Large-bodied, coral reef roving predators (e.g. sharks, jacks, and snappers) are generally believed to be depleted across much of their ranges, particularly close to human population centers1,2,3,4,5,6,7. Similarly, reduced numbers of sharks and large-bodied teleosts reflect comparable patterns in the heavily populated main Hawaiian Islands (MHI), with reef shark abundances estimated at 3–10% of natural baseline levels7 and populations of several jacks (e.g. Caranx ignobilis and Caranx melampygus) thought to be depleted as a result of fishing pressure over the past several decades8,9,10,11. This serves as a stark contrast to abundant roving predator groups found in the remote, difficult to access, and largely unpopulated (i.e. relatively lightly fished) Northwestern Hawaiian Islands (NWHI)1, 12.

The primary source of Hawaiian Archipelago large-bodied, shark, jack, and snapper abundance data comes from underwater visual censuses on open-circuit scuba in 30 meters or less1, 12, 13. However, these groups are also known to inhabit considerably deeper ‘mesophotic’ strata of 30–150 m or more, where information on predator movements and habitat use remains scarce14,15,16. For example, tiger sharks (Galeocerdo cuvier) and Galapagos sharks (Carcharhinus galapagensis) have been documented to depths greater than 200 m17,18,19,20,21, while whitetip reef sharks (Triaenodon obesus) have been recorded down to 330 m22. Other predators commonly observed during shallow water dive surveys in the NWHI, including the giant trevally (Caranx ignobilis) and the bluefin trevally (Caranx melampygus), have been found in waters to at least 188 m and 230 m respectively9, 23, 24. Mesophotic coral reefs (herein denoted as ‘MCEs’) and other mesophotic ecosystems ≥30 m may be partially shielded from environmental and anthropogenic influences impacting shallow water coral reefs between 0–30 m, and may serve as population reservoirs for predator species targeted by fishers in shallower depths15, 16, 25, 26. However, while mesophotic predator research has increased over the past two decades through the use of advanced sampling technologies, e.g. closed-circuit rebreather underwater visual surveys or acoustic/satellite tracking, predator assessments in Pacific mesophotic ecosystems remain largely unassessed in comparison with their shallower counterparts15, 27,28,29.

Given the documented evidence for higher roving predator abundance and/or biomass estimates in deeper waters around high-density human populations25, sparsely populated or remote areas16, 30, and the noted rarity or absence of several reef-associated shark species (e.g. sandbar sharks, Carcharhinus plumbeus and Galeocerdo cuvier) during diver surveys31, it’s feasible that open-circuit underwater visual censuses may be missing the bulk of their populations if surveys remain constrained to depths less than 30 m. Therefore, there is a clear need to extend research into deeper coral reef habitats in order to better understand patterns in distributions of roving predator in the Hawaiian Archipelago and elsewhere.

Baited remote underwater stereo-video systems (stereo-BRUVs; herein denoted as ‘BRUVS’) represent one alternative sampling tool to assess the relative abundance and size frequencies of roving predator populations. BRUVS can be deployed over a wide range of habitats and depth strata32, and can be used to generate highly accurate and precise length and abundance data for sharks, jacks, and other roving predators which are comparable to other survey methods33,34,35,36,37,38.

Here, we present results of roving predator BRUVS surveys across the Hawaiian Archipelago covering depths down to 100 m. Research objectives included the: (a) comparison of relative abundances and length-based distributions of major species contributing to roving predator assemblages across shallow and mesophotic depth strata in the MHI and NWHI; and (b) investigation of mesophotic habitats, which remain largely inaccessible to underwater visual censuses on open-circuit scuba, as possible ‘depth refugia’ (defined as areas protected from shallow water disturbances that may serve as potential reproductive population reservoirs) for MHI roving predator species considered rare in 0–30 m depths26, 39.


Ethics statement: Stereo-video sampling of reef fishes

This project was conducted under the Papahānaumokuākea Marine National Monument Research Permit no. PMNM-2013-018-M1, and meets the requirements of NOAA Administrative Order (NAO) Series 216-6, Environmental Review Procedures, Sections 5.05 and 6.03c.3 (a) for Categorical Exclusions (CE) for Research Programs (PIFSC-20120038) for survey activities in the Main and Northwestern Hawaiian Islands. Additional research clearance was granted by the National Environmental Policy Act (NEPA), Programmatic Environmental Assessment for Research Activities Conducted by the Coral Reef Ecosystems Program (CREP), Pacific Islands Fisheries Science Center (PIFSC), 2010–2015. Stereo-camera deployments conducted from 2012–2014 were completed under the University of Western Australia (UWA) animal ethics permit no. RA/3/100/1204 and the Curtin University animal ethics permit AEC-2014-09, in adherence to provisions contained within the Australian Code of Practice for the Care and Use of Animals for Scientific Purposes. All experimental stereo-video sampling protocols were approved in accordance with NOAA PIFSC CREP, UWA, and Curtin University research guidelines, permitting agencies, and/or animal ethics review committees as described above.

Study Area

The Hawaiian Archipelago (Hawaii, USA), consisting of 18 islands and atolls stretching across a 2400 km SE-NW gradient, is one of the most isolated archipelagos in the world. The archipelago includes the Main Hawaiian Islands (MHI), which are geologically-young, high-islands subjected to heavy population and fishing pressures1, and the older, largely unpopulated NWHI composed primarily of sandy islets, atoll systems, and submerged shoals. In 2005, the State of Hawaii established the NWHI Marine Refuge, which closed all NWHI state waters to fishing. Protection was further enhanced by the establishment and subsequent expansion of the Papahānaumokuākea Marine National Monument (PMNM) in 2007 and 2016 respectively. Because of their management status and their remoteness, access is almost entirely limited to research and management groups and traditional Native Hawaiian practitioners.

Survey Operations and Site Selection

Four of the MHI (Oahu, Maui, Molokai, Lanai) were sampled during two NOAA research expeditions in September and October 2012, with additional Oahu shore-based small boat sampling efforts completed in November 2013. Subsequent deployments in the NWHI (French Frigate Shoals, Lisianski, Pearl and Hermes Reef, Midway Atoll) were conducted during two NOAA research expeditions in May and September 2014 (Fig. 1). During each sampling effort, sites were selected in ‘mesophotic’ (30–100 m) and ‘shallow water’ (0–30 m) forereef and fringing reef habitats. Shallow water sites were randomly selected from locations previously surveyed by SCUBA divers conducting routine monitoring operations for reef fish and roving predators40, 41, with there being at least an hour between the completion of diver surveys and deployment of baited camera stations. Mesophotic survey sites were randomly selected from a pool of 500 × 500 m grid cells generated from bathymetric and backscatter data products produced by the University of Hawaii, School of Earth and Ocean Sciences (SOEST), Hawaii Mapping Research Group (Main Hawaiian Islands Multibeam Bathymetry and Backscatter Synthesis, Grid cells were constrained within a 100 m contour line using data derivatives from SOEST HMRG 50 m bathymetry and topography grid cells, and stratified into three predetermined, near “equally spaced” depth bins (30–53 m, 53–76 m, 76–100 m). Because the primary goal was to compare among hard-bottom habitats, grid cells containing backscatter values with >35% unconsolidated sediment (sand; obtained from SOEST HMRG 60 m backscatter grid cells) were excluded from the site pool. However, at some locations (esp. the MHI), bottom type information was not available or was inaccurate, leading to sampling of unconsolidated sediment (sand flats).

Figure 1
figure 1

(A) Map indicating BRUVS sampling locations across the Hawaiian Archipelago. Map generated in ArcGIS, 10.3 ( by Tomoko Acoba (NOAA PIFSC CREP). (B) Proportional relative abundance (% of total MaxN, hr−1) of total predator assemblages in the MHI and (C) NWHI. *Indicates numerical abundance of Seriola dumerili, Seriola rivoliana, and Seriola sp. (excluding Seriola lalandi) pooled. Staggered bar plots generated in MS Excel 2010 ( Maps in the figure were generated using Adobe Illustrator CS5 (

All BRUVS surveys were completed between 0800–1600, with soak times of 60 minutes, and all sampling sites separated by at least 500 meters.

Stereo-video collection and data processing

The BRUVS used in this study followed the design of Harvey et al.42,43,44, and were constructed from a pair of high definition Sony handheld video cameras with a wide-angle lens adaptor, held in waterproof housing and mounted on a base bar 0.7 m apart, inwardly converged at 8°. Prior to and following each research mission, each BRUVS was calibrated using CALTM software according to protocols described elsewhere43,44,45,46. The oily fish Japanese sanma (Cololabis saira) was used as bait, which was pulped and loaded into 800 g wire-mesh baskets attached 1.2 m from the stereo-cameras prior to deployments.

Upon completion of BRUVS deployments, all video footage was converted from MT2S to AVI format using the program XilisoftTM, followed by the annotation of stereo-video imagery with EventMeasure-StereoTM videographic software45. Species were identified to their lowest possible taxonomic level, with relative abundance recorded as MaxN measures. MaxN, defined as “the maximum number of fish belonging to each species present in the field of view of the cameras at one time”47,48,49,50,51,52 is a conservative abundance measure that avoids repeated counts of the same targets. Length-based measurements were derived by making nose-to-tail fork length measurements (FL) in EventMeasure at the time of MaxN. To ensure the accuracy and precision of measurements, and for consistency with established BRUVS protocols, MaxN and length measurements were limited to targets within 7 m of the stereo-cameras53. All MaxN and fork-length data were compiled and cataloged according to the National Fisheries Information System (FIS) Information Portal practices54.

Deployments were excluded from analysis when the field of view was ≥ 30% obstructed – i.e. if BRUVS had flipped and were facing straight down or straight up, if they were blocked by upright substrate, or when visibility dropped below 7 m, which occurred for a number of MHI sites in <6 m depth. A subtotal of 107 baited sites in the MHI and 78 sites in the NWHI were sampled (185 pooled deployments; Fig. 1, top panel). Outputs from efforts by region and depth strata are listed in Table 1.

Table 1 Summary of sampling effort in the Hawaiian Archipelago, detailing the number of sites per region, depth strata, and habitat type.

Target groups

Analysis of BRUVS surveys was focused on high-level roving predators, with selections based on assignments as described in Friedlander and DeMartini1, Holzwarth et al.13, Parrish et al.30, and Williams et al.12. These included all shark species, large-bodied non-planktivorous jack species (Carangidae), the great barracuda (Sphyraena barracuda), and the green jobfish (Aprion virescens).

Environmental variables

Depth data was obtained from UWATEC dive gauges attached to the stereo-camera base bar. Habitat type was visually classified based on video footage into one of 9 categories: aggregate reef, spur and groove, pavement, rock/boulder, reef rubble, aggregate patch reef, sand with scattered coral/rock, or sand flat (100% unconsolidated sediment)24. Habitat complexity was visually estimated on a five-point scale: 1 = flat, no vertical relief; 2 = low and sparse relief; 3 = low but widespread relief; 4 = moderately complex; and 5 = very complex with numerous fissures and caves55. Finally, percent cover of hard coral, soft coral, macroalgae, turf algae, crustose coralline algae, and sand was visually-estimated from video imagery using the NOAA PIFSC CREP fish team benthic classification protocol56.

Data Analysis

Experimental Design

Roving predator abundance and fork length-based measurements were examined according to two a priori factors: Region (MHI and NWHI: two levels, fixed) and Depth strata (shallow water (0–30 m); upper mesophotic (30–53 m); lower mesophotic (53–100 m); three levels, fixed). The decision to combine 53–76 m and 76–100 m abundance estimates post-hoc into a single level (lower mesophotic) came as a result of the reduced number of MHI hard-bottom mesophotic sites encountered below 53 m, with upper/lower mesophotic depth stratification aligning with coral reef fish assemblage structures observed in the MHI (Asher, unpublished data) and reported elsewhere39, 57. A third post-hoc, two-level fixed factor was added (Habitat; hard-bottom, unconsolidated sediment), as coral reef roving predators were commonly sighted in both substrate types which precluded the exclusion of BRUVS surveys that sampled sand flats. Finally, length data was pooled into two comparative depth strata (0–30 m; 30–100 m) because of small sample sizes.

Statistical analyses

Multivariate roving predator assemblage analysis was conducted on a zero-adjusted Bray-Curtis (B-C)58 dissimilarity matrix using square root transformed relative abundance data using PRIMER v7.0.11 with the PERMANOVA+ add on software59, 60. Segregated regional and depth-inferred differences between roving predator population aggregates were first obtained through the bootstrapping function61, 62, and visualized as a metric multidimensional scaling (mMDS)63 ordination with bootstrap regions set to 95% confidence intervals (plotted as ellipses), a Kruskal stress formula set to 1, and minimum stress assigned to 0.01. A successive Hierarchical Cluster Analysis64 was calculated from distanced-dissimilarities between group centroids (region x depth x habitat) in order to visualize potential effect sizes and their interactions, with the original dissimilarities (distances between individual centroids) compared against cophenetic dissimilarity (distance between centroid clusters). Akin to a suitability index, a cophenetic correlation of r > 0.8 can be interpreted as a strong representation of the original centroid dataset65.

Changes to MHI and NWHI roving predator assemblages were evaluated along the continuous depth gradient within each respective region using a canonical analysis of principal coordinates (CAP). Subsequent CAPs were used to examine the efficacy of a priori MHI and NWHI depth group assignments through “leave-one-out” cross validation and allocation of observations to groups66, 67. Finally, Person’s rank correlations of individual species recording >0.35 were superimposed (as vectors) with the resultant CAP axes within each respective region as additional exploratory measures59.

Variation in assemblage structure between regions, depth strata, and habitat types were further tested using a Permutational Multivariate Analysis of Variance (PERMANOVA) as this is a robust test for examining correlations within potential heterogeneous variances68. A random, mixed three-way design PERMANOVA with 9999 permutations, constructed using Type III sum of squares (SS) was carried out. If factor effects or their interactions were significant, additional PERMANOVA pair-wise comparisons were conducted to investigate levels of significance within and between factor levels, with Monte Carlo p-values used for cases with fewer than 30 unique permutations59. Because PERMANOVA can remain sensitive to differences in multivariate dispersions, tests for dispersion homogeneity within groups (permutation of dispersions, PERMDISP), with 9999 permutations, were conducted in concert with PERMANOVA to further assess the variability of sampling regions against different depth and habitat strata.

A shade plot/heat map69 was constructed to further delineate abundance distributions of individual species across regions and depth strata, with sites ordered along the x-axis according to region and increasing depth. The y-axis was constructed according to roving predator groups, which were first standardized, transformed into a distance-based resemblance matrix using Whittaker’s Index of Association, and plotted via Hierarchical Cluster analysis64 using group average clustering and a Type III similarity profile (SIMPROF) analysis70 with 9999 permutations. A Similarity Percentages, Species Contributions (SIMPER) test71, 72 was then used to identify the predominant species similarities/dissimilarities within and between regional and depth strata factors, along with the percentage of species which explained similarities/dissimilarities.

For species that provided significant contributions to those identified in the SIMPER tests, additional univariate PERMDISP and PERMANOVAs using Euclidean distance measures were conducted on square root transformed relative abundance data. For univariate non-parametric analyses of Seriola species, Seriola dumerili and Seriola rivoliana abundance totals were pooled together (pooling herein denoted as “Seriola sp ”) along with individuals marked “Seriola sp” that couldn’t be differentiated between the two. Seriola rivoliana, which had distinctly different characteristics than other members of the Seriola genus, were rarely encountered and were excluded from pooling.

Finally, changes to the relative abundance of individual species identified in SIMPER were modeled along continuous depth gradients using R statistical software (version 3.3.0) following the approach used by Fukunaga et al.73, generating non-parametric quantile regression splines through the rq () function in the quantreg package74, 75.

Length-based estimates

Differences in length distributions for those species identified in SIMPER output were compared between respective regions (MHI, NWHI) and depth strata (shallow [0–30 m], mesophotic [pooled 30–100 m strata]) using untransformed raw length data (no zeros) across model factors and the non-parametric Kolmogorov-Smirnov test76, with data pooled from all mesophotic depths due to insufficient target species length measurements in upper or mesophotic strata alone. Average fork-length estimates (mm) were obtained for several species, including Aprion virescens, Caranx melampygus, Caranx ignobilis, Carcharhinus galapagensis, and Triaenodon obesus. All other species were measured, but excluded from analysis due to insufficient fork-length sampling pools.

Habitat Characterization

Environmental relationships between regions and depth strata were visualized through bootstrapping from the original sampling pool. Bootstraps were plotted as a metric multidimensional scaling (mMDS) ordination, with bootstrap regions set to 95% confidence interval ellipses, a Kruskal stress formula set to 1, and minimum stress assigned to 0.01. In order to further gauge the ecological relationships between shallow water and upper and lower mesophotic zones, a Principal Component Analysis (PCA)77, 78 was performed on normalized environmental variables separately for the MHI and NWHI.

Finally, linkages between normalized, Euclidean-distance based environmental matrices and roving predator assemblage (abundance) matrices in the MHI and NWHI were explored using distance-based linear modeling (DISTLM) in PERMANOVA+59, 79, with the most parsimonious model constructed using modified Akaike’s Information Criterion (AICc) and BEST procedures. DISTLM allows for the testing of variation within predator assemblages to be explained through multiple environmental predictor variables, generating the most parsimonious models from the lowest AIC values. Distance-based redundancy analyses (dbRDA) were then used to construct constrained ordinations from BEST fitted values from the MHI and NWHI, using linear combinations of environmental variables which best explained the variation within roving predator assemblages belonging to each respective region59.


Roving Predator Assemblage Description

A total of 198 individual roving predators were recorded over 107 BRUVS samples in the MHI (mean and SE: 1.85 ± 0.27), while 425 roving predators were recorded over 78 BRUVS sites in the NWHI (5.45 ± 0.84, Table 2). The snapper Aprion virescens was the most common roving predator species overall, comprising a large proportion of the pooled roving predator community in each region (22% MHI, 19% NWHI; Fig. 1, lower panel). However, as a collective group, Carangidae comprised 65% of all roving predators belonging to ten species in the MHI (1.22 ± 0.19 SE, Table 2), with Caranx melampygus dominating shallow water abundances (51%, Fig. 2A) and Carangoides orthogrammus remaining prevalent in mesophotic depths (27%, Fig. 2B). Similarly, eight species of Carangidae accounted for 61% of all observations in the NWHI (3.33 ± 0.70 SE), with Caranx ignobilis dominating shallow waters (40%, Fig. 2C), and Seriola sp comprising the major group (28%) in mesophotic habitats (Fig. 2D). Finally, sharks formed 12% and 20% of MHI and NWHI roving predator abundances respectively (Table 2, Fig. 2). In total, 22 sharks belonging to 4 species were recorded in the MHI (0.21 ± 0.05 SE), with sandbar sharks (Carcharhinus plumbeus) encompassing the majority of all shark sightings (59%) and another 23% of sightings belonging to tiger sharks (Galeocerdo cuvier). In contrast, 85 sharks belonging to 5 species were recorded in the NWHI (1.09 ± 0.14 SE), with Galapagos (Carcharhinus galapagensis; 56%) and whitetip reef sharks (Triaenodon obesus; 30%) comprising the majority of encounters. Neither species were sampled by BRUVS in the MHI.

Table 2 Average abundance (mean MaxN), standard error (SE), and NWHI:MHI abundance ratios for roving predator species sampled in the Hawaiian Archipelago.
Figure 2
figure 2

(A) Shallow and (B) Mesophotic pproportional relative abundance (% of total MaxN, hr−1) of predator assemblages in the MHI. (C) Shallow and (B) Mesophotic pproportional relative abundance of predator assemblages in the NWHI. Staggered bar plots generated in MS Excel 2010 ( Maps in the figure were generated using Adobe Illustrator CS5 (

Roving predator assemblages differed between regions and depth strata (Global PERMANOVA, both p = 0.0001, Table 3). The relationship between roving predator assemblage structures and continuous depth gradients among the 107 surveys in the MHI (δ² = 0.35, m = 4 principal coordinate axes, Supplementary Materials, Figure S1A) and 78 surveys in the NWHI (δ² = 0.55, m = 3 principal coordinate axes, Figure S1B) confirmed a high degree of community overlaps between depths, particularly between 0–30 and 30–53 m (Fig. 3A, Supplementary Materials, Table S2). When examining the efficacy and cross validation of depth-zone assignments within the MHI and NWHI, 63% and 97% of assignments in the lower mesophotic zone were correctly made in the MHI and NWHI respectively, with misclassification errors largely driven by assignment switches (i.e. assemblage overlaps) between shallow water and upper mesophotic groups (Supplementary Table S1, Figure S1C,D), with MHI patterns being particularly susceptible to leave-one-out allocation errors due to the greater number of zero sightings or singleton predator observations during BRUVS surveys.

Table 3 PERMANOVA tests of pooled roving predator abundance (all species), Aprion virescens, Caranx melampygus, and Carangoides orthogrammus between region (Re), depth (De), and habitat strata (Ha).
Figure 3
figure 3

(A) Bootstrap resampling plot, 50 bootstraps per group. Square root transformed, zero-adjusted Bray Curtis roving predator abundance data (MaxN, hr−1) by Region (MHI, NWHI) x Depth Strata (SPC; upper and lower mesophotic), plotted metric multi-dimensional scaling (mMDS). Shaded bootstrap regions, which represent measurements of centroid error: 95% confidence ellipses, averages based on m = 10 dimensional metric MDS (rho = 0.985). Open symbols represent MHI sites, closed symbols represent NWHI sites. Light grey = shallow water (0–30 m), medium grey = upper mesophotic (30–53 m), dark grey = lower mesophotic (53–100 m). (B) Hierarchical cluster analysis dendrogram of group centroids f by Region (MHI, NWHI), Depth (0–30 m, 30–53 m, 53–100 m), and Habitat (Hard-bottom, unconsolidated sediment). Note the absence of NWHI unconsolidated sampling sites between 0–30 m. Cophenetic correlation = 0.92.

Upon assessing the unbalanced sampling of hard-bottom vs. unconsolidated sediment sites, assemblage patterns between group centroids largely mirrored as previously described (Fig. 3B) with outliers attributed to small sample sizes for those strata (MHI unconsolidated sediment: n = 2, 0–30 m and NWHI: n = 3, 30–53 m). Interactive effects were disproportionately driven by intra- and inter-regional differences highlighted in successive pair-wise tests (Supplementary Material, Table S2).

Finally, the prominent species identified in SIMPER similarity/dissimilarity measures and shade plot outputs (Fig. 4) largely drove assemblage differences between regions and depth strata. These included Aprion virescens, Caranx melampygus, Carangoides orthogrammus, Caranx ignobilis, Triaenodon obesus, Carcharhinus galapagensis, Pseudocaranx cheilio, Seriola sp ., and Carcharhinus plumbeus. Comparable with MHI CAP outputs, Caranx melampygus appeared aligned with shallow and upper mesophotic sites, while Carangoides orthogrammus and Aprion virescens were encountered in higher abundances in upper and lower mesophotic zones (Fig. 4, Supplementary Material, Figure S1C, lower panel). Caranx melampygus presented a similar pattern in the NWHI, with Carnagoides orthogrammus, Caranx ignobilis, and Triaenodon obesus likewise remaining more prevalent in shallow and upper mesophotic zones. In contrast, Aprion virescens and Carcharhinus galapagensis remained more broadly distributed between depth strata, although greater abundances were noted for both species in mesophotic depths. Finally, Seriola sp., Pseudocaranx cheilio, and Carcharhinus plumbeus remained prevalent in the upper and/or lower mesophotic zones, being near-absent from shallow-water strata (Fig. 4, Supplementary Material, Figure S1D, lower panel).

Figure 4
figure 4

Shade plot showing regional (MHI, NWHI) and depth distributions of all roving predator species. Raw species relative abundance values (MaxN, hr−1: color ramped blocks) were square root transformed to down-weight more abundant species. Y-axis (roving predator resemblance): position of standardized MaxN, hr−1 predator values, ranked by Whittaker’s Index of Association transformation and Group Average Hierarchical Cluster analysis (Type III SIMPROF, with permutation between sites). Red dotted lines: groups of coherent species. Species identified in SIMPER highlighted in red. (b) X-axis: Sites grouped according to region (MHI, NWHI) and depth strata, aligned from left to right. Shade plot generated in PRIMER 7.0.11 ( Maps in the figure were generated using Adobe Illustrator CS5 (

Roving Predator Abundances: Univariate analysis

Aprion virescens were homogeneously dispersed (p > 0.05) across all depth and habitat strata (Tables 34; Fig. 5, top left), recording significant regional differences (p < 0.001; 2.5 times greater abundance in the NWHI versus MHI) irrespective of depth strata or inclusion/exclusion of habitat as a pooled covariate. In contrast, Caranx melampygus recorded no differences with any tested factor when accounting for its absence beyond 53 m across the archipelago. Habitat served to obfuscate the 3-factor design (p > 0.45) for Carangoides orthogrammus. When constrained to 53 m or less, depth was significant in the MHI (p < 0.01) as a result of a 6–15 fold increase in abundance between 0–30 m hard-bottom and all substrates between 30–53 m (Supplementary Material Table S2).

Table 4 Average abundance (mean MaxN) and standard error (SE) of select roving predator species sampled on hard-bottom vs. unconsolidated substrate in the Hawaiian Archipelago.
Figure 5
figure 5

Mean relative abundance (Mean MaxN, hr−1 ± SE) of roving predator species identified in SIMPER analyses across regions and depth strata (habitats pooled). Depth is ordered in increasing intervals, with all habitats pooled. Light grey = MHI, dark grey = NWHI. Note the differences in scales along the y-axis.

Caranx ignobilis and Seriola sp (both p = 0.0001, Table 3) were an order of magnitude more abundant in the NWHI (Table 2). In particular, only small numbers of Caranx ignobolis were encountered between 30–100 m (upper and lower mesophotic zones) in the MHI (Tables 34, Supplementary Material Table S2, and Fig. 5 middle left) in contrast with estimates recorded between 0–53 m in the NWHI. When accounting for dispersion heterogeneity driven by depth absences and habitat obfuscation, pair-wise tests retained regional dissimilarities between counts compared between 30–53 m (Supplementary Materials, Table S2). In contrast, Seriola sp recorded between 3–8 (MHI) and 21–22 (NWHI) times higher abundances in 53–100 m versus 0–30 m (Tables 34, Fig. 5 center). Following the inclusion of pooled habitats, retests for region and depth remained significant (both p = 0.0001), interactive, and heterogeneously dispersed, primarily due to the 6–13 fold abundance increase between 53–100 m in the NWHI (p < 0.001), and asymmetric, intra-regional differences in shallow versus mesophotic strata. Lastly, Pseudocaranx cheilio were completely absent in shallow waters and often observed schooling with Seriola sp in mesophotic depths (Tables 34), although no differences were detected between mesophotic zones (Supplementary Materials, Table S2).

The most commonly encountered shark in the MHI - Carcharhinus plumbeus - were recorded exclusively in the lower mesophotic zone (Fig. 5, bottom left), with nearly 4 times the number of sightings occurring on unconsolidated sediment compared to hard-bottom substrate with a similar general pattern evident in the NWHI (Table 4). Regional abundances were homogenous and non-significant when pooled habitats were compared between regions (p > 0.05, Supplementary Materials, Table S2). Finally, the two species of shark only recorded in the NWHI - Carcharhinus galapagensis and Triaenodon obesus - similarly had peak abundances between 30–53 m, were present in 0–30 m, and uncommon in 53–100 m. Despite Carcharhinus galapagensis abundance peaking in the upper mesophotic zone (Table 3 and Fig. 5, bottom center), there were no significant depth differences even when habitats were pooled. Similarly, Triaenodon obesus was most frequently encountered in the upper mesophotic zone (Fig. 5, lower right), with significant differences between depth strata (p < 0.01, Table 4); However, subsequent PERMDISP comparisons of abundance were homogenously dispersed and non-significant between 0–30 and 30–53 m, coinciding with abundance peaks in those strata and its comparative rarity in deeper depths (Supplementary Materials, Table Results from univariate species-level regression spline models, with depth presented as a continuous variable for each species identified in SIMPER by region, corresponded with previously described patterns. A graphical summary can be found in Supplementary Materials, Figure S2).

Roving Predator Length Estimates

Aprion virescens (519 ± 40 and 626 ± 13 mm) and Caranx melampygus (367 ± 19 and 507 ± 24, Table 5 and Fig. 6) were significantly smaller (both species, p = 0.0014) in the MHI than in the NWHI. While there were no differences relating to depth strata for Aprion virescens (p = 0.5412, Table 6) in either region, Caranx melampygus mean size was 29% larger at MHI mesophotic sites than at shallow-water sites in <30 m (435 ± 23 versus 337 ± 23 mm, p = 0.0007). In addition, Caranx ignobilis mean size was 26% smaller in the MHI (650 ± 36 mm) than in the NWHI (878 ± 30 mm, p < 0.01, Tables 5 and 6, Fig. 6), primarily driven by larger individuals in the NWHI observed in mesophotic strata. Finally, Carcharhinus galapagensis mean size was 45% larger in mesophotic depths compared to shallow in the NWHI (1361 ± 43; 934 ± 15 mm), contrasting with Triaenodon obesus which recorded no significant depth-based size differences (1189 ± 20; 1088 ± 55 mm, p > 0.05). Comparisons made with less than 10 measurements (Aprion virescens: MHI, 0–30 m and Triaenodon obesus: NWHI, 0–30 m) should be treated with caution.

Table 5 Mean average length (Lmean) and standard error (±) for five major roving predator species in Hawaii.
Figure 6
figure 6

Box and whisker plots indicating fork-length size distributions for Aprion virescens, Caranx melampygus, Caranx ignobilis, Carcharhins galapagensis, and Triaenodon obesus. Whiskers indicate minimum and maximum values, the box specifies the lower interquartile range, and the solid black line indicates the median. Columns with the same letter are not significantly different (P > 0.05). Empty blue circles = individual fork-lengths, solid red circles = mean, shaded contour = density of measurements by length. Box and whisker plots generated in JMP statistical software, version 12.1.0 ( Maps in the figure were generated using Adobe Illustrator CS5 (

Table 6 Results of Kolmogorov-Smirnov (K-S) tests of differences between pairs of fish length density distributions sampled by region and depth strata.

Habitat Description and Predator Linkages

Environmental variables were similar between shallow and upper mesophotic zones PCA ordinations in the MHI and NWHI (Figure S3A–C). However, DISTLM-dbRDA linkages between discriminant MHI roving predators (Pearson’s r > 0.25, Caranx melampygus, Carcharhinus plumbeus, Seriola sp ) and environmental variables were weakly correlated, with only 10.5% of the total variation accounted for by depth, % turf algae, and habitat complexity (Figure S3D). While several NWHI species aligned with areas of greater habitat complexity (e.g. Carcharhinus galapagensis, Caranx ignobilis), and depth (Seriola sp., Carcharhinus plumbeus),DISTLM-dbRDA linkages remained weak with only 18.6% of the variation explained by % hard coral, % macroalgae, habitat complexity, and depth. More detail is given in Supplementary Materials, Figure S3C,D.


For assessing predator populations, BRUVS offer several potential benefits over shallow water diver surveys. Aside from removing depth constraints associated with open-circuit scuba and potential bias due to different responses of fishes to divers in different locations, i.e. predator avoidance in populated areas and attraction in remote areas80,81,82, and reducing concerns associated with diver instantaneous versus non-instantaneous predator counts6, archived video can be used to extract data on other species or to verify the authenticity of predator identifications and length measurements83. Like all field survey methods, BRUVS have limitations including deployment challenges in vertical habitats, variable bait plume areas48, 84, and the potential for competitive exclusion of some species50, 84, 85. However, for roving reef predators that are often rare or absent during underwater visual censuses, BRUVS may provide a better community-wide representation of assemblage composition34, 48, 50.

Survey results were consistent with predator abundance patterns documented in underwater visual censuses in the MHI and NWHI, albeit over a wider depth range (0–100 m). While pooled abundance values (all species) were three times higher in the NWHI (Table 2), differences were more pronounced for gregarious species. Specifically, Caranx ignobilis and pooled Seriola sp were over an order of magnitude more abundant in the NWHI (all depths and habitats combined), which aligns with historic predator densities recorded by belt transect in ≤30 m−1, although reported belt-derived ratios for Caranx ignoblis alone were considerably higher than 10:1.

Sharks can be patchily distributed over fine spatial scales86, 87, and while BRUVS sampled more shark species than are typically encountered by open-circuit scuba divers, several were potentially underrepresented (or were not recorded at all) in this study. This likely came as a result of (1) sparse sampling or exclusion of some habitat types (e.g. backreef and lagoons were not sampled) and/or several Hawaiian islands, (2) constraints due to limited seasonal and day-time only sampling; and (3) one-hour BRUVS soak time limits. For example, only a single blacktip reef shark was sighted during MHI surveys (Carcharhinus melanopterus, shallow water observation at Lanai, Fig. 7A), but localized aggregations of that species are known to occur, e.g. at Pelekane Bay on the Big Island, MHI88. In addition, a single mesophotic blacktip shark (Carcharhinus limbatus) sighting occurred outside of the one-hour BRUVS sampling period on Oahu (Fig. 7B) and while both species can be found in low numbers in the both the MHI and NWHI, their absence during this study suggests future BRUVS sampling could be improved, at minimum, by expanding surveys to include additional islands in the Hawaiian Archipelago, increasing the number of sites at each island, and incorporating backreef/lagoonal environs into future designs31, 89.

Figure 7
figure 7

(A) Carcharhinus melanopterus, Lanai. (B) Carcharhinus limbatus, Oahu. Mesophotic sighting outside of 1-hour BRUVS sampling period (C) Carcharhinus amblyrhynchos, Maui. (D) Juvenile Galeocerdo cuvier, Maui. BRUVS frame grab photographs by J. Asher.

Similarly, no Carcharhinus galapagensis or Triaenodon obsesus were sampled during MHI BRUVS surveys, and only two Carcharhinus amblyrhynchos were recorded (one mesophotic site off of the Maui town of Lahaina (Fig. 7C), and one shallow water site off of the south shore of Oahu). While Galapagos sharks were once deemed abundant in the MHI and are noted for frequent sightings and seasonal movements in certain areas (e.g. north shore of Oahu), they remain spatially restricted around islands hosting high human population densities, with historic catch-rates low in comparison with sandbar, tiger, and grey reef sharks89,90,91,92,93,94. In addition, while MHI divers on open-circuit scuba may encounter grey reef sharks or white tip reef sharks more frequently than other species, they appear relatively uncommon and/or patchily distributed outside of localized populations, with known grey reef shark aggregations around Molokini, Niihau, and Ka’ula Rock in the MHI and Necker and French Frigate Shoals in the NWHI, and historic white tip reef shark sightings along Oahu’s western, southern, and eastern shorelines, along with South Maui, Molokini, and the Kona coast of the Big Island91, 95, 96. When combining the absence (in BRUVS surveys) of both species in the MHI irrespective of surveyed depths or habitats, scant grey reef and blacktip reef shark sightings, common bycatch rates observed for commercial and recreational fisheries across the state’s coastal waters, and the 5-fold difference in pooled shark abundances between MHI and NWHI (Table 2), these collectively serve as additional evidence towards reduced reef-shark baselines around populated areas7, 95,96,97.

The majority of MHI BRUV sightings occurred in mesophotic depths. Aside from Carcharhinus plumbeus and a single Carcharhinus amblyrhynchos, these consisted exclusively of mature or small-bodied (≤2 m) female tiger sharks, Galeocerdo cuvier (Fig. 7D), which may be indicative of migratory patterns documented from the NWHI to the MHI linked to the September – November pupping season, or possible evidence of sex segregation98, 99. While additional environmental effects (thermal, available food resources) may explain the increased mesophotic presence seen here, interpretations based on small BRUVS sample sizes should be treated with caution, as tiger sharks are depth-generalists that may be considerably more abundant (comprising up to 20% of all sharks captured during longline surveys in the NWHI) than accounted for in this study17, 31.

Overlaps between shallow water and upper mesophotic zone roving predator communities, coupled with a partial separation of lower mesophotic zone assemblages, was seen in both the MHI and NWHI, albeit with divergent species and depth distributions driving interzone connectivity. In the NWHI, Aprion virescens remained more broadly distributed between depth strata; however, shallow water-upper mesophotic zone overlaps for three jacks (Caranx melampygus, Caranx ignobilis, and Carangoides orthogrammus) and the numeric majority of two sharks (Triaenodon obesus and Carcharhinus galapagensis) between 0–53 m hint at several possible, interactive drivers, including prey-partitioning mechanisms100, competition with more abundant species in the lower mesophotic zone (e.g. Seriola sp , Carcharhinus plumbeus), and/or the reduced density of preferred prey in deeper depths. While isotopic analyses indicate Carcharhinus galapagensis primarily forage in shallow water, their movements in mesophotic depths may be underestimated, and runs contrary to longline studies which captured the majority of Carcharhinus galapagensis between 40–45 m15, 29, 92. The prevalence of smaller Carcharhinus galapagensis and Caranx ignobilis in <30 m depths suggests possible body size and depth segregation, potential avoidance of intra- or inter-specific predation pressures101 in deeper waters despite documented juvenile Galapagos shark movements in mesophotic depths thought to be tied to diel, vertical migration patterns, and no evidence of NWHI shallow water nursery areas as seen elsewhere91, 92, 102. Predator alignments with thermocline position103, and increases in mesophotic fish densities (i.e. prey availability) between 50–60 m25, 73 coincide with higher upper mesophotic abundances documented for the principal species encountered during NWHI BRUVS surveys. Finally, Hawaiian monk seal (Neomonachus schauinslandi) CrittercamTM surveys noted peak predator escort and foraging interactions between seals and Aprion virescens, sharks, and jacks occurring between 60–80 m, suggesting predator depth adjustments may be coupled to seal foraging in some cases30, 104. The general absence of predator movements in >100 m depths or interisland transits15, 30, 105, 106 are indicative of predatory spatial residency, and that BRUVS appear to capture overall depth-range demographics for these aforementioned species in the NWHI. This appears to be confirmed with historic bait station and submersible surveys in bottom fish depths (286–657 m), where shark sightings were rare and Aprion virescens, Caranx ignobilis, Caranx melampygus, and Carangoides orthogrammus were absent, but Pseudocaranx cheilio and Seriola sp were commonly sighted107. Whether size-differences or depth distributions directly relate to prey-partitioning, proportionately available habitats and host prey resources, competition with other species in deeper depths, or other causes remains an important area for future research, along with expanded investigations into Carangidae diel, lunar, and seasonal migrations (e.g. with Caranx ignobilis)105, and nutrient transport potential between depth zones15.

Large-bodied snappers, jacks and sharks are susceptible to fishing activities in the MHI, and changes in abundance and/or biomass may be indicative of extraction pressures12, 25, 108, 109. Mesophotic habitats may act as depth-refuges for species considered particularly vulnerable to fishing16, 25, 110, and evidence from this study remains suggestive of potential depth insulation for several predators in the MHI, mirroring patterns seen elsewhere26, 39, 103, 111. In particular, Caranx melampygus was one of the primary species responsible for shallow-upper mesophotic zone overlaps in the MHI, with relatively similar numbers recorded between zones; however, overall mean fork-lengths were smaller in <30 m than at mesophotic sites or at sites in the NWHI. Carangoides orthogrammus were 6–15 times more abundant in the upper mesophotic zone than in diver depths, and Caranx ignobilis were only recorded in mesophotic zones in the MHI. In contrast, inferences on MHI shark population parameters are limited by low number of encounters during this study. Sightings of Carcharhinus plumbeus align with previous research, which have shown sandbar sharks to be the most common shark species in the MHI, that they are primarily captured in 60–90 m depths (although they may diurnally migrate to shallower depths of 18–20 m at night, and depth-segregate by age and sex), and that they are less abundant than several other shark species at location in the NWHI91, 112. However, in this study, mean abundance (0.12 ± 0.05 vs. 0.09 ± 0.03) and encounter rate (8.4% vs. 9%) were similar between regions (Table 2, which coupled with comparable longline catch-rates at French Frigate Shoals31, suggests that sandbar sharks may not be as uncommon in the NWHI as previously suspected.

Pooled environmental covariates delineated largely along a priori designated survey depth strata, with overlaps between regions, i.e. environmental variables generally appear similar between the MHI vs. NWHI (Supplementary Materials, Figure S3A–C). However, environmental linkages with roving predator assemblages were tenuous at best (Supplementary Materials, Figure S3D,E), and may be indicative of (a) the highly mobile nature of the roving predators and the utilization of multiple habitats; or (b) limited or asymmetric sampling frequencies between depths and habitats.

Finally, most open-circuit dive surveys focus exclusively on hard-bottom substrates, which may miss a proportion of the predator population occupying large areas of unconsolidated sediment in the Hawaiian Archipelago (especially the MHI). While roving predators may retain inherent preferences towards hard-bottom substrates, the assessed species presented here (except for whitetip reef sharks) are known to utilize shallow water sandy habitats13, 105, 106, 113,114,115 and were similarly encountered on mesophotic sand flats during the course of this study. In addition, Caranx melampygus, Caranx ignobilis, Aprion virescens, and Seriola sp were all observed feeding in areas of unconsolidated sediment (J. Asher, pers. obs.); however, while several studies indicate the presence of high predator biomass over sand flats in comparison with other functional groups, the frequency and ecological effects of sand flat usage as foraging grounds, seasonal aggregation sites, refugia, or as transitional habitats (i.e. as corridors between areas hosting higher complexity, hard-bottom substrates) remains largely unaccounted for97, 116, 117. Future BRUVS surveys would benefit from the inclusion of these areas in subsequent designs, as roving predators normally associated with reef and hard-bottom systems are clearly present in deeper, underexplored, unconsolidated sediment habitats in the MHI.

In conclusion, roving predator research has been heavily reliant on underwater visual censuses, along with a smaller number of fishery independent remote underwater video surveys, tracking studies, and limited fishery-dependent or extractive surveys31. The use of BRUVS and the expansion of surveys into mesophotic depths augment our understanding of roving predator distributions across the Hawaiian Archipelago, and illustrate the need to expand long-term predator research and monitoring beyond open-circuit SCUBA depths.