diluted because of freshwater inputs39,41. The outer area connects the waters from the inner area to the Great Australian Bight, and is influenced by oceanographic features of the Southern Ocean38. In the outer area productivity is low during winter; however, a nearby summer-autumn (February and March) upwelling brings cold, nutrient-rich water to the surface74,75. In the study area, especially in the internal bays, marked seasonal fluctuations are observed in water conditions such as sea surface temperature (SST) and salinity39.

Survey design and data collection

Boat-based line-transect surveys were conducted between September 2013 and October 2015 to collect location data on dolphins and vessels. Surveys were conducted along two alternative equal-spaced zigzag transect routes76 covering a range of environmental conditions (e.g., depth, distance to shore, temperature, salinity) and human activities (e.g., location of aquaculture farms, distribution of vessels). To complete a single route in the inner and outer area, it took 2–4 and 2–3 days of surveys, respectively. Transects covered 85.5 km2 in the inner area and 154.1 km2 in the outer area of Coffin Bay. Surveys were done during daylight hours, at an average speed of 15 km/hr and under good weather conditions (i.e. Beaufort state ≤3, good-average visibility, no rain or fog, swell height <1 m). Once a route was completely surveyed in each area, we started with the alternate route on the next day of survey. During surveys, an observer on each side of the boat searched continuously for dolphins and vessels from −5° to 90° degrees of the transect with Fujinon 7 × 50 binoculars or the naked eye. All observers were trained in dolphin observation techniques to reduce observer bias in dolphin detection and group size estimation. A group of dolphins was defined as all animals seen within a radius of approx. 100 m77. Whenever a group of dolphins was sighted the position of the research vessel on the transect was recorded with a GPS, and search effort was suspended to approach the group within 10–20 m, and record their location using a GPS and group size. Whenever an operating power vessel (i.e. with people on board who were either navigating or fishing), or group of vessels (defined as ≥2 vessels encountered within a radius of 100 m), was sighted on a transect the following data were gathered: GPS position on transect, number of vessels, horizontal sighting angle, and downward angle (in reticles) to vessel (or to the centre of the group), measured with the binoculars compass and reticles, respectively. This information was used to derive the position of vessels using formulae proposed by Lerczak and Hobbs78. Data on environmental variables (water depth, sea surface temperature, turbidity, salinity and pH) were collected in situ at the location of every group of dolphins encountered, every 2 km along the transect line, and at the beginning and end of each transect leg. An YSI Professional Plus handheld multiparameter was used to record sea surface temperature (accuracy ± 0.2 °C), salinity (accuracy ± 0.1 ppt) and pH (accuracy ± 0.2 units); turbidity was measured using a Secchi disc; and depth was recorded using the boat’s depth sounder.

Data analysis

A Geographic Information System (GIS) in ArcMap 10.3.1 (ESRI) was used to create spatial layers of all response (dolphin presence-absence) and ecogeographic and anthropogenic explanatory variables (Table 4) at 500 × 500 m grid cell resolution. The location of dolphin groups and survey tracks were imported into ArcMap to create a binary presence-absence grid of dolphins while taking into account survey effort. A grid layer of survey effort (km2) was generated by adding a 500 m buffer (average distance to which dolphins could be reliably observed from the boat) on either side of the transect surveyed. Survey coverage was quantified for the entire study period and per season by calculating the total amount of area surveyed on-effort within each grid during each time period.

Table 4 List of anthropogenic and ecogeographic variables considered for modelling the presence-absence of SABD (Tursiops cf. australis) in Coffin Bay. For each variable we show its classification, the type (i.e. categorical or numeric) and range of values, and the data source. It is also indicated if a particular variable was used in overall and/or seasonal models.

Obtaining data on true absences for mobile species is difficult79. In dolphin studies, false absences can occur due to observer error (visibility bias), when animals are underwater and remain undetected (availability bias), or if survey effort is not high enough to reliably cover the study area79,80,81. Including false absences in models that require presence-absence data can produce inaccurate predictions of species distribution82. As true absence data were not available, for presence-absence models we generated inferred absence data (pseudo-absences) by incorporating survey effort in the definition of absences82,83. Similarly to previous studies, we defined pseudo-absence cells based on areas with highest survey effort36,84. For each area (inner and outer), we calculated the mean survey effort per grid. After this, grids in the inner and outer areas with survey effort higher than the mean per area, and with no presence of dolphins, were considered pseudo-absences. This definition of pseudo-absence allows us to assume that selected grids are as close to ‘true’ absences as possible, since they were surveyed several times during the study period without dolphin detections. We generated the same number of pseudo-absences as available presences, which results in an equal weighting of presences and pseudo-absences in the species–habitat models, a procedure that has been shown to perform well for a variety of SDM algorithms81. For Maxent, which is a presence-only approach that requires background samples of the environment85, we used as background data those grid cells with environmental data that were surveyed in a given data set (i.e. entire Coffin Bay or inner area) and period (i.e. entire study period or seasons), regardless of amount of effort.

Ecogeographical and anthropogenic explanatory variables were selected based on the availability of data and published evidence suggesting that they could potentially affect the presence of bottlenose dolphins or their prey (e.g.,5,36,57,58,86,87). Each 500 × 500 m grid within the study area was characterised by each ecogeographical and anthropogenic explanatory variable considered in this study (Table 1). The distance to sanctuary zones, oyster farms, and to land was measured using the Euclidean distance function in ArcMap. The benthic habitat type of each grid cell was assigned as the category (Table 1) covering the greatest proportion of each cell. To generate raster layers of the environmental data collected in situ (i.e. water depth, SST, salinity, water visibility and pH), the point data were interpolated in ArcMap using the Ordinary Kriging function and a spherical semivariogram model (500 m cell size) within the Spatial Analysis Tools. The vessel encounter rate for each grid cell was calculated in ArcMap as the number of vessels sighted divided by the survey effort (km2) per cell. Explanatory variables such as habitat type (Fig. 1), water depth, and distance to sanctuary zones, oyster farms, and to land (Supplementary Appendix 1, Fig. S2), were considered fixed in time and included in all models (Table 1). Thus, a single raster layer of water depth was built by pooling in situ data collected across the entire study period. Meanwhile, to account for the seasonality of dynamic variables (i.e. SST, salinity, water visibility, pH and vessel encounter rate), in situ data were pooled per austral season to build seasonal raster layers for each variable (Supplementary Appendix 1, Fig. S3).

Ensemble species distribution modelling

To model the presence-absence of dolphins in relation to explanatory variables, we used an ensemble modelling approach that combined results from five different algorithms implemented in Biomod2 package in R v.3.3.253: two regression methods, generalised additive models (GAMs88) and generalised boosted models (GBMs89); one classification technique, classification tree analysis (CTA90); and two machine learning approaches, random forest (RF91) and maximum entropy (MaxEnt92). These modelling algorithms are known to perform well and provide a good comparison between three different modelling approaches93,94. All algorithms were run with the default settings of Biomod2. Within Biomod 2, we used Maxent version 3.4.0, which uses as the default output a complementary log-log (cloglog) transformation to produce an estimate of occurrence probability95. Before running the SDMs, correlations between continuous explanatory variables were investigated using correlation coefficients (threshold = 0.796) and variance inflation factors (VIF, threshold = 397). Highly correlated variables were excluded from the set of variables used for SDMs using the stepwise procedures ‘vifcor’ and ‘vifstep’ with the package ‘usdm’ in R98. The ‘vifcor’ first finds a pair of variables which has the maximum linear correlation (greater than the threshold), then excludes one of them which has greater VIF; these steps are repeated until there is no variable remaining with a correlation coefficient greater than the threshold. Similarly, ‘vifstep’ first calculates VIF for all variables, then excludes the variable with highest VIF (if this is greater than threshold), and these steps are repeated until no variables with VIF greater than threshold remains98.

We built SDMs for the whole study area using data across the entire study period to determine general spatial distribution patterns in relation to benthic habitat type, water depth, and distance to land, sanctuary zones, and oyster farms. Besides, we built seasonal models (austral spring, summer, autumn and winter) to also consider any seasonal shifts due to explanatory variables that varied in space and time over the study period (i.e. encounter rate of vessels, SST, salinity, turbidity and pH) (Table 1). Seasons were defined as winter (June–August), spring (September–November), summer (December–February), and autumn (March–May). The response curves of the most important variable of these models indicated that a plateau of high probabilities of dolphins occurred at values within ranges that are only characteristic of the inner area (see results). Previous studies indicated that dolphins in the inner area of Coffin Bay have low emigration rates37, strong site fidelity, and most are year-round residents to the inner area40. Thus, we also built separate SDMs for the inner area to identify the most important variables influencing the distribution of dolphins residing in this area. Collinearity was explored for each dataset separately.

SDMs were built using a binomial error distribution with logit as the link function. We implemented a 10-fold cross-validation method for each SDM and a random data splitting procedure of 75/25% for respective model calibration and testing using Biomod253. This percentage split of training/testing dataset is a common approach to data partitioning used in various SDM studies (e.g.36,99,100,101,102,103), and it is considered best practice for training and testing distribution models2,104. The importance of the explanatory variables was assessed using a randomisation procedure in Biomod2 based on 10 permutations53. This procedure calculates the Pearson’s correlation between the standard predictions (i.e. fitted values) and predictions where one variable has been randomly permutated, thus allowing direct comparison between models regardless of the modelling method. When the correlation between the two predictions is low, it indicates that the variable is important in the model, and when the correlation is high the variable is not important. The mean correlation coefficient is calculated over multiple runs. The relative importance of each explanatory variable is calculated by subtracting the mean correlation coefficient from 1, so each variable is ranked from zero to one. Variables with zero ranking have no influence in the model, while variables ranked high (closest to one) are considered as the most influential53.

The data-splitting procedure allows the evaluation of model accuracy (or predictive performance) when data are non-independent53. The area under the receiver operating characteristics curve (AUC) was used to assess SDMs predictive performance and compare SMDs104. As non-independent data were used for model evaluation, variability in model accuracy can be interpreted as a measure of the sensitivity of the model results to the initial conditions rather than as a measure of predictive accuracy53,105. Here we assumed that models with AUC < 0.7 had poor predictive performance, 0.7 ≤ AUC < 0.9 moderate to good, and AUC ≥ 0.9 excellent performance105.

Finally, the five modelling methods were combined to obtain an ensemble prediction of dolphin presence53. To generate the ensemble models, only SDMs with AUC ≥ 0.7 were considered and the contribution of selected SDMs to the ensemble model was weighted based on their predictive accuracy106. Maps of probability of dolphin occurrence were created based on the ensemble models, where values closer to zero indicate low probabilities, and values closer to one indicate higher probability of presence. When using distribution models to predict occurrence probability of a species to other areas, the values of explanatory variables in the original study area have to be within the ranges of values in the new areas to avoid overestimating the suitability of new areas2,92. Since the inner and outer areas of Coffin Bay differ in the ranges of explanatory variables (see Results; Supplementary Appendix 1, Fig. S2), and to avoid making predictions to new collinearity structures in space and/or time96, the ensemble predictions of dolphin distribution were done only for the areas corresponding to each dataset (i.e., either the whole Coffin Bay or the inner area only). These included cells where data on explanatory variables was available but had no presence-absence records because of low or null survey effort. Lastly, the performance between the ensemble and single SDMs was compared using AUC values106.

To evaluate the relevance of the current zoning of the MPA to the protection of dolphins, the sanctuary zones were overlapped with the predicted values of dolphin occurrence (from the ensemble models), and the mean probability of occurrence (per cell) in each sanctuary zone was estimated.


This study was carried out in accordance to the Flinders University Animal Welfare Committee under the ethics approval of project number E310. Fieldwork was done under Permits to Undertake Scientific Research (numbers: E26171-1, E26171-2, E26171-3 and MR00056-1) from the Department of Environment, Water and Natural Resources (DEWNR), South Australia, and under S115 Ministerial Exemptions (MEs: 9902601, 9902660, 9902714 and 9902779) provided by Primary Industries Resources South Australia (PIRSA).

Data Availability Statement

Data made available to all interested researchers upon reasonable request to Cecilia Passadore ( and Guido J. Parra (

Additional information

Publisher’s note: Springer Nature remains neutral with regard to jurisdictional claims in published maps and institutional affiliations.


  1. 1.

    Guisan, A. & Thuiller, W. Predicting species distribution: offering more than simple habitat models. Ecology letters 8, 993–1009 (2005).

  2. 2.

    Franklin, J. Mapping species distributions: spatial inference and prediction. (Cambridge University Press, 2010).

  3. 3.

    Redfern, J. V. et al. Techniques for cetacean–habitat modeling. Marine Ecology Progress Series 310, 271–295 (2006).

  4. 4.

    Bearzi, G. et al. Dolphins in a scaled-down Mediterranean: the gulf of Corinth’s odontocetes. Advances in Marine Biology 75, 297–331, (2016).

  5. 5.

    Bonizzoni, S. et al. Fish farming and its appeal to common bottlenose dolphins: modelling habitat use in a Mediterranean embayment. Aquatic Conservation: Marine and Freshwater Ecosystems 24, 696–711 (2014).

  6. 6.

    Lusseau, D. & Bejder, L. The long-term consequences of short-term responses to disturbance experiences from whalewatching impact assessment. International Journal of Comparative Psychology 20, 228–236 (2007).

  7. 7.

    Elith, J. & Leathwick, J. R. Species distribution models: ecological explanation and prediction across space and time. Annual Review of Ecology, Evolution, and Systematics 40, 677–697, (2009).

  8. 8.

    Guisan, A. et al. Predicting species distributions for conservation decisions. Ecology Letters 16, 1424–1435, (2013).

  9. 9.

    Halpern, B. S. et al. A global map of human impact on marine ecosystems. Science 319, 948–952, (2008).

  10. 10.

    Reeves, R. R., Smith, B. D., Crespo, E. A. & Sciara, G. N. d. Dolphins, whales and porpoises: 2002–2010 conservation action plan for the world’s cetaceans. Vol. 58 ix+139pp (IUCN, 2003).

  11. 11.

    Monk, A., Charlton-Robb, K., Buddhadasa, S. & Thompson, R. M. Comparison of mercury contamination in live and dead dolphins from a newly described species. Tursiops australis. PLoS ONE 9, e104887, (2014).

  12. 12.

    Rojas‐Bracho, L., Reeves, R. R. & Jaramillo‐Legorreta, A. Conservation of the vaquita Phocoena sinus. Mammal Review 36, 179–216, (2006).

  13. 13.

    Atkins, S. et al. Net loss of endangered humpback dolphins: integrating residency, site fidelity, and bycatch in shark nets. Marine Ecology Progress Series 555, 249–260, (2016).

  14. 14.

    Currey, R. J., Dawson, S. M. & Slooten, E. New abundance estimates suggest Doubtful Sound bottlenose dolphins are declining. Pacific Conservation Biology 13, 274–282, (2007).

  15. 15.

    Parra, G. J. & Cagnazzi, D. in Advances in marine biology Vol. 73 (eds Thomas, A. Jefferson & Barbara, E. Curry) 157–192 (Academic Press, 2016).

  16. 16.

    Cagnazzi, D., Parra, G. J., Westley, S. & Harrison, P. L. At the heart of the industrial boom: Australian snubfin dolphins in the Capricorn Coast, Queensland, need urgent conservation action. PLoS ONE 8, e56729 (2013).

  17. 17.

    Guerra, M. & Dawson, S. M. Boat-based tourism and bottlenose dolphins in Doubtful Sound, New Zealand: The role of management in decreasing dolphin-boat interactions. Tourism Management 57, 3–9, (2016).

  18. 18.

    Hooker, S. K. et al. Making protected area networks effective for marine top predators. Endangered Species Research 13, 203–218 (2011).

  19. 19.

    Notarbartolo di Sciara, G. et al. Place‐based approaches to marine mammal conservation. Aquatic Conservation: Marine and Freshwater Ecosystems 26, 85–100 (2016).

  20. 20.

    Davidson, A. D. et al. Drivers and hotspots of extinction risk in marine mammals. Proceedings of the National Academy of Sciences 109, 3395–3400, (2012).

  21. 21.

    Grech, A. & Marsh, H. Rapid assessment of risks to a mobile marine mammal in an ecosystem-scale marine protected area. Conservation Biology 22, 711–720, (2008).

  22. 22.

    Bilgmann, K., Möller, L. M., Harcourt, R. G., Gales, R. & Beheregaray, L. B. Common dolphins subject to fisheries impacts in Southern Australia are genetically differentiated: implications for conservation. Anim Conserv 11, 518–528 (2008).

  23. 23.

    Hamer, D. J., Ward, T. M. & McGarvey, R. Measurement, management and mitigation of operational interactions between the South Australian Sardine Fishery and short-beaked common dolphins (Delphinus delphis). Biological Conservation 141, 2865–2878, (2008).

  24. 24.

    Kemper, C. M. & Gibbs, S. E. Dolphin interactions with tuna feedlots at Port Lincoln, South Australia and recommendations for minimising entanglements. J Cetacean Res Manag 3, 283–292 (2001).

  25. 25.

    Robbins, W. D., Huveneers, C., Parra, G. J., Möller, L. & Gillanders, B. M. Anthropogenic threat assessment of marine-associated fauna in Spencer Gulf, South Australia. Marine Policy 81, 392–400, (2017).

  26. 26.

    Hammond, P. S. et al. Tursiops truncatus. The IUCN Red List of Threatened Species, e.T22563A17347397, (2012).

  27. 27.

    Hammond, P. S. et al. Tursiops aduncus. The IUCN Red List of Threatened Species, e.T41714A17600466, (2012).

  28. 28.

    Charlton-Robb, K. et al. A new dolphin species, the Burrunan dolphin Tursiops australis sp nov., endemic to southern Australian coastal waters. PLoS ONE 6, e24047, (2011).

  29. 29.

    Perrin, W. F., Rosel, P. E. & Cipriano, F. How to contend with paraphyly in the taxonomy of the delphinine cetaceans? Marine Mammal Science 29, 567–588, (2013).

  30. 30.

    Committee on Taxonomy. List of marine mammal species and subspecies. Society for Marine Mammalogy,, consulted on June 2016 (2016).

  31. 31.

    Charlton-Robb, K., Taylor, A. C. & McKechnie, S. W. Population genetic structure of the Burrunan dolphin (Tursiops australis) in coastal waters of south-eastern Australia: conservation implications. Conserv Genet 16, 195–207, (2015).

  32. 32.

    Bilgmann, K., Möller, L. M., Harcourt, R. G., Gibbs, S. E. & Beheregaray, L. B. Genetic differentiation in bottlenose dolphins from South Australia: association with local oceanography and coastal geography. Marine Ecology Progress Series 341, 265–276, (2007).

  33. 33.

    Bilgmann, K., Griffiths, O. J., Allen, S. J. & Möller, L. M. A biopsy pole system for bow‐riding dolphins: sampling success, behavioral responses, and test for sampling bias. Marine Mammal Science 23, 218–225, (2007).

  34. 34.

    Pratt, E. A. L. et al. Hierarchical metapopulation structure in a highly mobile marine predator: the southern Australia coastal bottlenose dolphin (Tursiops cf. australis). Conserv Genet, 1–18, (2018).

  35. 35.

    Cribb, N., Miller, C. & Seuront, L. Indo-Pacific bottlenose dolphin (Tursiops aduncus) habitat preference in a heterogeneous, urban, coastal environment. Aquatic biosystems 9, 1–9, (2013).

  36. 36.

    Zanardo, N., Parra, G. J., Passadore, C. & Möller, L. M. Ensemble modelling of southern Australian bottlenose dolphin Tursiops sp. distribution reveals important habitats and their potential ecological function. Marine Ecology Progress Series 569, 253–266 (2017).

  37. 37.

    Passadore, C., Möller, L., Diaz-Aguirre, F. & Parra, G. J. Demography of southern Australian bottlenose dolphins living in a protected inverse estuary. Aquatic Conservation: Marine and Freshwater Ecosystems 27, 1186–1197, (2017).

  38. 38.

    DEH. Parks of the Coffin Bay Area Management Plan. (Department for Environment and Heritage, Adelaide, South Australia, 2004).

  39. 39.

    Kämpf, J. & Ellis, H. Hydrodynamics and flushing of Coffin Bay, South Australia: a small tidal inverse estuary of interconnected bays. Journal of Coastal Research 31, 447–456, (2015).

  40. 40.

    Passadore, C., Möller, L., Diaz-Aguirre, F. & Parra, G. J. High site fidelity and restricted ranging patterns in southern Australian bottlenose dolphins. Ecology and Evolution 8, 242–256, (2018).

  41. 41.

    Saunders, B. Shores and shallows of Coffin Bay. An identification guide. 152 (Australian Printing Specialists, 2009).

  42. 42.

    DENR. Environmental, Economic and Social Values of the Thorny Passage Marine Park Part 1. (Department of Environment and Natural Resources, South Australia, 2010).

  43. 43.

    DEWNR. Thorny Passage Marine Park Management Plan 2012. (Department of Environment, Water and Natural Resources, Government of South Australia, South Australia, 2012).

  44. 44.

    Markowitz, T. M., Harlin, A. D., Würsig, B. & McFadden, C. J. Dusky dolphin foraging habitat: overlap with aquaculture in New Zealand. Aquatic Conservation: Marine and Freshwater Ecosystems 14, 133–149 (2004).

  45. 45.

    Pearson, H., Vaughn-Hirshorn, R., Srinivasan, M. & Würsig, B. Avoidance of mussel farms by dusky dolphins (Lagenorhynchus obscurus) in New Zealand. New Zealand Journal of Marine and Freshwater Research 46, 567–574 (2012).

  46. 46.

    Ribeiro, S., Viddi, F. A., Cordeiro, J. L. & Freitas, T. R. Fine-scale habitat selection of Chilean dolphins (Cephalorhynchus eutropia): interactions with aquaculture activities in southern Chiloé Island, Chile. Journal of the Marine Biological Association of the United Kingdom 87, 119–128 (2007).

  47. 47.

    Watson-Capps, J. J. & Mann, J. The effects of aquaculture on bottlenose dolphin (Tursiops sp.) ranging in Shark Bay, Western Australia. Biological Conservation 124, 519–526, (2005).

  48. 48.

    Bejder, L., Samuels, A., Whitehead, H. & Gales, N. Interpreting short-term behavioural responses to disturbance within a longitudinal perspective. Animal Behaviour 72, 1149–1158 (2006).

  49. 49.

    Lemon, M., Lynch, T. P., Cato, D. H. & Harcourt, R. G. Response of travelling bottlenose dolphins (Tursiops aduncus) to experimental approaches by a powerboat in Jervis Bay, New South Wales, Australia. Biological Conservation 127, 363–372, (2006).

  50. 50.

    Pirotta, E., Merchant, N. D., Thompson, P. M., Barton, T. R. & Lusseau, D. Quantifying the effect of boat disturbance on bottlenose dolphin foraging activity. Biological Conservation 181, 82–89, (2015).

  51. 51.

    Kemper, C. M. et al. Cetacean captures, strandings and mortalities in South Australia 1881–2000, with special reference to human interactions. Australian Mammalogy 27, 37–47, (2005).

  52. 52.

    Bejder, L. et al. Decline in relative abundance of bottlenose dolphins exposed to long‐term disturbance. Conservation Biology 20, 1791–1798 (2006).

  53. 53.

    Thuiller, W., Lafourcade, B., Engler, R. & Araújo, M. B. BIOMOD–a platform for ensemble forecasting of species distributions. Ecography 32, 369–373 (2009).

  54. 54.

    Acevedo-Gutiérrez, A. & Parker, N. Surface behavior of bottlenose dolphins is related to spatial arrangement of prey. Marine Mammal Science 16, 287–298, (2000).

  55. 55.

    Heithaus, M. R. & Dill, L. M. Does tiger shark predation risk influence foraging habitat use by bottlenose dolphins at multiple spatial scales? Oikos 114, 257–264, (2006).

  56. 56.

    McCluskey, S. M., Bejder, L. & Loneragan, N. R. Dolphin prey availability and calorific value in an estuarine and coastal environment. Frontiers in Marine Science 3,, (2016).

  57. 57.

    Di Tullio, J. C., Fruet, P. F. & Secchi, E. R. Identifying critical areas to reduce bycatch of coastal common bottlenose dolphins Tursiops truncatus in artisanal fisheries of the subtropical western South Atlantic. Endangered Species. Research 29, 35–50, (2015).

  58. 58.

    Parra, G. J., Schick, R. & Corkeron, P. J. Spatial distribution and environmental correlates of Australian snubfin and Indo-Pacific humpback dolphins. Ecography 29, 396–406, (2006).

  59. 59.

    Kämpf, J. In Estuaries of Australia in 2050 and beyond (ed.Wolanski, E.) 153–166 (Springer, 2014).

  60. 60.

    EPA. Water quality report for Douglas Nearshore Marine Biounit,, consulted onJune 2016 (Environment Protection Authority, 2014).

  61. 61.

    Gibbs, S. E., Harcourt, R. G. & Kemper, C. M. Niche differentiation of bottlenose dolphin species in South Australia revealed by stable isotopes and stomach contents. Wildlife Research 38, 261–270, (2011).

  62. 62.

    Bruce, B. D. Preliminary observations on the biology of the white shark, Carcharodon carcharias, in South Australian waters. Australian Journal of Marine and Freshwater Research 43, 1–11, (1992).

  63. 63.

    Bruce, B., Stevens, J. & Malcolm, H. Movements and swimming behaviour of white sharks (Carcharodon carcharias) in Australian waters. Marine Biology 150, 161–172, (2006).

  64. 64.

    Sprogis, K. R., Raudino, H. C., Rankin, R., MacLeod, C. D. & Bejder, L. Home range size of adult Indo-Pacific bottlenose dolphins (Tursiops aduncus) in a coastal and estuarine system is habitat and sex-specific. Marine Mammal Science 32, 287–308, (2016).

  65. 65.

    Zanardo, N., Parra, G. J. & Möller, L. M. Site fidelity, residency, and abundance of bottlenose dolphins (Tursiops sp.) in Adelaide’s coastal waters, South Australia. Marine Mammal Science 32, 1381–1401, (2016).

  66. 66.

    Tanner, C. J. & Jackson, A. L. Social structure emerges via the interaction between local ecology and individual behaviour. J Anim Ecol 81, 260–267, (2012).

  67. 67.

    Blondel, D. V., Pino, J. & Phelps, S. M. Space use and social structure of long-tailed singing mice (Scotinomys xerampelinus). J Mammal 90, 715–723, (2009).

  68. 68.

    Campbell, P., Akbar, Z., Adnan, A. M. & Kunz, T. H. Resource distribution and social structure in harem-forming Old World fruit bats: variations on a polygynous theme. Anim Behav 72, 687–698, (2006).

  69. 69.

    Diaz-Aguirre, F. Socio-genetic structure of southern Australian bottlenose dolphins (Tursiops cf. australis) In a South Australian embayment PhD thesis, Flinders University, (2017).

  70. 70.

    Kemper, C. M. et al. In Marine mammals: fisheries, tourism and management issues (eds Nick Gales, Mark Hindell, & Roger Kirkwood) Ch. 11, 208–228 (CSIRO, 2006).

  71. 71.

    Díaz-López, B., Bunke, M. & Shirai, J. A. B. Marine aquaculture off Sardinia Island (Italy): ecosystem effects evaluated through a trophic mass-balance model. Ecological modelling 212, 292–303 (2008).

  72. 72.

    Würsig, B. & Gailey, G. Marine mammals and aquaculture: conflicts and potential resolutions. (CAP International Press, 2002).

  73. 73.

    Bryars, S. et al. Baseline and predicted changes for the Thorny Passage Marine Park. (Department of Environment, Water and Natural Resources, Government of South Australia, Adelaide, 2016).

  74. 74.

    Petrusevics, P. SST fronts in inverse estuaries, South Australia-indicators of reduced gulf-shlef exchange. Marine and Freshwater Research 44, 305–323, (1993).

  75. 75.

    Kämpf, J., Doubell, M., Griffin, D., Matthews, R. L. & Ward, T. M. Evidence of a large seasonal coastal upwelling system along the southern shelf of Australia. Geophysical Research Letters 31, L09310, (2004).

  76. 76.

    Strindberg, S. & Buckland, S. T. Zigzag survey designs in line transect sampling. Journal of Agricultural, Biological, and Environmental Statistics 9, 443–461 (2004).

  77. 77.

    Wells, R. S., Irvine, A. B. & Scott, M. D. In Cetacean Behavior: Mechanisms and Functions (ed. Louis Herman, M.) 263–317 (Wiley 1980).

  78. 78.

    Lerczak, J. A. & Hobbs, R. C. Calculating sightings distances from angular readings during shipboard, aerial and shore-based marine mammal surveys. Marine Mammal Science 14, 590–598, (1998).

  79. 79.

    MacKenzie, D. I. & Royle, J. A. Designing occupancy studies: general advice and allocating survey effort. Journal of applied Ecology 42, 1105–1114 (2005).

  80. 80.

    MacLeod, C. D., Weir, C. R., Pierpoint, C. & Harland, E. J. The habitat preferences of marine mammals west of Scotland (UK). Journal of the Marine Biological Association of the United Kingdom 87, 157–164 (2007).

  81. 81.

    Barbet-Massin, M., Jiguet, F., Albert, C. H. & Thuiller, W. Selecting pseudo-absences for species distribution models: how, where and how many? Methods in Ecology and Evolution 3, 327–338, (2012).

  82. 82.

    Gu, W. & Swihart, R. K. Absent or undetected? Effects of non-detection of species occurrence on wildlife–habitat models. Biological Conservation 116, 195–203, (2004).

  83. 83.

    Phillips, S. J. et al. Sample selection bias and presence-only distribution models: implications for background and pseudo-absence data. Ecological Applications 19, 181–197 (2009).

  84. 84.

    Rayment, W., Dawson, S. & Webster, T. Breeding status affects fine‐scale habitat selection of southern right whales on their wintering grounds. Journal of Biogeography 42, 463–474 (2015).

  85. 85.

    Elith, J. et al. A statistical explanation of MaxEnt for ecologists. Diversity and Distributions 17, 43–57, (2011).

  86. 86.

    Cañadas, A. & Hammond, P. S. Abundance and habitat preferences of the short-baked common dolphin Delphinus delphis in the southwestern Mediterranean: implications for conservation. Endangered species research 4, 309–331, (2008).

  87. 87.

    Rayment, W., Dawson, S. & Slooten, E. Seasonal changes in distribution of Hector’s dolphin at Banks Peninsula, New Zealand: implications for protected area design. Aquatic Conservation: Marine and Freshwater Ecosystems 20, 106–116 (2010).

  88. 88.

    Guisan, A., Edwards, T. C. Jr. & Hastie, T. Generalized linear and generalized additive models in studies of species distributions: setting the scene. Ecological modelling 157, 89–100 (2002).

  89. 89.

    Friedman, J., Hastie, T. & Tibshirani, R. Additive logistic regression: a statistical view of boosting (with discussion and a rejoinder by the authors). The annals of statistics 28, 337–407 (2000).

  90. 90.

    De’ath, G. & Fabricius, K. E. Classification and regression trees: A powerful yet simple technique for ecological data analysis. Ecology 81, 3178–3192,[3178:CARTAP]2.0.CO;2 (2000).

  91. 91.

    Breiman, L. Random Forests. Machine Learning 45, 5–32, (2001).

  92. 92.

    Phillips, S. J., Anderson, R. P. & Schapire, R. E. Maximum entropy modeling of species geographic distributions. Ecological modelling 190, 231–259 (2006).

  93. 93.

    Elith, J. & Graham, C. H. Do they? How do they? WHY do they differ? On finding reasons for differing performances of species distribution models. Ecography 32, 66–77 (2009).

  94. 94.

    Elith, J. et al. Novel methods improve prediction of species’ distributions from occurrence data. Ecography 29, 129–151, (2006).

  95. 95.

    Phillips, S. J., Anderson, R. P., Dudík, M., Schapire, R. E. & Blair, M. E. Opening the black box: an open-source release of Maxent. Ecography 40, 887–893, (2017).

  96. 96.

    Dormann, C. F. et al. Collinearity: a review of methods to deal with it and a simulation study evaluating their performance. Ecography 36, 27–46 (2013).

  97. 97.

    Zuur, A. F., Ieno, E. N. & Elphick, C. S. A protocol for data exploration to avoid common statistical problems. Methods in Ecology and Evolution 1, 3–14, (2010).

  98. 98.

    Naimi, B. usdm: Uncertainty analysis for species distribution models. R package version 1, 1–12 (2015).

  99. 99.

    Hijmans, R. J. Cross‐validation of species distribution models: removing spatial sorting bias and calibration with a null model. Ecology 93, 679–688 (2012).

  100. 100.

    Bucklin, D. N. et al. Comparing species distribution models constructed with different subsets of environmental predictors. Diversity and Distributions 21, 23–35 (2015).

  101. 101.

    Watling, J. I. et al. Performance metrics and variance partitioning reveal sources of uncertainty in species distribution models. Ecological Modelling 309, 48–59 (2015).

  102. 102.

    Pikesley, S. K. et al. Modelling the niche for a marine vertebrate: a case study incorporating behavioural plasticity, proximate threats and climate change. Ecography 38, 001–010, (2015).

  103. 103.

    Scales, K. L. et al. Identifying predictable foraging habitats for a wide‐ranging marine predator using ensemble ecological niche models. Diversity and Distributions 22, 212–224 (2016).

  104. 104.

    Fielding, A. H. & Bell, J. F. A review of methods for the assessment of prediction errors in conservation presence/absence models. Environmental conservation 24, 38–49 (1997).

  105. 105.

    Araújo, M. B. & Guisan, A. Five (or so) challenges for species distribution modelling. Journal of biogeography 33, 1677–1688 (2006).

  106. 106.

    Marmion, M., Parviainen, M., Luoto, M., Heikkinen, R. K. & Thuiller, W. Evaluation of consensus methods in predictive species distribution modelling. Diversity and distributions 15, 59–69 (2009).

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Funding for this project was provided by Flinders University, Lirabenda Endowment Fund of the Field Naturalists Society of South Australia, Nature Foundation South Australia Inc., and Holsworth Wildlife Research Endowment (ANZ and Equity Trustees). C. Passadore had an Australian Development Scholarship by the Australian Agency for International Development (AusAID). Especial thanks to all the volunteers who assisted in data collection: E. Heber, I. Reis, F. Schlichta, K. Indeck, J. Lucas, M. Valdivia, F. Vivier, J. Rodriguez, E. Wilson, D. Carter, Y. Mevorach, and E. Benavente. J. Kaempf from the School of the Environment, Flinders University, and H. Rammers from South Australia Shellfish Quality Assurance Program, Primary Industries and Resources South Australia, provided a multiparameter to collect environmental data.

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  1. Cetacean Ecology, Behaviour and Evolution Lab, College of Science and Engineering, Flinders University, South Australia, 5001, Australia

    • Cecilia Passadore
    • , Luciana M. Möller
    • , Fernando Diaz-Aguirre
    •  & Guido J. Parra
  2. Molecular Ecology Lab, College of Science and Engineering, Flinders University, South Australia, 5001, Australia

    • Luciana M. Möller
    •  & Fernando Diaz-Aguirre


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C.P., G.J.P. and L.M.M. conceived and designed the study. C.P. and F.D.A. collected the data. C.P. processed and analysed the data with advice and contributions to data analysis from G.J.P. and L.M.M. C.P. wrote the manuscript with contributions to drafting, critical review, and editorial input from G.J.P., L.M.M. and F.D.A.

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The authors declare no competing interests.

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Correspondence to Cecilia Passadore.

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