Marine ecosystems are the most extensive and among the most threatened in the world (MEA, 2005). The increasing rates of exploitation and incidental capture in the fisheries industry (Halpern et al., 2007) often exhibit disproportionate impacts on marine megafauna (Abercrombie, Balchowsky & Paine, 2005; Read, Drinker & Northridge, 2006; Capietto et al., 2014). The consequences and subsequent declines are far reaching; marine megafauna are often apex predators, therefore, their removal has cascading impacts on lower tropic levels, causing community restructuring and enhanced vulnerability of other species (Lewison et al., 2004; Casini et al., 2008; Howarth et al., 2014). Impacts are not only ecological; presence of megafauna often significantly contributes to local economies through ecotourism (Catlin & Jones, 2010). Despite their importance, little is understood about the factors affecting the movements and global distributions of many marine megafauna species. Identifying and understanding areas used in important periods of their life is essential for future conservation efforts (Hays et al., 2016). The whale shark (Rhincodon typus) is one such species where there are still many knowledge gaps about their global distribution, movements and the factors affecting these (Sequeira et al., 2013).
Rhincodon typus is one of three large pelagic filter feeding shark species and is the largest fish in the world (Smith, 1828). They have a circumglobal distribution, found in tropical and warm temperate seas between the latitudes of 30°N and 35°S (Pierce & Norman, 2016). As filter feeders, R. typus primarily feed on zooplankton and therefore tend to be observed in areas with high productivity (Colman, 1997; Rohner et al., 2018). However, recent studies have shown whale sharks also feed on the spawn of various corals, fish and invertebrates (Graham & Roberts, 2007; Hobbs et al., 2009; Rohner et al., 2016). There is no robust population estimation for this species, but it is listed as endangered on the IUCN Red List (Pierce & Norman, 2016). Their late sexual maturation, highly mobile nature and relatively low abundance make this species extremely vulnerable, particularly to incidental capture and overexploitation, which has caused global population decline and fragmentation (Dulvy et al., 2008; Pierce & Norman, 2016). More recently, the economic value of live whale sharks to ecotourism has been shown to be considerably higher than when fished (Catlin & Jones, 2010; Cagua et al., 2014). A report published by the WWF-Philippines (Pine, 2007) estimates the value of a whale shark to be worth US$250,000 dead, or US$2,000,000 provided in ecotourism benefits over the animal’s lifetime.
The importance of this species has triggered a growing interest amongst the scientific community, with the majority of papers on R. typus published within the past two decades. Together with the increases in ecotourism, there is now a depth of knowledge about local and regional whale shark ecology and biology. Yet there is still a dearth of information about global distribution, especially connectivity of populations and pattern in movements (Sequeira et al., 2012; Sequeira et al., 2013). R. typus were once perceived to be solitary animals that live and feed in the open ocean, but it is now well documented that juvenile whale sharks do aggregate in response to the forming of predictable, seasonal feeding opportunities (Colman, 1997; Heyman et al., 2001; Riley et al., 2010).
An increasing number of coastal aggregation areas are being discovered, with research showing there could be up to 25 sites globally (Colman, 1997; Eckert et al., 2002; Andrzejaczek et al., 2016). Nevertheless, 25 sites is a very small number in all of the world’s oceans, indicating that whale sharks only aggregate in response to a very specific set of conditions. There is great variability among aggregation events in terms of available prey, when they occur and the number of individuals aggregating (Rowat & Brooks, 2012; Andrzejaczek et al., 2016). Studies have shown R. typus aggregate in areas of high biological productivity and the seasonal nature of such aggregations appears to be the result of local increases in prey (Meekan et al., 2006; Rowat et al., 2007; Rowat et al., 2009). The timing of a number of aggregations is predictable due to the close association with increased prey availability. For example, Heyman et al. (2001) show whale sharks are only regularly seen in large numbers at Gladden Spit, Belize, during full moon periods in April and May where a large number aggregate to feed on Lutjanidae spp. spawn. This is again reflected in the Gulf of Tadjouran, Djibouti, when throughout the winter months (November to February) a large aggregation of R. typus can be observed feeding on zooplankton (Rowat et al., 2007). There are disparities in aggregation size and structure between sites; numbers vary from 10 to 1,000-plus individuals and exhibit a spatial segregation by age and gender, typical in shark populations (Springer, 1967; Brunnschweiler et al., 2009; De la Parra Venegas et al., 2011).
R. typus is a pelagic species believed to spend most of their lives in deep offshore waters except during aggregation events, which are thought to be predominantly seasonal (Abercrombie, Balchowsky & Paine, 2005; Andrzejaczek et al., 2016). There have only been a handful of studies researching the deep diving behaviour of R. typus, nonetheless they suggest R. typus dive to the mesopelagic zone to feed (Graham, Roberts & Smart, 2006; Brunnschweiler et al., 2009; Sun et al., 2016). Using pop-up satellite archival tags, Tyminski et al. (2015) recorded one individual diving to a depth of 1,928 m in the north-eastern Gulf of Mexico. These studies indicate deep water is important for R. typus, therefore the neighbouring bathymetry could play a role in aggregation events.
Bathymetric features such as continental and reef slopes, shallow banks and seamounts tend to be areas of high marine productivity, in particular high zooplankton abundance, often driving predator prey aggregations (Afonso, McGinty & Machete, 2014). Bouchet et al. (2015) show areas with complex bathymetry such as seamounts or steep slopes found on outer reefs accumulate zooplankton, which subsequently attracts filter feeders, particularly at epipelagic and mesopelagic depths. This was shown by Sims (2008) with a greater abundance of basking sharks (Cetorhinus maximus) in areas with steeper slopes, owing to the higher densities of zooplankton.
Studies have shown almost all R. typus aggregations occur in coastal areas of shallow bathymetry in close proximity to the reef slope and deeper water (De la Parra Venegas et al., 2011; Donati et al., 2016; Diamant et al., 2016). Past studies have illustrated increased zooplankton availability in areas of steep bathymetry, which R. typus preys upon (Bouchet et al., 2015). Therefore, bathymetry at and around areas of aggregation events could be an important factor in driving them. There are currently few in-depth studies into bathymetry and R. typus globally (Sleeman et al., 2007; Rohner et al., 2013; Sequeira et al., 2012) use coarse scale bathymetry data to look at the distribution of R. typus, and McKinney et al. (2012) use bathymetry to investigate the feeding habitat of R. typus in the Gulf of Mexico. However, the current lack of highly detailed studies into bathymetry and R. typus could limit future conservation efforts for this species (Rowat & Brooks, 2012).
Our study therefore aims to address this knowledge gap by investigating whether there is an association between bathymetry and R. typus feeding aggregation sites by quantitatively analysing previous qualitative and anecdotal observations. We will address the following questions: Are there similarities in bathymetry between aggregation sites? How does this compare to bathymetry at non-aggregation sites? Which bathymetric variables are most associated with aggregations? And, what is the biggest potential driver of aggregations? By addressing these key questions, we will deliver a quantitative update to previous qualitative research and aim to provide an increased understanding of the bathymetric conditions at R. typus aggregation sites.
Materials & Methods
To identify R. typus aggregation sites, an extensive literature review was done using the following search terms in Web of Science and Google Scholar: Whale shark, Rhincodon typus, aggregation, coastal, bathymetry, topography, relief, depth, movements, feeding. All relevant articles (in excess of 150) were evaluated and papers that mentioned aggregations were retained for further use. From these, a database of 17 aggregation events was created containing size, spatial and temporal occurrence and coordinates at the centre of the aggregation. Although more sites were found in the literature search (Gulf of Oman (Robinson et al., 2016), Japan (Colman, 1997), Tawian (Stewart & Wilson, 2005; Hsu, Joung & Liu, 2012) and Thailand (Theberge & Dearden, 2006)), there was a lack of detailed location information and no clarity as to if these were recognised aggregations or one-off events. Therefore, these potential additional sites could not be used accurately in our analysis and were not included in this study. See Table 1 for a list of the included aggregation sites.
Furthermore, three of the 17 aggregation sites appeared vastly different from the other sites in this study. The Al Shaheen Oil Field site aggregation, Qatar, described by Robinson et al. (2013) is an area of high whale shark abundance, however it is not coastal and is dispersed over a large area, therefore not considered a truly comparable aggregation. Literature suggests the aggregations around the Mississippi Delta and the Christmas Island aggregation are driven by unique ecological phenomena. The aggregation in the Gulf of Mexico appears to be driven by runoff from the Mississippi stimulating high primary productivity at a scale far higher than other aggregation sites (Hoffmayer et al., 2007; Hueter, Tyminski & De la Parra, 2013). Meanwhile, the Christmas Island aggregation is driven by red crab (Gecarcoidea natalis) spawning events which do not occur at any other sites (Hobbs et al., 2009; Meekan et al., 2009). Moreover, these three sites have considerably fewer literature describing the aggregations compared to the other sites in this study. Therefore, for the purpose of this study we decided these sites were not comparable with the other 14 well-known large aggregations.
The global range of R. typus was obtained from the IUCN (International Union for Conservation of Nature , IUCN) to examine the spatial distribution of aggregation sites. Bathymetric depth data were obtained from the 2014 General Bathymetric Chart of the Oceans (GEBCO, 2015) at a resolution of 30 arc-seconds (approximately 1 km). The GEBCO dataset was highest resolution, freely available bathymetric that covered the whole study area. Whilst more detailed datasets are available for specific areas such as Western Australia, there is no comparable data for many of the areas in the tropics, therefore the GEBCO dataset was used throughout to ensure consistency and to allow comparison between sites. To examine relationships between bathymetry, primary productivity and their association with whale shark aggregations we also obtained data on sea surface temperature (SST) and chlorophyll-a concentration from OceanColor (NASA, 2014), an archive of oceanographic data from satellite based remote sensing. SST data were a seasonal composite of the years 2000 to 2016 at a 4 km resolution recorded by the Terra MODIS instrument. The seasonal composite of chlorophyll-a concentration from 2012 to 2016 at a 4 km resolution, recorded by the SNPP-VIIRS instrument was also used. Seasonal composites were used as R. typus aggregate seasonally and a composite of a number of years should mitigate the influence of anomalies such as El Niño.
R. typus aggregation point data were imported, and locations re-checked against source papers to ensure locations were correct. To investigate if aggregation sites are unique, they were compared to areas where aggregations do not occur; therefore, 1,000 random points in non-aggregation areas were created (Fig. 1). 1,000 points were chosen to allow a large geographic spread within R. typus’ range to capture a range of bathymetric characteristics. Whilst there is no consensus on the correct number of pseudo absence points to include, the large number of pseudo absence points we used allowed for a powerful comparison with aggregation sites. Although R. typus has a global range, the aggregations in this study are coastal, therefore unproductive and deep high seas areas were excluded, as these would have biased our absence data. Thus, random points were constrained to coastal areas by calculating the maximum distance of the observed aggregation sites from the coast (26 km) and using this to create a zone around coastlines within R. typus’ range. Due to the resolution of the bathymetry data, each point covers an area of approximately 1 km2. Aspect, slope and vertical/profile curvature, hereafter referred to as “curvature”, layers were generated from bathymetric depth to further examine the characteristics of bathymetry in key areas. Positive values of curvature indicate upwardly concave slopes, negative values show upwardly convex slopes, and values close to 0 indicate planar slopes. Benthic complexity was generated from the standard deviation of depth and slope roughness was generated as the standard deviation of slope. Although there are other ways to measure complexity and roughness, using the standard deviation of slope or depth is one of the most simple and effective measures at a variety of scales (Fox & Hayes, 1985; Grohmann, Smith & Riccomini, 2011). These variables were chosen based on similar research focusing on both R. typus and other marine megafauna species (Sleeman et al., 2007; Sequeira et al., 2012; Afonso, McGinty & Machete, 2014; Bouchet et al., 2015).
Twenty km buffer zones were generated around each aggregation and random point, allowing extraction of information about the surrounding areas. This size of zone was selected based on distances R. typus travels; Hueter, Tyminski & De la Parra (2013) show the mean daily distance travelled during long distance movements to be 24.7 km, which would be lower during aggregation events with the focus on feeding. Minimum, maximum, mean, range were extracted for depth, complexity, slope and curvature for the point data and buffer zones. SST and chlorophyll data were extracted by the same method but only for point data, not buffer zones due to the lower resolution of these data, where one cell covers a large portion of the buffer zone. The distance of aggregation sites to the 200 m and 1,000 m isobaths (mesopelagic and bathypelagic zones) were also measured as these depths were previously shown to be important for R. typus feeding (Brunnschweiler et al., 2009).
Of the 1,000 random points, five had missing data for one or more variables so were removed, leaving 995 random points for analysis. Literature shows aggregations occur in the seasons with the highest chlorophyll-a concentration and SST (Sequeira et al., 2012; Afonso, McGinty & Machete, 2014). Therefore, maximum values across the four seasons were extracted and used during analysis. Basic statistics were run on the variables, examining means and variance to initially look for differences in the data. To test whether differences between aggregation and non-aggregation sites were significant, an independent samples t-test was used. This was chosen due to its power and robustness, particularly with large datasets (Zimmerman, 1987; Erceg-Hurn & Mirosevich, 2008). Generalised linear models (GLMs) with a binomial error function were used to investigate which variable had the greatest influence on aggregation presence. Whilst examining data, a number of predictor variables exhibited collinearity (Variance Inflation Factors ≤5.0 or Pearsons Correlation r ≥ 0.7). Variables with the strongest covariate relationship were removed from the dataset, strongest first, in an iterative stepwise process, whilst retaining the variables with the strongest univariate relationship with the response variable. To minimise this intercorrelation and prevent masking of trends whilst modelling, data were split into four sub-sets based on the stepwise reduction (Zuur, Ieno & Elphick, 2010; Tamura et al., 2017). These four sub-sets were modelled separately to keep variables with strong covariate relationships apart (see Table 2 for the list of variables in each GLM). The four model outputs showed no overdispersion so minimum adequate models were created using backward-forward stepwise reduction based on the Akaike Information Criterion (AIC) (Hilbe, 1994; Dobson & Barnett, 2008). Analysis of deviance was used to test whether the deviance explained had not reduced from the full models, therefore justifying the use of stepwise reduction (McCulloch, 2000).
|Mean point depth||Site depth|
|Mean buffer zone depth||Buffer depth|
|Maximum buffer zone depth||Buffer max|
|Buffer zone depth range||Buffer range|
|Mean point slope||Site slope|
|Mean buffer zone slope||Buffer slope|
|Maximum buffer zone slope||Max slope|
|Curvature at point||Site curvature|
|Mean curvature in buffer zone||Mean curvature|
|Maximum curvature in buffer zone||Concavity|
|Minimum curvature in buffer zone||Convexity|
|Proximity to 200 m isobath||200 m|
|Proximity to 1,000 m isobath||1,000 m|
|Mean Chlorophyll-a concentration||Chlorophyll|
Many of the bathymetric variables studied showed distinct differences between the aggregation and non-aggregation sites. All depth measures were significantly shallower in areas R. typus aggregate (Table 3), with the biggest difference shown to be between mean depth at the aggregation sites, 22.2 m, an order of magnitude lower than non-aggregation sites (635.3 m); this difference was highly significant (t = 19.262, df = 1006.7, p < 0.001). Similarly, the mean depth in 20 km buffer zones was shown to be significantly shallower than mean depth in non-aggregation sites (t = 9.578, df = 25.601, p < 0.001). Maximum depth and range of depths within the 20 km buffer zones were around 50% lower at aggregation sites, further highlighting aggregations occur in shallower areas. Benthic complexity was significantly lower at aggregation sites than that at non-aggregation sites (Table 3), meaning a smoother, less rugged surface.
|Variable||Aggregation site mean||Non-aggregation site mean||t-test statistics|
|Site depth (m)||22.2||635.3||t = 19.262, df = 1006.7, p < 0.001|
|Buffer depth (m)||173.0||713.6||t = 9.578, df = 25.601, p < 0.001|
|Buffer max (m)||716.6||1,350.8||t = 3.086, df = 14.441, p = 0.008807|
|Buffer range (m)||712.4||1,295.3||t = 2.836, df = 14.319, p = 0.013|
|Complexity||180.3||336.5||t = 2.571, df = 14.121, p = 0.022|
|Site slope (degrees)||0.67780||0.00003||t = 2.931, df = 13, p = 0.012|
|Buffer slope (degrees)||1.41||2.55||t = 2.951, df = 14.46, p = 0.011|
|Max slope (degrees)||8.95||10.31||t = 0.624, df = 13.616, p = 0.543|
|Roughness||0.00744||1.96266||t = 30.083, df = 994, p < 0.001|
|Site curvature||0.000002||0.000011||t = 1.274, df = 21.855, p = 0.216|
|Mean curvature||0.000005||0.000003||t = 1.386, df = 13.177, p = 0.189|
|Concavity||0.000613||0.000584||t = 0.181, df = 13.549, p = 0.859|
|Convexity||−0.000648||−0.000594||t = 0.312, df = 13.444, p = 0.759|
|200 m (km)||0.170||71.781||t = 14.477, df = 994.2, p < 0.001|
|1,000 m (km)||0.416||99.385||t = 17.694, df = 994.32, p < 0.001|
|Aspect||190.498||172.826||t = 0.73397, df = 13.518, p = 0.475|
|Chlorophyll (mg/m3)||0.669||1.532||t = 6.397, df = 35.86, p < 0.001|
|SST (°C)||30.4||29.8||t = 2.173, df = 18.129, p = 0.063|
The mean slope at aggregation sites was significantly steeper than that at non-aggregation sites, however the inverse was displayed with mean slope in the buffer zones (Table 3). T-tests showed no significant differences between the means of maximum slope in buffer zones, with a difference of only 1.4 degrees between aggregation and non-aggregation sites. However, the absolute maximum slope recorded was steeper; 29.8 degrees at aggregation sites and 60.1 degrees at non-aggregation sites. Aggregation sites had a lower slope roughness by three orders of magnitude compared to non-aggregation sites, and the t-tests showed these differences were highly significant. The curvature at and around both aggregation and non-aggregation sites was slightly concave with no real differences (Table 3). The buffer zones around aggregation sites showed greater concavity than areas around non-aggregation sites and the result is the same when looking at the slight convexity displayed at both sites. With such small variation in all mean values, there were no significant differences between curvature at aggregation and non-aggregation sites.
Aggregation sites were two orders of magnitude closer to the 200 m isobaths with a mean distance of 0.14 km, whereas the mean distance for non-aggregation sites was 71.78 km. Similar results are shown in the distance to the 1,000 m isobaths; aggregation sites had a mean distance of 0.41 km compared to non-aggregation sites which had a mean distance of 99.38. The observed differences in distance to both the 200 m and 1,000 m isobaths were highly significant (Table 3). The mean slope aspect was south for both aggregation and non-aggregation sites; the majority of individual slope aspects were either southeast, south or southwest, with very few facing north. There were differences in chlorophyll-a concentration and SST between aggregation and non-aggregation sites. Surprisingly, chlorophyll-a was significantly lower at aggregation sites with a mean concentration of 0.67 mg/m3, compared to 1.53 mg/m3 at non-aggregation sites (t = 6.397, df = 35.86, p < 0.001). SST showed no significant difference between aggregation sites, and non-aggregation sites.
Main drivers of aggregations
The six predictor variables left in the four minimum adequate models were significant (p < 0.05) and three of the models (Table 4) had high percentage of deviance explained (>85%) for aggregation site presence. Aggregation site presence was best modelled by GLM3, with the mean depth in the buffer zone (buffer depth) explaining 88.71% of deviance. GLM1 containing mean depth at points (site depth) and proximity to the 200 m isobaths explained 87.96% of deviance of aggregation sites. Site slope and proximity to 1,000 m, which were left in GLM2 after stepwise reduction, explained 88.16% of aggregation site deviance. These three GLMs all explain high deviation with significance, therefore indicating commonality in bathymetric features at aggregation sites and differences to those found at non-aggregation sites. Diagnostic plots were checked for outliers and showed the residuals were close to the line and Cook’s Distance values below 0.5 for all points, suggesting no single point had an overpowering or unnecessary influence on the overall trend of aggregation site presence. P[D] values (probability of decreased deviance explained from the full model) for all models were high, suggesting the minimum adequate models used explain no less deviance than the full GLMs and the stepwise reduction of variables was justified.
|Model Name||Predictor variables tested||Minimum adequate model|
|GLM1||Site depth, 200 m, Site curvature, Complexity||Site depth:%D = 0.7748, p[t] = 0.0143, 200 m:%D = 0.7496, p[t] = 0.0379, (AIC = 23.2, %D = 0.8796, p[D] = 0.683)|
|GLM2||Site slope, Depth range, 1,000 m, Mean curvature, Max slope||Site gradient:%D = 0.6571, p[t] = 0.0021, 1,000 m:%D = 0.4885, p[t] = 0.0157, (AIC = 27.3, %D = 0.8816, p[D] = 0.784)|
|GLM3||Buffer depth, Roughness, SST, Convexity, Concavity||Buffer depth:%D = 0.8871, p[t] = 0.029, (AIC = 19.4, %D = 0.8871, p[D] = 0.793|
|GLM4||Buffer slope, Buffer max, Aspect, Chlorophyll||Buffer max:%D = 0.4631, p[t] = 0.0011, (AIC = 67.006, %D = 0.4631, p[D] = 0.538)|
Our analysis shows bathymetry to be significantly different at and around coastal areas where R. typus aggregate compared to coastal areas where aggregations do not occur. Aggregation sites were significantly shallower over both spatial scales (point data and the 20 km buffer zone). Despite the area surrounding aggregation sites being roughly 500 m shallower than that measured at non-aggregation sites, the mean distance of aggregation sites to both the mesopelagic and bathypelagic zones was significantly closer by two orders of magnitude than non-aggregation sites. Steeper slopes were found at the aggregation sites, but not in the surrounding buffer zones. These results suggest three aspects of bathymetry are important to aggregation formation; shallow areas at aggregation sites, proximity to deep water and steep slopes. These bathymetric characteristics were found to be important in a number of local and regional studies of R. typus distribution (McKinney et al., 2012; Sequeira et al., 2012; Afonso, McGinty & Machete, 2014).
Site depth and buffer zone depth were among the biggest drivers of aggregations. Literature extensively illustrates R. typus aggregating in shallow water for two main reasons. Firstly, primarily to feed, hence chlorophyll-a concentration being included in this study as an indicator of planktonic productivity (Platt & Herman, 1983; Sequeira et al., 2012). However, non-aggregation sites had a mean chlorophyll-a concentration twice as high as that at aggregation sites. The mean chlorophyll-a concentration at aggregation sites of 0.67 mg/m3 can be considered relatively high compared to pelagic areas where typically chlorophyll-a concentration is <0.25 mg/m3 (Hu, Lee & Franz, 2012), nevertheless it was significantly lower than other coastal areas within R. typus’ range. One reason for this can be attributed to the diversity of R. typus’ prey; a number of studies have shown aggregations coincide with spawning events such as Scombridae spp. spawn at the Yucatan peninsula (De la Parra Venegas et al., 2011) or Lutjanidae spp. spawn in Belize (Heyman et al., 2001). However, Donati et al. (2016) describe the aggregation at South Ari atoll as a yearlong phenomenon with no seasonal peak and there is a current lack of understanding as to the main cause of this aggregation if it is not seasonally prey driven. Nonetheless, these whale sharks will feed on plankton and various spawn in the shallow coastal waters where they are regularly observed (Hoffmayer et al., 2007; Motta et al., 2010).
The second main reason suggested for aggregations in shallow waters is for thermoregulation after deep dives into cooler water. Research into this field is limited (Brunnschweiler et al., 2009; Thums et al., 2013; Tyminski et al., 2015), however this is a viable theory and the results of this study illustrate aggregations occurred in warmer waters than the random non-aggregation sites selected. Although SST was only higher by ∼0.5 °C, this was at a coarse resolution, larger than the aggregation areas, therefore SSTs on site may in fact be higher. Furthermore, the temporal averaging of SSTs may have influenced the extent of difference between sites (this was done to ensure consistency and avoid anomalous data produced by El Niño years). A number of ectothermic species require surface intervals to raise body temperature to levels needed to regulate physiological processes after time spent foraging in cooler, deep waters (Thums et al., 2013). The size of R. typus’ gills make them extremely efficient at filtering prey from the water, but the large volume of water passing over the gills causes R. typus to cool relatively quickly when in deeper water (Colman, 1997). If thermoregulation occurs in warm shallow areas with high productivity, or an abundance of prey, R. typus could continue to feed whilst increasing body temperature from deep dives.
The proximity of R. typus aggregations to deep water is therefore thought to be due to frequent deep dives for prey (Graham, Roberts & Smart, 2006; Tyminski et al., 2015), whilst remaining close to shallow areas of high productivity for thermoregulation (Thums et al., 2013) and potential feeding. All aggregation sites in this study were significantly closer to areas with water in the mesopelagic and bathypelagic zones. The deep water bathymetric variables (site depth, buffer depth and proximity to the 200 m and 1,000 m isobaths) explained the greatest deviance of R. typus aggregation site presence, showing these aspects may be highly important for separating aggregation from non-aggregation sites. Sequeira et al. (2012) found similar results when modelling R. typus habitat suitability in the Indian Ocean; depth and distance to the continental shelf were two of the biggest indicators of habitat preference.
A number of studies with tagged whale sharks show their deep diving behaviour; Rowat & Gore (2007) recorded three R. typus individuals spent ∼30% of their time at depths of 750–1,000 m. A recent study by Tyminski et al. (2015) showed one individual diving as deep as 1,928 m in temperatures 4.2 °C, similarly reflected by Brunnschweiler et al. (2009) in which two tagged whale sharks were recorded at depths of 1,286 m in temperatures of 3.4 °C. Graham, Roberts & Smart (2006) carried out a similar study, further illustrating deep diving behaviour and also recording available prey at these depths. It has been suggested R. typus feeds on zooplankton (euphausiids and myctophids), squid and jellyfish in these deep waters seaward of the shelf breaks (Graham, Roberts & Smart, 2006; Wilson et al., 2006). Although chlorophyll-a concentration was lower at aggregation sites, the satellite sensors cannot penetrate deeper than 60 m (Mélin & Hoepffner, 2011), causing deep-water areas with high productivity, such as around slopes and shelfs, to be missed. These areas have been shown to be highly important to R. typus for feeding in a number of studies (Graham, Roberts & Smart, 2006), and more recently Sequeira et al. (2012) and McKinney et al. (2012) showed areas with these bathymetric characteristics are the most associated with R. typus sightings.
Similarly, the basking shark (Cetorhinus maximus) and megamouth shark (Megachasma pelagios) have also been recorded diving into the mesopelagic and bathypelagic zones in search of prey (Nelson et al., 1997; Sims et al., 2003; Gore et al., 2008). Wilson et al. (2006) hypothesise the deep diving behaviour in all three species is to locate the deep scattering layer and associated prey at dusk and dawn. This idea was further supported by Gore et al. (2008) who suggested regular dives of increasing depths is indicative of systematic foraging, supporting the theory that deep dives occur to locate horizontally dispersed prey. However, despite research into deep diving of these shark species, the function of deep dives for R. typus remains poorly understood.
In this study, R. typus aggregations occurred in relatively flat areas with a mean slope of 0.68 degrees, however, this was significantly steeper than non-aggregation sites. Steepness of slopes increased further from aggregation sites with a mean of 1.4 degrees and absolute maximum of 29.84 degrees in the 20 km buffer zone. Aggregations typically occur in the fore reef and lagoon areas, leading out to the reef slope, reef wall or continental slope, which has a steeper slope and deeper water.
Areas with steep slopes are known to induce upwelling events (Botsford et al., 2003; Zavala-Hidalgo et al., 2006), particularly coastal areas where depth changes rapidly, forcing offshore deep-water currents to deflect against the steep slopes, bringing nutrient rich water to the surface (Jacox & Edwards, 2011; Connolly, 2013). These areas have biological significance, and often associated with enhanced primary productivity, therefore increasing plankton abundance and attracting a number of species throughout the trophic levels (Botsford et al., 2003; Jacox & Edwards, 2011).
Wolanski & Hamner (1988) carried out one of the first studies on the biological impacts of steep bathymetry, suggesting these areas are of great significance to large marine species due to availability of prey. Sims (2008) confirmed this with Cetorhinus maximus, as steep slopes were shown to be their most common foraging habitat, where the highest zooplankton densities were observed. McKinney et al. (2012) modelled the feeding habitat of R. typus aggregations in the Gulf of Mexico using bathymetry, showing areas close to the continental shelf are often selected as aggregation sites due to their productivity. The model of McKinney et al. (2012) suggested proximity to a continental shelf is one of the biggest influences on aggregation site location. Subsequent research by Afonso, McGinty & Machete (2014) show increased R. typus abundance in areas with steep bathymetric slope and in areas associated with increased prey abundance.
Because R. typus aggregate in only a handful coastal areas and aggregation events are highly predictable, these sites should be focal points for conservation efforts to protect this species through a number of means such as MPA creation, fishing restrictions, boat speed limits and limited visitor numbers. By showing that these aggregations occur in areas with specific bathymetry, there is the possibility to use species distribution models or habitat models to predict other suitable areas where aggregations may already occur or areas aggregations may shift to with projected anthropogenic climate change. The aggregations investigated in this study represent only one of a number of habitats used in R. typus’ life cycle, with these aggregations shown to be used predominantly by juvenile males (Heyman et al., 2001; Riley et al., 2010). There may be other types of aggregation occurring in offshore waters, but there is currently little research being undertaken due to the high economic and time requirements for such research.
Aggregations increase vulnerability to capture, boat strikes and overexploitation (Lewison et al., 2004), particularly during crucial periods in their lives, such as feeding events and breeding, and when sharks may be recovering from deep dives. Whilst there is no evidence R. typus aggregations are for breeding, there is lack of information regarding the breeding behaviour of this species. Therefore, it is plausible aggregations could also be used for mating, which has been observed in zebra sharks (Stegostoma fasciatum) (Dudgeon, Noad & Lanyon, 2008) and is suspected to occur at Cetorhinus maximus aggregations (Wilson, 2004). This study and a handful of others (McKinney et al., 2012; Sequeira et al., 2012; Afonso, McGinty & Machete, 2014) have shown there are defined bathymetric characteristics in R. typus aggregations. As certain characteristics and features of bathymetry are of great importance to a number of marine megafauna species, more research should be carried out in this field with conservation efforts focusing on areas where species are at their most abundant, but also at their most vulnerable.
This study shows clear evidence that there are significant differences in bathymetry between the coastal areas where R. typus aggregate compared to areas where R. typus aggregations do not occur. Aggregations occur in shallow areas in close proximity to a reef slope or shelf break with a steep slope, which leads into water in the mesopelagic and bathypelagic zones. The bathymetric characteristics at and around aggregation sites are all associated with increased productivity and prey availability, which are the main reasons R. typus and a number of other species aggregate. Knowing this, future conservation efforts for marine megafauna could look for areas with these key bathymetric characteristics, which have been shown to be present in areas of aggregations for a number of species. This study is the latest addition to that research; we have shown that key bathymetric characteristics are a feature of areas in which whale sharks aggregate.