Large-bodied reef fishes represent an economically and ecologically important segment of the coral reef fish assemblage. Many of these individuals supply the bulk of the reproductive output for their population and have a disproportionate effect on their environment (e.g. as apex predators or bioeroding herbivores). Large-bodied reef fishes also tend to be at greatest risk of overfishing, and their loss can result in a myriad of either cascading (direct) or indirect trophic and other effects. While many studies have investigated habitat characteristics affecting populations of small-bodied reef fishes, few have explored the relationship between large-bodied species and their environment. Here, we describe the distribution of the large-bodied reef fishes in the Mariana Archipelago with an emphasis on the environmental factors associated with their distribution. Of the factors considered in this study, a negative association with human population density showed the highest relative influence on the distribution of large-bodied reef fishes; however, depth, water temperature, and distance to deep water also were important. These findings provide new information on the ecology of large-bodied reef fishes can inform discussions concerning essential fish habitat and ecosystem-based management for these species and highlight important knowledge gaps worthy of additional research.
Citation: Richards BL, Williams ID, Vetter OJ, Williams GJ (2012) Environmental Factors Affecting Large-Bodied Coral Reef Fish Assemblages in the Mariana Archipelago. PLoS ONE 7(2): e31374. https://doi.org/10.1371/journal.pone.0031374
Editor: Simon Thrush, National Institute of Water & Atmospheric Research, New Zealand
Received: May 11, 2011; Accepted: January 8, 2012; Published: February 27, 2012
This is an open-access article, free of all copyright, and may be freely reproduced, distributed, transmitted, modified, built upon, or otherwise used by anyone for any lawful purpose. The work is made available under the Creative Commons CC0 public domain dedication.
Funding: The National Marine Fisheries Service Office of Habitat Conservation and National Oceanic and Atmospheric Administration's Coral Reef Conservation Program provided funding for this work. The funders had no role in study design, data collection and analysis, decision to publish, or preparation of the manuscript.
Competing interests: The authors have declared that no competing interests exist.
In the terrestrial world, studies of habitat use and resource selection form much of our understanding of wildlife habitat requirements , and such studies can potentially provide the basis for effective, spatially based ecosystem management in the marine world as well. Agardy et al.  state that marine spatial planning should, at a minimum, include the identification of priority areas as a key element in the design process, and investigations of the relationships between reef fishes and their environment are key in identifying such priority areas. Indeed, many reef fishes have evolved adaptations suiting them to particular reef zones , and many studies have described ways in which habitat characteristics affect assemblages of small-bodied reef fishes living in close association with the reef framework and how knowledge of these associations can inform management decisions –. Several authors have also investigated the effects of environmental variables on the distribution of small and large-bodied pelagic  and estuarine – fishes. However, less work has focused on the relationships between environmental variables and large-bodied fishes associated with coral reefs , especially those in the Mariana Archipelago. Many of these large-bodied fishes are capable of traveling great distances, allowing them to regularly move among various different habitat types. Meyer et al.  found that giant trevally (Caranx ignobilis) in the Northwestern Hawaiian Islands, made periodic atoll-wide excursions of up to 29 km. These same authors found that green jobfish (Aprion virescens) were seasonally attached to core areas of up to 12 km in length. These fish were able to range 19 m across atolls with daily round-trip excursions of up to 24 km . McKibben and Nelson  found that grey reef sharks (Carcharhinus amblyrhynchos) at Enewetak inhabited home ranges of up to 53 km2 and 16 km in length. Finally, Holland et al.  found that Bluefin trevally (Caranx melampygus) on patch reefs in Kaneohe Bay, Hawai'i, appear to inhabit fairly stable home ranges for periods of at least a few weeks and possibly up to a year. During the day, tagged fish would patrol back and forth along the face of the patch reef, traveling distances of several hundred meters, and often changing direction at the same point each along the reef. With the exception of most of the pelagic studies and work done on the Great Barrier Reef –, most research has focused at relatively small scales—a single estuary, bay, or island—and not at the scale of an entire archipelago. While it is important to investigate small-scale relationships that may differ from island to island and even between different sites within an island, it is no less important to investigate higher-level relationships operating at the archipelagic scale and which may not be apparent from analyses carried out at the site or even island scale , .
Although tourism is now a key industry, a healthy nearshore coral reef ecosystem able to provide key ecological, economic, and social benefits is no less important . Fish represent the primary natural resource in the Mariana Archipelago, and large-bodied individuals including some species of surgeonfishes (Acanthuridae), jacks (Carangidae), emperors (Lethrinidae), snappers (Lutjanidae), groupers (Serranidae), wrasses (Labridae), and parrotfishes (Scaridae) tend to be preferentially harvested both for local consumption and export –. Large-bodied reef fishes also are of particular importance for a variety of ontogenetic and phylogenetic reasons. Within a species, the largest individuals tend to supply the bulk of the reproductive output for their population . For example, Sudekum et al.  found that fecundity in Caranx melampygus ranged from approximately 50,000 mature ova for a fish of 760 g (32.8 cm SL) to over 4 million for an individual of 6490 g (64.0 cm SL). Sequential hermaphroditism is common in many teleost fishes including many parrotfishes (e.g. Scarus rubroviolaceus) and wrasses (e.g. Cheilinus undulatus), with the largest individuals often being disproportionately male or female . Hence, the removal of the largest individuals can have a disproportionate impact on a single gender with associated effects on the reproductive potential of the population. Large-bodied species also tend to have protracted spawning periods , and can have a disproportionate impact on their environment, often as apex predators ,  or primary agents of bioerosion , . Furthermore, the loss of large-bodied species can have a cascading (direct) or indirect effect on lower trophic levels and ecosystem balance –. Unfortunately, large-bodied individuals tend to be preferentially targeted by fishers, and many large-bodied species are among the most vulnerable to overfishing because they share a suite of life-history characteristics including large size, slow growth rates, and delayed sexual maturity –. Many species of sharks are additionally vulnerable due to their low reproductive rates.
Currently, several fishery targets including snappers, groupers, jacks, surgeonfish, sharks, and large emperors show higher relative abundances in the remote northern islands of the Mariana Archipelago compared to the populated islands of the south, and it has been suggested that abundance and biomass of some taxa has declined in recent decades . Guam, the southernmost major island in the archipelago, has experienced a decline in nearshore reef-associated fish populations accompanied by a sharp decline in catch per unit effort (CPUE) –. Large-bodied species including bumphead parrotfish, humphead wrasse, stingrays, parrotfish, jacks, emperors, and groupers are considered rare in Guam, and it has been suggested that this may be the result of heavy fishing . Technological improvements, which have facilitated the expansion of activities like nighttime SCUBA spearfishing, have resulted in a reappearance of larger species in fishery catch statistics . While it is possible that this resurgence in catches indicates greater targeting of “healthy” populations, it would seem more likely that such increases are related to the use of new technology, representing the next step in the serial depletion cycle seen in many fisheries , .
At local, regional, and international scales, marine resource management is moving toward a suite of ecosystem-based management approaches including spatial closure and the protection of Essential Fish Habitat . The Western Pacific Regional Fishery Management Council is beginning to integrate ecosystem approaches to management in Guam and the CNMI . However, their current Fishery Ecosystem Plan for the Mariana Archipelago report also states that little is known about the life history, habitat utilization, food habits, or spawning behavior of most of the resident coral reef species. Agardy et al.  further argue that true integrated marine protected area planning has yet to be achieved and that the “blind faith” many have placed in often poorly planned and inadequately thought-out marine protected areas carries with it great risk.
Here we test the relative influence of various anthropogenic, physical, oceanographic, and biological environmental factors on the distribution of large-bodied reef fishes in the Mariana Archipelago. Our results show that human populations likely affect the distribution of large-bodied reef fishes but that assemblages are highly variable and other factors including depth, temperature, distance to deep water and many others likely play a role. These results provide additional insight on the relationship between these reef fishes and their environment, can inform discussions of essential fish habitat for these large-bodied reef fishes, and can provide information for managers in their efforts to implement ecosystem-based approaches to fishery management.
The Mariana Archipelago (politically the CNMI and the US Territory of Guam) is an elongate string of islands stretching 950 km northward in an arc from the island of Guam (13.44°N, 144.76°E) to the Farallon de Pajaros (20.54°N, 144.89°E) (Fig. 1). Islands range in age from 1 to 1.5 million years in the north to >30 million years in the south . The northern islands are volcanically active and topographically complex. The archipelago contains ∼230 km2 of shallow-water (<18 m) coral reef habitat, and is the second largest reef area under U.S. jurisdiction in the Pacific , . Each island is surrounded by diverse shallow-water coral reefs ranging in size from 0.8 km2 around Farallon de Pajaros to 108 km2 surrounding Guam . Humans have occupied the Mariana Archipelago since about 3500 B.P. , and the present day human population generally declines along a south-to-north gradient from ∼150,000 in Guam and ∼62,000 in Saipan to near zero in the northern islands (U.S. Census Bureau; Census 2000).
Between 2003 and 2009, the Coral Reef Ecosystem Division (CRED) of the NOAA Pacific Islands Fisheries Science Center (PIFSC) conducted 508 large-scale towed-diver surveys for large-bodied (>50 cm Total Length) reef fishes, covering 1038 ha (10.4 km2) of the shallow-water (<30 m), coral reef environment around 20 islands and offshore banks in the Mariana Archipelago. These surveys were conducted as part of an ecosystem-wide long-term monitoring program and the lower size threshold of 50 cm TL was chosen to enable observers to concentrate their efforts on the large-bodied, patchily distributed, rare and more mobile species and individuals that were not as effectively sampled by other methods . The 50 cm TL threshold also effectively captured the majority of species often referred to as “apex predators” (e.g., carcharhinids, carangids), as well as the larger herbivores (e.g., scarids) and some species of particular concern (i.e., C. undulatus). With the exception of sharks, this size threshold also generates data on the largest of the sexually mature individuals (e.g. Lm for Caranx melampygus = 35 cm), which, as mentioned earlier, are expected to have the greatest effect on their environment or population.
Within each year, the entire archipelago was surveyed within a span of 1–2 months. The details of the methodology and its utility for surveying assemblages of large-bodied reef fishes are provided by Richards et al. . In brief, surveys were conducted by means of SCUBA diver-controlled towboards equipped with still and video camera equipment and SeaBird™ SBE39 high-resolution temperature/depth recorders. Divers were towed side-by-side at the end of 60 m lines behind a small survey launch along a depth contour (∼15 m) at a speed of ∼1.5 kt for a duration of 50 minutes per survey. Each survey was partitioned into ten 5-minute survey segments. A global positioning system (GPS) unit mounted on the survey launch recorded survey track points at 5-second intervals, and a custom layback algorithm allowed the diver track to be plotted in a geographic information system (GIS) and merged with spatial data sets (e.g. benthic habitat maps, wave energy estimates). During each survey, one diver recorded, to the lowest possible taxon, all large-bodied reef fishes (>50 cm TL) observed within a 10-m wide lane, focusing observations ahead in a 10-m long moving window. The total length of each fish was estimated to the nearest 5 cm. Cryptic species and fish observed behind the diver were not recorded. Fishes seen leaving and then reentering the survey area were recorded only once. The second diver simultaneously recorded benthic habitat information (e.g. % cover of coral, algae, habitat complexity) as detailed by Kenyon et al. . Habitat complexity is recorded on a six-point scale and is a subjective measure of the topographic diversity or amount of “roughness” of the substrate. Examples of low complexity include sand flat or rubble plains. Areas of steep spur and groove, canyon, pinnacles and walls would be classified as high or very high complexity.
Fish abundance and size data were converted to biomass density (hereafter “biomass”) using the allometric length-weight conversion: W = aTLb, where parameters a and b are species-specific constants, TL is total length in mm, and W is weight in grams. Length-weight fitting parameters that most closely matched they survey location and fish size class were obtained from FishBase  and Kulbicki et al. . When length-weight fitting parameters used other than total length, length-length conversions were made using formulas from the same sources. A data subset was created that contained species-level biomass values. A relational database and ArcGIS 9.3.1 were used to generate a variety of in situ and remotely sensed environmental variables having demonstrated potential to influence the distribution of reef fishes (Table 1). While measures of primary productivity are important to include in ecological models, we have excluded such measures from this analysis for several reasons. Firstly, existing data are unlikely to provide an accurate measure of nearshore primary productivity patterns in this region and at the scale of our study as the standard algorithms are based on the assumption of “optically deep” (i.e. no bottom reflectance) waters. This assumption is violated in the clear, nearshore, shallow-water areas from which the data for this study was derived. Secondly, terrigenous nutrient loading from natural and anthropogenic sources is likely to greatly exceed and mask any open ocean patterns. Hence, remotely sensed primary productivity values derived form open ocean sources would not reflect actual nearshore patterns in primary productivity. Because many of the data layers did not completely overlap with one another or with our towed-diver surveys, it was necessary to further subset the data to create a data matrix that contained only those records with values for all variables.
Reef area was calculated based on hard-bottom habitat present within the 0–30 m depth range. Benthic habitat was classified using a combination of in situ and remotely sensed data. In situ data included % cover of coral, macroalgae, crustose coralline algae (CCA), sand, and rubble and the habitat complexity index we described in the survey protocols. Remotely sensed benthic habitat map layers depicting benthic habitat structure and cover classes, based on IKONOS™ satellite imagery  were converted to 5-m resolution raster layers in ArcGIS 9.3.1. Major reef structure (e.g. Rock/Boulder, Pavement, Aggregate Reef) and cover (e.g. Coral, Macroalgae, Uncolonized) categories were defined by NOAA's National Centers for Coastal Ocean Science (NCCOS), using a standard hierarchical classification scheme in which the term benthic cover refers only to biological cover type (i.e. coral, algae) and structure refers to only substrate type, denoting geomorphologic structure (i.e. pavement, sand, reef). The dominant benthic cover and structure were calculated for each survey. The dominant habitat was defined as that assigned to the majority of grid cells within a given survey area. Cover and structure richness values were also calculated based on the “variety” or number of different cover or structure types contained within each survey area.
An attempt was made to incorporate quantitative information on benthic slope and complexity from existing shallow-water multibeam bathymetric maps . However, the level of overlap (∼20%) between the multibeam data (for which the shallowest extent is ∼30 m) and our biological surveys (where the deepest extent is 30 m) was insufficient for analysis. In an effort to nonetheless incorporate information of this type, measures of benthic habitat complexity (as recorded by the benthic towed diver) and distance between each survey and the 50-m isobath were used.
Oceanography and other Variables
Sea water temperature and diver depth were recorded during each survey using SeaBird™ SBE39 temperature and pressure loggers. Larger-scale sea surface temperature at the island-scale was derived from Pathfinder 4.1 Advanced Very High Resolution Radiometer (AVHRR) Global Climatology . SST values were averaged over a 9 km grid spacing, using nighttime monthly means, averaged over five years of data (2006–2010). NOAA Wave Watch III (WW3) data were used as a proxy for overall wave energy impinging on the shallow reef. WW3 output is a time series (six hour interval) of offshore (deepwater) directional wave energy spectra. Twelve years of WW3 data (1997–2009) were used to calculate average energy flux for each frequency and direction, using deepwater linear wave theory (Equation 1). Direction was binned in 10-degree increments from 0–360 degrees. Period was binned in 2-second increments from 4 seconds to 20 seconds. Frequency is defined as 1/Period yielding a frequency range of 0.05 Hz to 0.25 Hz.
Equation 1. Wave energy flux in watts per meter of wave front.
The frequency range with the maximum calculated energy flux was used as an approximation of maximum, and therefore most significant, offshore wave stress. This yielded a maximum offshore wave energy flux (watts per meter of wave front), or maximum power, for each directional bin for each island. The maximal wave energy bin in each quadrant was then used as input for the model. Island quadrant (i.e., NE, SE, SW, NW) was also included as a descriptive variable and was calculated based on the previously calculated directional bins. The time of day for each survey was recorded and moon phase was calculated based on the survey date.
In the absence of specific data on human impacts such as fishing intensity, human population density per unit reef area was used as a proxy for anthropogenic pressure. Local population estimates came from the 2000 United States Census. Reef area was calculated using a range of GIS layers on bathymetry and bottom type to represent all hardbottom area <30 m deep. Islands were also classified into human population categories of High (>100,000 individuals), Mid (50–1,000 individuals), Low (1–50 individuals), and None. Islands in the Saipan-Tinian-Aguijan complex were each classified as Mid-level based on likely impact level given their close proximity to one another (Tinian is 5 km from Saipan, Aguijan is 8 km from Tinian and 30 km from Saipan), reports that fishers frequently travel among these islands, and information that shore-based fishing has occurred on Aguijan by operations based on the other islands (Trianni, M., pers. comm.). It should be noted that, while we do not have data on the percentage of the population that regularly engages in fishing activities, a large number of immigrant workers reside on Saipan, and these workers do not typically engage in fishing. There are fewer of these workers on Tinian and Rota and therefore, while the total population is lower, the percentage of fishers on these islands is likely greater than on Saipan.
The final merged data set (with fish and environmental variables) contained 3711 individual survey segments from 445 surveys conducted around 12 of the 20 islands/banks: Agrihan, Aguijan, Alamagan, Asuncion, Guam, Guguan, Maug, Pagan, Rota, Saipan, Sarigan, and Tinian (Fig. 1). The offshore banks (Stingray Shoals, Pathfinder, and Arakane) and Anatahan were excluded from the analysis, as they were surveyed only during the first year of sampling. Farallon de Pajaros (FDP) was excluded because of the low number of replicates that included all variables. A two-stage analysis was employed using PRIMER v6.1.13 , followed by Boosted Regression Trees (BRT)  in the R statistical language v2.6.1 . Data were analyzed at two scales: a larger scale in which data were pooled by island and a smaller scale using data from each towed-diver survey.
PRIMER was used for the initial, broad-scale multivariate analysis involving all large-bodied reef fish species at both the island and survey-segment scale to determine the following: 1) similarities in large-bodied reef fish assemblages among islands across the archipelago, 2) which large-bodied reef fish species contributed primarily to any observed patterns and 3) which of the available environmental variables best predict the patterns in the large-bodied reef fish assemblages. The results of the PRIMER analyses were further used to help define the scope of the smaller-scale BRT analysis (e.g. which large-bodied reef fish species would be analyzed). Overall, PRIMER was deemed better able to handle the full multivariate data set, whereas BRT was better able to handle the combination of categorical and continuous variables and produced a more detailed description of the relationship between environmental predictor variables and fish response variables.
Species-level biomass densities were transformed using species-specific dispersion weighting to down-weight highly variable or ‘clumped’ species and to reduce similarity between sampled subregions –. This transformation also down-weighted particularly high biomass species and the need for further transformation was not indicated.
Data were pooled by island to assess large-scale patterns across the archipelago and the relationship among islands. A similarity profile test (SIMPROF;  was used to determine if significant, interpretable structure in the data existed and, where structure was evident, resemblance matrices were constructed using Bray-Curtis similarity measures . The results of the SIMPROF analysis were visualized using hierarchical cluster analysis and nonmetric multidimensional scaling (nMDS) . The SIMPER  routine was used to determine the relative influence of individual species on the dissimilarity among groups.
At the smaller scale, Spearman rank correlation was used to identify covarying explanatory variables and, where pairwise rank correlation coefficients were greater than |0.75|, we selected a single variable to represent each variable group. This variable was selected based on data range, interpretability, and ecological theory. Variables estimating % cover were log transformed to reduce skew and all variables were normalized to account for different ranges and measurement scales. The RELATE routine  was used to test for a relationship between segment-level species biomass and environmental variables and the BEST routine  was used to select a subset which best explained the overall structure in the large-bodied assemblage.
To measure the relative impact of candidate environmental predictor variables on fish response variables and to assess the specific shape of each relationship, 3711 individual survey segments were modeled simultaneously against 18 continuous and categorical predictor variables (Table 1) using Boosted Regression Trees (BRTs) . BRTs were constructed using the gbm (v1.5-7)  and gbm.step  packages in the R statistical language v2.6.1  (Table 2). Regression trees have many desirable properties, including 1) the ability to handle various types of response and predictor variables including both continuous and categorical, 2) the invariance of trees to monotonic transformations of predictors, 3) the ability to model complex interactions in a simple form, and 4) the ability to easily manage missing predictor values with minimal information loss . The two main weaknesses of trees – that they are poor predictors and that large trees can be difficult to interpret – are largely overcome through the use of boosting and consequently, boosted trees are increasingly used in ecological studies –.
BRTs do not assign real probabilities (i.e. p-values) and instead use a cross-validation process, which requires some of the data to be held back for model development and validation. Nevertheless, the full data set is still used to fit the model. We used cross validation deviance (CVD) and standard error (SE) as the measure of model performance, where lower values indicate a better model (e.g. a CVD of zero indicates that the model is able to predict new data without any predictive error, and larger CVDs indicate increasing amounts of error). Model optimization was achieved by varying the model parameters: tree complexity, learning rate, and bag-fraction. Tree complexity determines the number of nodes in a tree, while the learning rate is used to shrink the contribution of each tree as it is added to the model. The bag-fraction determines the proportion of the data to be selected at each step in model development and therefore affects stochasticity. We coded a loop routine which sought to minimize model CVD, among models with a minimum of 1000 trees, by adjusting all possible combinations of tree complexity (1, 2, 3, 4, 5), learning rate (0.05, 0.01, 0.001, 0.0001), and bag fraction (0.1, 0.5, 0.75). The combination with the lowest CVD was used to create the final BRT model. Relative importance values for each environmental variable were calculated based on the number of times each variable was selected for splitting . Higher relative importance values for a given environmental variable indicate a stronger influence on either total large-bodied reef fish biomass or species distribution. Partial dependency plots were used to interpret the relationship between the environmental predictors and the fish response variables.
Analyses were carried out for total biomass of large-bodied reef fishes and for the occurrence (presence-absence) of eight individual species (Table 3). We were unable to use biomass data at the species level, as assumptions of normality were not valid even after extreme transformation. Species were primarily chosen based on their prevalence in the data, but also because of their relative contribution to overall patterns, and/or their ecological, economic, or management importance (e.g. as apex predators , , bioeroding herbivores , , fishery targets, or as IUCN “red list” species) (Table 3). Macolor niger and M. macularis were grouped as species of Macolor because of their ecological similarity and the difficulty distinguishing between the two species in the field. Total biomass values were double (log+1) transformed to achieve normality (or pseudo-normality)  and were analyzed based on a Gaussian distribution as required by the technique. Species-level counts were converted to presence-absence by survey segments and were analyzed using a binomial distribution, because the large proportion of zero values precluded normality even after extreme transformation. For each taxanomic group, we also quantified interaction effects among the various predictors (the collinearity and synergistic effect upon predicting the response in question) using the gbm.interactions routine . In this routine, the relative strength of interaction fitted by BRT is quantified by the residual variance from a linear model, and the value indicates the relative degree of departure from a purely additive effect, with zero indicating no interaction effects. One can also think of the interaction value as the relative contribution of the interaction between the two predictors towards the overall predictive performance of the individual model (the cv deviance value). For each taxonomic group, we have chosen to report the top two interactions based on interaction value.
A total of 6280 individual large-bodied reef fish from 67 species were encountered during the survey period. While we were able to reject a null hypothesis of no spatial autocorrelation using Spearman rank correlation between resemblance matrices based on multivariate species-level biomass and the geographic coordinates for each survey segment, the effect size was weak (ρ = 0.113, p = 0.001, 999 permutations). The predominant pattern is that of a latitudinal gradient in mean total biomass of large-bodied reef fish (all species and years pooled), ranging from 0.10 g/100 m2 (SE 0.02) at Guam to 2.13 g/100 m2 (SE 0.39) at Farallon de Pajaros (Fig. 2). The northern (FDP – Sarigan) section of the archipelago has a mean total biomass level nearly twice that of the southern (Saipan – Guam) section (1.81 g/100 m2 [SE 0.10] vs. 0.97 g/100 m2 [SE 0.05]). This separation between the northern and southern portion of the archipelago was maintained in the restricted data set that incorporates the environmental data.
Error bars are 1 standard error.
This pattern was evident in the hierarchical CLUSTER and nMDS analysis, based on species-level biomass density, and the SIMPROF test, which showed a distinct separation between the northern islands, which showed absent (None) to Low human population levels, and those in the south, which showed Mid to High populations (Global R = 0.044, p = 0.001) (Fig. 3). This dissimilarity was driven primarily by five major taxa (Carcharhinus amblyrhynchos, Lutjanus bohar, species of Macolor, Triaenodon obesus, and Naso hexacanthus), all of which showed higher biomass values at the northern, less populated islands (Table 4). Carcharhinus amblyrhynchos and species of Macolor were observed only in the northern islands, with the highest biomass densities observed at Asuncion Island (0.57 g/100 m2 [SE 0.16] and 0.21 g/100 m2 [SE 0.08], respectively). Although Lutjanus bohar and Naso hexacanthus were observed at both the northern and southern islands, biomass densities were higher at the northern islands, with the highest levels of both observed also at Asuncion (0.28 g/100 m2 [SE 0.04] and 0.11 g/100 m2 [SE 0.03], respectively). Triaenodon obesus were observed at both the northern and southern islands; however, biomass densities were higher in the northern islands with the highest levels at Maug and Alamagan Islands (0.14 g/100 m2 [SE 0.02] and 0.12 g/100 m2 [SE 0.03], respectively).
Cluster contours represent significant SIMPROF groups (∼30% similarity within groups). In the first panel, symbols reflect level of human population. Aguijan is categorized as “Mid” human population due to the influence of nearby Tinian and Saipan as well as reported visitation by fishers from Guam. Subsequent panels are the same nMDS as panel 1, with symbols representing relative biomass of each species.
The null hypothesis of no relationship between large-bodied reef fish species distribution and the predictor variables was rejected (ρ = 0.109, p = 0.001). Of the 15 continuous predictors, human population density (human population per reef area) provided the BEST match (corr. = 0.197). Excluding human population density from the analysis resulted in a BEST match that, while having a lower correlation (0.106), indicated four environmental variables as significant predictors (Moon phase, % Coral Cover, % Sand Cover, and Variety in Habitat Structure). We were able to quantify the relative influence of each of the 18 continuous and categorical environmental variables using Boosted Regression Trees (Fig. 4 & Table 2) and were able to interpret the specific nature of each relationship in more detail using the resulting partial dependency plots (Fig. 5).
Species selection was based on maximum data density, and management and ecological importance. CAAB = Carcharhinus amblyrhynchos, LUBO = Lutjanus bohar, MASP = Macolor spp., TROB = Triaenodon obesus, NAHE = Naso hexacanthus, SCRU = Scarus rubroviolaceus, CAME = Caranx melampygus, CHUD = Cheilinus undulatus.
Species selection was based on maximum data density, and management and ecological importance. CAAB = Carcharhinus amblyrhynchos, LUBO = Lutjanus bohar, MASP = Macolor spp., TROB = Triaenodon obesus, NAHE = Naso hexacanthus, SCRU = Scarus rubroviolaceus, CAME = Caranx melampygus, CHUD = Cheilinus undulatus.
Total large-bodied reef fish
Three relationships contributed most strongly to predicting total large-bodied reef fish biomass (Figs. 4 & 5a). Biomass was highest in areas with low human population density (relative influence [RI] = 26.4%) and decreased as human population increased. Biomass also gradually increased as in situ water temperature increased (RI = 15.7%), rose steeply once water temperature neared 30°C, and peaked at just over 30°C. Total biomass density of large-bodied reef fish also increased with increasing depth (RI = 11.5%) and with proximity to deep water (RI = 9.4%). Overall model CVD was 0.003 with a second order interaction between depth and temperature (Table 5). The effect of depth was exacerbated in the warmest areas (near 30°C) and the effect of temperature was similarly exacerbated in the deepest areas (deeper than ∼20 m). In general biomass is highest at deeper depths (>20 m) and at higher temps (above 30°) (Fig. 6). However, biomass is also higher below 20 m across the entire temperature range.
The effect of temperature on total large-bodied reef fish biomass is magnified in areas of warm water and the effect of temperature is magnified at deeper depths.
Three relationships contributed most strongly to predicting the occurrence (presence/absence) of Carcharhinus amblyrhynchos (Figs. 4 & 5b). These were a steep negative relationship with human population density (RI = 19.9%), a somewhat variable relationship with in situ water temperature (RI = 17.4%), and a negative relationship with distance to deep water (RI = 12.8%). Sightings were most frequent where water temperatures were just below 28°C and decreased gradually with a smaller peak at 29°C. Overall model CVD was 0.207 with second order interactions between habitat structure and temperature as well as between depth and human population (Table 5). While the partial dependency plots show that both human population density and depth are correlated with distribution of C. amblyrhynchos (with higher occurrences in areas of low human population density and in deep water), the correlation with depth is partially dependent on local human population density. The effect of depth is weaker (or almost non-existent) where human population density is high and stronger (or only seems to matter) where there are fewer (to zero) people (Fig. 7). Similarly, the effect of local human population density is much reduced in shallower depths.
Depth is only influential in areas of low human population density and the effect of human population density is reduced in shallow waters.
Two relationships contributed most strongly to predicting the occurrence of Lutjanus bohar (Figs. 4 & 5c). A negative relationship with human population density was the strongest predictor (RI = 22.6%). This was followed by a relationship with benthic habitat structure (RI = 17.9%) for which Lutjanus bohar sightings were highest in areas classified as “Rock/Boulder”. Sightings decreased as water temperatures warmed from 27°C to 28°C and increased again once water temperatures reached 29°C (RI = 13.5%). Sightings also dropped steeply as distance to deep water increased (RI = 7.8%). Overall model CVD was 0.595 with second order interactions between wave energy and temperature as well as between depth and island quadrant (Table 5). L. bohar occurred most frequently in low temperature (<27.5°C) high wave energy waters (>250 kW/m). The effect of wave energy was stronger at these lower water temperatures and temperature appeared to have more of an effect at higher wave energies (Fig. 8). The interaction between depth and island quadrant suggests that the effect of depth was not universal across island quadrants, but this type of interaction (between categorical and continuous variables) is difficult to interpret.
The effect of temperature is magnified by wave energy while wave energy is primarily influential at temperatures below 28°C.
Three relationships contributed most strongly to predicting the occurrence of species of Macolor (Figs. 4 & 5d). An overall negative relationship with distance to deep water was the strongest predictor (RI = 29.5%). This was followed by a steep negative relationship with human population density (RI = 24.2%). Sightings of species of Macolor also decreased as water temperatures warmed from 27°C to 29°C and increased again once water temperatures exceeded 29°C (RI = 17.9%). Sightings of species of Macolor also increased with increases in observed benthic habitat complexity (RI = 7%). Overall model CVD was 0.309 and sample sizes were insufficient to model secondary interactions.
A negative relationship with human population density was the strongest predictor of sightings of Triaenodon obesus (RI = 30.8%) with a steep decline in presence between 0 and approximately 200 humans/km2 of reef and another drop once human population density reached 1000 individuals/km2 (Figs. 4 & 5e). A slightly positive relationship existed between sightings of Triaenodon obesus and depth (RI = 17%), with a spike in sightings at depths between 15 and 20 m. Slightly positive relationships also existed between sightings of this species and temperature (RI = 12.1%) and wave energy (RI = 11.9%). Overall model CVD was 0.341 with second order interactions between human population density and depth and wave energy (Table 5). In a pattern reminiscent of that seen in C. amblyrhynchos, the relationship between T. obesus and depth is partially dependent on local human population density. The effect of depth is weaker (or almost non-existent) where human population density is high and stronger (or only seems to matter) where there are fewer (to zero) people (Fig. 9). Similarly, the effect of local human population density is much reduced in shallower depths. Similarly, wave energy was only influential when human population density was low and the effect of human population density appeared to be reduced in areas with low wave energy (Fig. 10).
The effect of depth is influential only at the lowest human population densities and the effect of human population density is reduced in shallow areas.
The effect of wave energy is influential only at the lowest human population densities and the effect of human population density is magnified in higher wave energy areas.
A steep negative relationship with distance to deep water most strongly predicted sightings of Naso hexacanthus (RI = 23.6%), with fitted values dropping to near zero as distances to the 50 m isobath exceeded 200 m (Figs. 4 & 5f). A positive relationship also existed with depth (RI = 14.2%), and there was a steep negative relationship with human population density (RI = 11%). Overall model CVD was 0.228 with second order interactions between distance to deep water and benthic structure and cover (Table 5). The interaction between distance to deep water and benthic structure and cover (both categorical variables) suggests that the effect of distance to deep water was stronger in certain structure or cover classes as opposed to others, and that the relationship with cover and structure is partially dependent on proximity to deep water. Again however, this type of interaction (between categorical and continuous variables) is difficult to interpret.
Relationships with temperature and depth contributed most strongly to predicting the occurrence of Scarus rubroviolaceus (RI = 21.1% and 19.2%, respectively) (Figs. 4 & 5g The relationship with temperature was generally positive but was highly variable. The relationship with depth was also highly variable but sighting frequency was highest in depths near 10 m or less than 5 m. Highly variable relationships also existed with wave energy (RI = 11.7%) and distance to deep water (RI = 11.1%). There was not a strong relationship between the occurrence of this species and local human population density. Overall model CVD was 0.394 with second order interactions between wave energy and depth and sand cover (Table 5). The interaction between depth and wave energy is complicated. The relationship between S. rubroviolaceus and depth appears to be most pronounced in low wave energy environments (Fig. 11). As one might expect, the relationship between S. rubroviolaceus and wave energy is apparent only at depths shallower than 15 m and is strongest at depths shallower than 5 m. The effect of wave energy is also much reduced in areas of high sand cover. The effect of sand is highest at wave energies of between 100 and 200 kW/m (Fig. 12).
The effect of wave energy is influential only in depths shallower than 15 m. The effect of depth is somewhat magnified in lower wave energy areas.
The effect of wave energy was highest in areas with low sand cover and the effect of sand cover was greatest in areas were wave energy was between 100 and 200 kW/m.
Temperature, depth, distance to deep water, and human population density all contributed to predicting the occurrence of Caranx melampygus (RI = 18.4%, 13.4%, 13.2%, 12.7%, respectively; Figs. 4 & 5h). The relationship with temperature and depth were positive but highly variable, while the relationship with distance to deep water was negative. Sighting frequency declined steeply as human population density increased from zero. Overall model CVD was 0.300 with second order interactions between depth and percent cover of crustose coralline algae (CCA) and benthic structure (Table 5). The effect of percent cover of CCA was almost non-existent and depth shallower than 17 m and the effect of depth seems to have been reduced in areas with low CCA cover (Fig. 13). The interaction between depth and benthic structure (another categorical variable) suggests that the effect of depth was stronger in certain structure classes as opposed to others, and that the relationship with structure is partially dependent on depth.
The effect of CCA was greatest at depths greater than 15 m while the effect of depth was reduced in areas with lower CCA cover.
Depth most strongly contributed to predicting the occurrence of Cheilinus undulatus with a greater number of sightings at depths greater than 15 m (RI = 49.4%) (Figs. 4 & 5i). Sightings were also higher in areas classified as pavement and aggregate reef (RI = 10.7%). Human population density had a relative influence of 8.6%, with higher occurrences of Cheilinus undulatus in areas where human population density was between 0 and 750 individuals per km2 of reef. Overall model CVD was 0.131 and sample sizes were insufficient to model secondary interactions.
The islands of the Mariana Archipelago span a wide range of geographic, environmental, and anthropogenic gradients. The archipelago spans nearly ten degrees of latitude and ranges from relatively large, heavily populated, carbonate islands in the south to small, remote, unpopulated, volcanic islands in the north. While one might expect significant spatial structure in this type of data, a test for spatial autocorrelation indicates that our data are highly variable across space and that any effect of spatial autocorrelation is weak and likely overshadowed by the environmental variables used out model. Nevertheless, a number of the environmental and anthropogenic variables selected for analysis covaried, thus limiting our ability to draw definitive conclusions about the effect of any one variable to the exclusion of others. For example, the north-south gradient in human population density followed similar gradients in latitude, mean sea surface temperature, open ocean primary productivity and island size. Consequently, while we feel that human populations density is the most likely causative factor, and a substantial body of literature exists that would support such a conclusion , , –, we are nevertheless, not able to say with certainty that human population density is the causative factor to the exclusion of all others and our results should be used to indicate factors that appear to be important in shaping the spatial distribution of large-bodied reef fishes in this geographic area.
Measurements of in situ temperature factored highly in our analysis of relative influence and many studies have focused on the importance of temperature in the ontogeny of fishes as well as in structuring marine and aquatic communities. Francis  discusses the importance of sea surface temperature in determining the year class strength of New Zealand snapper while Worm et al.  show that patterns of diversity in top predators can be correlated with thermal fronts and patterns in the distribution of dissolved oxygen. In their 1980 study of habitat preference and fisheries oceanography, Magnuson et al.  showed that sea surface temperature was the best predictor of catch per unit effort (CPUE). These authors do, however, suggest that, as with any environmental correlation, the causal hypothesis regarding temperature needs laboratory verification as the finding that fish distributions following temperature gradients does not necessarily mean that temperature itself is the forcing function. Rather, it is possible that higher trophic-level fishes may be responding to the availability of prey species that are the ones responding to temperature. Furthermore, it is clear that fish assemblages are not responding directly to human population density, but are rather responding to a variety of direct and indirect factors (e.g. fishing, sedimentation, habitat degradation, etc.) related to human population density. It should also be noted that the coral reef system is enormously complex, with myriad interacting factors affecting species distributions through a variety of direct and indirect ways. Furthermore, the assemblages of large-bodied reef fishes we describe are rare, highly mobile, and patchily distributed. Hence, even our most complete model leaves the majority of deviance unexplained. That being said, the key findings of our study, such as the high relative importance of human population density and the effect of depth and distance to deep water remain important considerations for management of the marine resources of Guam and the Commonwealth of the Northern Mariana Islands and are consistent with research on other taxa from other locations , , , , . While the low relative influence of small-scale environmental factors (i.e. benthic cover and habitat heterogeneity) that have been previously identified as important in the distribution of small-bodied reef fishes , – is intuitive given their life history, to our knowledge this has seldom been demonstrated in the literature regarding this area. It stands to reason that small-scale factors are of prime importance to those species that interact most directly with the reef either for food or shelter . Chabanet et al.  found no relationship between habitat cover and the abundance of planktivores or carnivores at Reunion Island, and suggest that the relationship between the abundance of fish and coverage of living coral may be stronger in shallow water where fish remain in closer physical proximity to the substrate. However, as Levins  suggests, the perceived “grain size” or “resolution” of habitat depends on the body size of the individual animal. Hence, for wide-ranging large-bodied species small-scale differences in benthic cover are likely less important.
Community structure, relative biomass, and species occurrence differed substantially between the heavily populated southern islands and the more remote and unpopulated islands in the north. Overall biomass of large-bodied reef fish in the northern islands was nearly twice that found in the southern islands. Several taxa such as Carcharhinus amblyrhynchos and species of Macolor were abundant in the northern islands and nearly absent in the southern islands (Fig. 3). Other species such as Lutjanus bohar, Triaenodon obesus, Scarus rubroviolaceus, and Caranx melampygus were found both north and south, but biomass densities were much lower at the southern islands. At present, we do not know of a robust direct measure of fishing pressure in the Mariana Archipelago, so the evident relationship between many of the taxa in our study and local human population density cannot be directly attributed to the effects of fishing. While anthropogenic habitat destruction cannot be ruled out as a possible cause, we would expect anthropogenic habitat destruction to manifest itself through changes in biological benthic cover (e.g. shifts from coral to algae) and possibly changes in small-scale substrate complexity (e.g. sedimentation, coral death and erosion). As these habitat factors were of low relative influence in our study, it seems unlikely that anthropogenic habitat destruction is the basis for the high relative influence of human population density on the distribution of large-bodied reef fishes in this study. It should be noted that, with the exception of the two shark species, each of the chosen species do appear, in varying levels, in commercial and recreation catch data from Guam and the Commonwealth of the Northern Mariana Islands. While L. bohar is considered ciguatoxic in the Mariana Archipelago, and is therefore not commonly considered a “fishery target”, the species does appear—albeit in modest amounts—in both boat-based and shore-based creel survey data from Guam, as well as in commercial landings data, where it is classified under the the common name “Tagafi” and possibly as a component of the overall “snapper” grouping (unpublished data collected and processed by Guam Division of Aquatic Resources and provided to the authors via the WPacFIN program ).
Interestingly, overall biomass density of Cheilinus undulatus, an IUCN Red List species, was higher in the southern islands than in the north, with the highest densities found around the islands of Rota and Sarigan, which have moderate to low human population densities. Initially we thought this might be due to a higher number of smaller individuals in the southern islands compared with a lower number of larger individuals in the north. However, this does not appear to be the case, as few individuals of any size were sighted in the northern portion of the archipelago. Of the environmental factors evaluated in the present study, depth had the highest relative influence with higher occurrence of C. undulatus at deeper depths. However, the waters around the southern islands tend to be shallower than those in the north, so this does not explain our findings. It is possible that C. undulatus distribution reflects the availability of certain habitats or conditions conducive to this species at Rota and Sarigan that we failed to measure, or the lack of the same in the northern islands. Cheilinus undulatus is an IUCN Red List species and is, therefore, of high management importance. However, it should be noted that C. undulatus was observed on only 49 of our surveys compared to a minimum of 100 survey observations for each of the other taxonomic groups. Hence, our results may be an artifact of low sample size, may not be representative of true distribution patterns, and should be interpreted with caution. Further, targeted research on this low-density species is needed to fully resolve the factors affecting its distribution.
All in situ surveys likely influence their study subjects, causing fishes to either aggregate around or flee from the observers or instrument platform . We feel that the towed-diver methods used in this study are not as prone to bias as other diver-based techniques . However, it should be noted that the relative difference between remote and human-inhabited islands could be exaggerated if fishes aggregate around divers in remote areas and flee from divers in areas frequented by people. That being said, our findings are consistent with the preliminary findings of Schroeder et al. , statements such as those by the Western Pacific Regional Fishery Management Council  suggesting that many large bodied species “became rare on shallow reefs [around Guam] due to heavy fishing …”, and the substantial literature linking anthropogenic impacts to decreases in fish populations , , , , , , –, –. Fish and shellfish dominate middens dated to the period of early human habitation in the Mariana Islands and those from early settlement sites contain the remains of a wide range of fishes from coastal reefs, lagoons, and deep water (Green 1997). During this time, fishing appears to have been concentrated on coral reef and lagoon species  and stable isotope data indicate that marine foods constituted nearly 40% of the prehistoric diet . Shortcomings in fishery statistics make it virtually impossible to assess the total harvest of contemporary coral reef fisheries in the Mariana Archipelago . While most fisheries are limited to nearshore areas off Saipan, Rota, and Tinian, the accuracy of reporting is suspect in many areas and virtually no information is available for the inshore subsistence and recreational fisheries. At least six of the northern islands have been commercially fished to some extent , and poaching by foreign vessels has been documented . While poaching is difficult to quantify, it is a legitimate concern as poachers tend to target high-value, rare, or otherwise heavily fished resources  – qualities that describe many large-bodied reef fish populations.
The evidence that early human populations had at least some impact on the local reef environment and that contemporary anthropogenic impacts may be greatly underestimated should be to be taken into account when discussing relationships between reef fishes and their habitat, as it is likely that contemporary relationships that include human influences may not necessarily be representative of healthy let alone “pristine” systems. Nevertheless, contemporary fish-habitat relationships can reveal the importance of certain physical, oceanographic, and biological factors in structuring the distribution of large-bodied reef fishes. As we discuss below, these relationships between fishes and their environment can inform discussions of important or “essential” fish habitats and their roles in ecosystem-based management.
Fish - Habitat Relationships
The Boosted Regression Tree analysis, based on species presence/absence, was able to assess the relative influence of each environmental factor adjusting for the impacts of each of the other variables. Human population density was still the most influential factor, but others appear to play a role (Figs. 4 & 5). In certain cases, such as with the two shark species Carcharhinus amblyrhynchos and Triaenodon obesus, a look at prominent pairwise interactions among variables shows that variables including depth and wave energy are only influential in areas with the lowest human population densities. While the absolute influence of each variable was relatively low in this highly variable data set, oceanographic factors such as depth, temperature, and proximity to deep water (quantified as distance to the 50-m depth contour) consistently the most influential of the factors we analyzed. In almost all cases, species occurrence increased in deeper waters and in areas of higher temperature. The effects of temperature and depth were synergistic with respect to total large-bodied reef fish biomass, with the effect of each being magnified by the other. Depth was particularly important for Cheilinus undulatus, which was only observed on surveys in greater than 15 m. Caranx melampygus and Scarus rubroviolaceus displayed an inverse relationship with respect to depth, which highlights their differing niches. Carnivorous C. melampygus were primarily found in deeper waters (>15 m) while herbivorous S. rubroviolaceus were primarily found in the shallower areas (<15 m) more conducive to algae growth. Proximity to deep water was particularly important for Carcharhinus amblyrhynchos, species of Macolor, Caranx melampygus and Naso hexacanthus, which are all found near escarpments or walls. These findings are consistent with those of Friedlander et al.  who found depth and proximity to the pelagic environment to predictably alter the structure of reef fish assemblages at Kingman Reef in the northern Line Islands. Specifically, these authors found that both abundance and biomass increased with proximity to the pelagic environment and with increasing depth on the forereef. Our findings are also consistent with those of Wetherbee et al.  and Papastamatiou et al.  who found that CPUE or the relative number of grey reef sharks (Carcharhinus amblyrhynchos) caught in Hawai'i generally increased with depth. Friedlander et al.  also found that apex predators, and the planktivorous snappers, on which they prey, were more abundant on the deeper forereef and reef walls, presumably because currents consistently deliver higher concentrations of plankton to these areas , . These findings are consistent with the relationship we describe regarding the planktivorous species of Macolor and Naso hexacanthus. It is possible that the relationship between the apex predators (Carcharhinus amblyrhynchos, Caranx melampygus) and proximity to deep water is a secondary relationship related to the distribution of their prey species. This conclusion is consistent with Wetherbee et al.  and Papastamatiou et al. , who found that teleost fishes (e.g., holocentrids, monacanthids, and acanthurids) dominated the gut contents of Carcharhinus amblyrhynchos in the Hawaiian Islands.
In situ temperature also factored highly in the distribution of large-bodied reef fish, with overall biomass and the occurrence of many taxa positively correlated with temperature. In certain taxa including Carcharhinus amblyrhynchos and Lutjanus bohar, temperature showed high relative influence, but the relationship did not have a clear linear trend. In the case of L. bohar, there was an interaction between temperature and wave energy in which the effect of temperature was magnified in areas of high wave energy. The thermal environment of coral reefs is highly stable and thermal gradients can play a large role in life history and distribution both on and off coral reefs –; hence it is not surprising that fish react to temperature and that the relationship can be quite complex. Meyer et al.  found that short-term movements of Aprion virescens at Pearl and Hermes Reef in the NWHI were oriented to tidal cycles, with fish moving along the barrier reef on the flooding tide and returning on the ebbing tide, and tidal rhythmicity has been previously documented in acoustic monitoring studies of other fishes. We did not account for tidal cycle in our analysis, and it is possible that the importance of temperature is magnified by a correlation with tidal cycling. There may also be a relationship between temperature and primary productivity that would follow the north-south human population gradient. However, unlike remotely sensed mean sea surface temperature, in situ temperature measurements did not clearly correlate with other environmental gradients measured in this study (max ρ = 0.41 with % sand cover) and the difference in mean in situ temperature measurements between remote and populated sections of the archipelago (the strongest overall pattern) was only 0.4°C.
Topographic complexity, benthic habitat structure, and benthic cover had relatively little influence in our analysis of large-bodied reef fish. In contrast, these factors have a strong influence on the distribution and relative abundance of smaller reef fishes , , , , , , , . It is likely that our estimates of topographic complexity, which are based on a six-point scale visually estimated by divers, are more subjective or variable than quantitative measures such as multibeam SONAR or LIDAR. These latter types of data might provide a better means for assessing this relationship, but, unfortunately, they are presently unavailable for these areas. Organisms interact with their environment at a range of scales, and the relative heterogeneity of the environment depends on the size of the individual . It is possible that the resolution at which we measured these variables is not ideal for the large-bodied portion of the reef fish assemblage.
Benthic habitat structure appeared to be important for Lutjanus bohar and Cheilinus undulates, with higher occurrences of these species in areas characterized as “Rock/Boulder” and “Pavement” or “Aggregate Reef,” respectively. While a majority of species showed a positive relationship with benthic complexity, the relative influence of complexity was not high compared to the other measured variables. This may be because many large-bodied reef fishes are not as closely associated with small-scale benthic structures (but see Lindberg et al. , tend to have wider ranges, and interact with their environment in a more “coarse-grained” manner (sensu Levins ). It is also possible that we failed to measure habitat characteristics in sufficient detail or at the scales important to this portion of the assemblage. As noted above, the ability to incorporate high-resolution bathymetric information for large areas, such as that provided by multibeam SONAR or LIDAR technologies, would likely allow for a more detailed investigation of these relationships.
Fisheries management in coral reef ecosystems is moving towards ecosystem-based approaches with a priority placed on the identification of “essential fish habitat” – ‘those waters and substrate necessary to fish for spawning, feeding, breeding, and growth to maturity’ , . However, logistical constraints have limited much of the previous research to small-bodied coral reef fishes and often to areas adjacent to human populations , –. As many fisheries tend to preferentially target large-bodied species and large individuals , , , determination of the relative importance of environmental factors for this segment of the assemblage is essential to improving fisheries and ecosystem-based management. Our results show that proximity to areas of high human population had the highest influence relative to the other environmental factors we measured and likely influences large-bodied reef fish assemblages in the Mariana Islands. Whether this is a result of fishing or other anthropogenic impacts for which we do not yet have accurate data is unknown, but extraction is commonly assumed to be the most important impact associated with human population centers , , , .
While the negative relationship with human population was the most important predictor variable in this study, the human population gradient was correlated with latitudinal and temperature gradients. Large-scale oceanographic factors such as depth, temperature, and proximity to deep water were also important. Shallow-water wave stress may be significant locally, but this is difficult to quantify accurately without bathymetry data. Large-scale habitat structure was also shown to be important for certain species. Conveniently, data on many of these factors may be easily obtained at large scales through remote sensing, allowing managers and researchers to develop predictive models delineating areas conducive to large-bodied reef fishes using methods similar to those outlined by Pittman et al. , De'ath  and Elith et al. . Such information can be used in ecosystem-based spatial planning and management. For example, even for cases in which visual or other population survey data are lacking, areas likely capable of supporting species of particular concern can be identified as a areas for further research or consideration as marine protected areas. The reader will note that, as with other studies focusing on low density and patchily distributed assemblages, our models explain only a small portion of the overall deviance. There are likely many factors that contribute to the spatial and temporal distribution of individual species. Our aim has been to evaluate the relative influence of a specific suite of environmental variables that have been identified as important in previous studies. By gaining a better understanding of the relationships between large-bodied reef fishes and their environment, especially with those environmental variables that showed high relative influence, management agencies can better conserve large-bodied reef fish populations. While many of the environmental variables identified as important in this study cannot be directly manipulated, such as proximity to human population or distance to deep water, our results can highlight the importance of certain areas, such as remote and uninhabited islands with steep walls, that may serve as important refuges for these fishes and are therefore worthy of protection and monitoring. With appropriate caution, model predictions resulting from this kind of research can be used in an adaptive management framework to adjust the boundaries of existing marine protected areas that are not meeting their management objectives and to target further detailed research.
This work is part of an interdisciplinary effort by the NOAA Pacific Islands Fisheries Science Center, Coral Reef Ecosystem Division (PIFSC CRED) to assess, understand, and monitor coral-reef ecosystems in the U.S. Pacific. We thank the many CRED towed divers who, over the past 10 years, have been instrumental in collecting these data. Special thanks to F. Parrish, E. DeMartini and R. Boland of the PIFSC who initially developed the CRED towed-diver method and to the CRED benthic team who have worked tirelessly to collate the benthic towed-diver data set. We would also like to thank the officers and crews of the NOAA Ships Townsend Cromwell, Hi'ialakai and Oscar Elton Sette for logistic support and field assistance. Permission to work in the Mariana Archipelago was granted by the Commonwealth of the Northern Mariana Islands (CNMI) Division of Fish and Wildlife, Coastal Resources Management Office, Division of Environmental Quality and the Guam Division of Aquatic and Wildlife Resources. The use of trade, firm, or corporation names in this publication is for the convenience of the reader and does not constitute an official endorsement or approval of any product or service to the exclusion of others that may be suitable.
Conceived and designed the experiments: BLR IDW GJW. Performed the experiments: BLR GJW. Analyzed the data: BLR IDW OJV GJW. Contributed reagents/materials/analysis tools: BLR IDW OJV GJW. Wrote the paper: BLR OJV.
- 1. Long RA, Muir JD, Rachlow JL, Kie J (2009) A comparison of two modeling approaches for evaluating wildlife-habitat relationships. Journal Of Wildlife Management 73: 294–302.
- 2. Agardy T, Notarbartolo di Sciara G, Christie P (2011) Mind the gap: Addressing the shortcomings of marine protected areas through large scale marine spatial planning. Marine Policy 35: 226–232.
- 3. Friedlander AM (2001) Essential fish habitat and the effective design of marine reserves: application for marine ornamental fishes. Aquarium Sciences and Conservation 3: 135–150.
- 4. Jones RS (1968) Ecological relationships in Hawaiian and Johnston Island Acanthuridae (Surgeonfishes). Micronesica 4: 309–361.
- 5. Hixon MA, Beets JP (1993) Predation, prey refuges, and the structure of coral-reef fish assemblages. Ecological Monographs 63: 77–101.
- 6. Friedlander AM, Parrish JD (1998) Habitat characteristics affecting fish assemblages on a Hawaiian coral reef. Journal of Experimental Marine Biology and Ecology 224: 1–30.
- 7. Lange M (2003) What is essential in fish habitat? Environmental Biology of Fishes 66: 99–101.
- 8. Friedlander AM, Brown EK, Jokiel PL, Smith WR, Rodgers KS (2003) Effects of habitat, wave exposure, and marine protected area status on coral reef fish assemblages in the Hawaiian archipelago. Coral Reefs 22: 291–305.
- 9. Pittman SJ, McAlpine CA, Pittman KM (2004) Linking fish and prawns to their environment: a hierarchical landscape approach. Marine Ecology Progress Series 283: 233–254.
- 10. Chittaro PM (2004) Fish-habitat associations across multiple spatial scales. Coral Reefs 23: 235–244.
- 11. Friedlander AM, Brown EK, Monaco MA, Clark A (2005) Fish habitat utilization patterns and evaluation of the efficacy of marine protected areas in Hawaii: integration of NOAA digital benthic habitat mapping and coral reef ecological studies. NOAA Technical Memorandum NOS NCCOS 23: 210.
- 12. Pittman SJ, Christensen JD, Caldow C, Menza C, Monaco MA (2007) Predictive mapping of fish species richness across shallow-water seascapes in the Caribbean. Ecological Modeling 204: 9–21.
- 13. Bigelow KA, Boggs CH, HE XI (1999) Environmental effects on swordfish and blue shark catch rates in the US North Pacific longline fishery. Fisheries Oceanography 8: 178–198.
- 14. Hopkins TE, Cech JJ (2003) The Influence of Environmental Variables on the Distribution and Abundance of Three Elasmobranchs in Tomales Bay, California. Environmental Biology of Fishes 66: 279–291.
- 15. Simpfendorfer C, Freitas G, Wiley T, Heupel M (2005) Distribution and habitat partitioning of immature bull sharks (Carcharhinus leucas) in a Southwest Florida estuary. Estuaries and Coasts 28: 78–85.
- 16. Heithaus MR, Delius BK, Wirsing AJ, Dunphy-Daly MM (2009) Physical factors influencing the distribution of a top predator in a subtropical oligotrophic estuary. Limnology and Oceanography 54: 472–482.
- 17. Lindberg WJ, Frazer TK, Portier KM, Vose F, Loftin J, et al. (2006) Density-dependent habitat selection and performance by a large mobile reef fish. Ecological Applications 16: 731–746.
- 18. Meyer CG, Holland KN, Papastamatiou YP (2007) Seasonal and diel movements of giant trevally Caranx ignobilis at remote Hawaiian atolls: implications for the design of Marine Protected Areas. Marine Ecology Progress Series 333: 13–25.
- 19. Meyer CG, Papastamatiou YP, Holland KN (2007) Seasonal, diel, and tidal movements of green jobfish (Aprion virescens, Lutjanidae) at remote Hawaiian atolls: implications for marine protected area design. Marine Biology 151: 2133–2143.
- 20. McKibben JN, Nelson DR (1986) Patterns of movement and grouping of gray reef sharks, Carcharhinus amblyrhynchos, at Enewetak, Marshall Islands. Bulletin of Marine Science 38: 89–110.
- 21. Holland KN, Lowe CG, Wetherbee BM (1996) Movements and dispersal patterns of blue trevally (Caranx melampygus) in a fisheries conservation zone. Fisheries Science 25: 279–292.
- 22. Russ GR (1984) Distribution and abundance of herbivorous grazing fishes in the central Great Barrier Reef. I. Levels of variability across the entire continental shelf. Marine Ecology Progress Series 20: 23–34.
- 23. Newman SJ, Williams DM (1996) Variation in reef associated assemblages of the Lutjanidae and Lethrinidae at different distances offshore in the central Great Barrier Reef. Environmental Biology of Fishes 46: 123–138.
- 24. Beger M, Possingham HP (2008) Enrironmental factors that influence the distribution of coral reef fishes: modeling occurrence data for broad-scale conservation and management. Marine Ecology Progress Series 361: 1–13.
- 25. Caselle JE, Warner RR (1996) Variability in Recruitment of Coral Reef Fishes: The Importance of Habitat at Two Spatial Scales. Ecology 77: 2488–2504.
Western Pacific Regional Fishery Management Council (2009) 231 p. Fishery Ecosystem Plan for the Mariana Archipelago.
- 27. Russ GR, Alcala AC (1989) Effects of intense fishing pressure on an assemblage of coral-reef fishes. Marine Ecology Progress Series 56: 13–27.
- 28. Schroeder RE, Trianni MS, Moots KA, Laughlin JL, Zgliczynski BJ, et al. (2003) Status of target species on coral reefs of the Marianas Archipelago. Proceedings of the 10th International Coral Reef Symposium 1016–1027.
- 29. Birkeland C, Dayton PK (2005) The importance in fishery management of leaving the big ones. Trends in Ecology and Evolution 20: 356–358.
- 30. Coleman FC, Koenig CC, Huntsman GR, Musick JA, Eklund AM, et al. (2000) Long-lived reef fishes: The grouper-snapper complex. Fisheries 25: 14–21.
- 31. Sudekum AE, Parrish JD, Radtke RL, Ralson S (1991) Life History and Ecology of Large Jacks in Undisturbed, Shallow, Oceanic Communities. Fishery Bulletin 89: 493–513.
- 32. DeMartini EE, Friedlander AM, Sandin SA, Sala E (2008) Differences in fish-assemblage structure between fished and unfished atolls in the northern Line Islands, central Pacific. Marine Ecology Progress Series 365: 199–215.
- 33. Francis RC, Hixon MA, Clarke ME, Murawski SA, Ralson S (2007) Perspective: Fisheries management. Fisheries 32: 217–233.
- 34. Friedlander AM, DeMartini EE (2002) Contrasts in density, size, and biomass of reef fishes between the northwestern and the main Hawaiian islands: the effects of fishing down apex predators. Marine Ecology Progress Series 230: 253–264.
- 35. Bellwood DR, Choat JH (1990) A functional analysis of grazing in parrotfishes (family Scaridae): the ecological implications. Environmental Biology of Fishes 28: 189–214.
- 36. Bruggemann H, van Kessel AM, van Rooij JM, Breeman AM (1996) Bioerosion and sediment ingestion by the Caribbean parrotfish Scarus vetula and Sparisoma viride: implications of fish size, feeding mode and habitat use. Marine Ecology Progress Series 134: 59–71.
Hixon MA (1997) Effects of reef fishes on corals and algae. In: Birkeland C, editor. Life and Death of Coral Reefs. New York: Chapman & Hall. pp. 230–248.
- 38. Jackson JBC, Kirby MX, Berger WH, Bjorndal KA, Botsford LW, et al. (2001) Historical overfishing and the recent collapse of coastal ecosystems. Science 293: 629–638.
Sandin SA, Walsh SM, Jackson JBC (2010) Prey release, trophic cascades, and phase shifts in tropical nearshore ecosystems. In: Terborgh J, Estes JA, editors. Trophic cascades: predators, prey, and the changing dynamics of nature. Washington DC: Island Press. pp. 71–90.
- 40. Jennings S, Reynolds JD, Mills SC (1998) Life history correlates of responses to fisheries exploitation. Proceedings of the Royal Society B: Biological Sciences 265: 333–339.
- 41. Russ GR, Alcala AC (1998) Natural fishing experiments in marine reserves 1983–1993: roles of life history and fishing intensity in family responses. Coral Reefs 17: 399–416.
- 42. Jennings S, Greenstreet PR, Reynolds JD (1999) Structural change in an exploited fish community: a consequence of differential fishing effects on species with contrasting life histories. Journal of Animal Ecology 68: 617–627.
Flores T (2006) Offshore Fisheries Program Annual Program Report. Government of Guam Department of Agriculture Annual Report.
Flores T (2006) Inshore Fisheries Participation, Effort, and Harvest Surveys Program Annual Program Report FY 2006. Government of Guam Department of Agriculture Annual Report.
Burdick D, Brown V, Asher J, Caballes C, Gawel M, et al. (2006) 76 p. Status of the Coral Reef Ecosystems of Guam.
- 46. Green A (1997) An assessment of the status of the coral reef resources, and their patterns of use, in the U.S. Pacific Islands. Final report prepared for the Western Pacific Regional Fishery Management Council 278:
- 47. Ault JS, Bohnsack JA, Meester GA (1998) A retrospective (1979–1996) multispecies assessment of coral reef fish stocks in the Florida Keys. Fishery Bulletin 96: 395–414.
- 48. Pauly D, Christensen V, Dalsgaard J, Froese R Jr, FT (1998) Fishing down marine food webs. Science 279: 860–863.
United States Congress (1996) Magnuson-Stevens Fishery Conservation and Management Act. Public Law 94-265.
- 50. Asakura A, Ohba T, Miyano S, Furuki T, Kurozumi T, et al. (1994) Outline of the biological expedition to the Northern Mariana Islands, Micronesia. Natural History Research Special Issue 1: 1–11.
- 51. Rohmann SO, Hayes JJ, Newhall RC, Monaco ME, Grigg RW (2005) The area of potential shallow-water tropical and subtropical coral ecosystems in the United States. Coral Reefs 24: 370–383.
- 52. Rainbird P (1994) Prehistory in the northwest tropical Pacific: The Caroline, Mariana, and Marshall Islands. Journal of World Prehistory 8: 293–349.
- 53. Richards BL, Williams ID, Nadon MO, Zgliczynski BJ (2011) A towed-diver survey method for mesoscale fishery-independent assessment of large-bodied reef fishes. Bulletin of Marine Science 87: 55–74.
- 54. Kenyon JC, Brainard RE, Hoeke RK, Parrish FA, Wilkinson CB (2006) Towed-diver surveys, a method for mesoscale spatial assessment of benthic reef habitat: a case study at Midway Atoll in the Hawaiian Archipelago. Coastal Management 34: 339–349.
Froese R, Pauly D (2009) FishBase. Available: www.fishbase.org via the Internet.
- 56. Kulbicki M, Guillemot N, Amand M (2005) A general approach to length-weight relationships for New Caledonian lagoon fishes. Cybium 29: 235–252.
- 57. NOAA National Centers for Coastal Ocean Science [NCCOS] (2005) Shallow-Water Benthic Habitats of American Samoa, Guam, and the Commonwealth of the Northern Mariana Islands (CD-ROM). NOAA Technical Memorandum NOS NCCOS 8:
Pacific Islands Benthic Habitat Mapping Center (2010) Commonwealth of Northern Mariana Islands (CNMI) and Guam. http://wwwsoesthawaiiedu/pibhmc/pibhmc_cnmihtm via the Internet.
- 59. Kilpatrick KA, Podestá GP, Evans RH (2001) Overview of the NOAA/NASA Pathfinder algorithm for Sea Surface Temperature and associated Matchup Database. Journal of Geophysical Research 106: 9179–9198.
Clarke KR, Gorley RN (2006) PRIMER v6: User Manual/Tutorial. vv6113. PRIMER-E.
- 61. Elith J, Leathwick JR, H T (2008) A working guide to boosted regression trees. Journal of Animal Ecology 77: 802–813.
R Development Core Team (2009) R: A Language and Environment for Statistical Computing. v261. R Foundation for Statistical Computing.
- 63. Plotkin JB, Muller-Landau HC (2002) Sampling the species composition of a landscape. Ecology 83: 3344–3356.
- 64. Valesini FJ, Potter IC, Clarke KR (2004) To what extent are the fish compositions at nearshore sites along a heterogeneous coast related to habitat type? Estuarine, Coastal and Shelf Science 60: 737–754.
- 65. Clarke KR, Chapman MG, Somerfield PJ, Needham HR (2006) Dispersion-based weighting of species counts in assemblage analyses. Marine Ecology Progress Series 320: 11–27.
- 66. Williams GJ, Cameron MJ, Turner JR, Ford RB (2008) Quantitative characterization of reef fish diversity among nearshore habitats in a northeastern New Zealand marine reserve. New Zealand Journal of Marine and Freshwater Research 42: 33–46.
- 67. Clarke KR, Somerfield PJ, Gorley RN (2008) Testing of null hypotheses in exploratory community analyses: similarity profiles and biota-environment linkage. Journal of Experimental Marine Biology and Ecology 366: 56–69.
- 68. Clarke KR, Somerfield PJ, Chapman MG (2006) On resemblance measures for ecological studies, including taxonomic dissimilarities and a zero-adjusted Bray–Curtis coefficient for denuded assemblages. Journal of Experimental Marine Biology and Ecology 330: 55–80.
- 69. Clarke KR (1993) Non-parametric multivariate analyses of changes in community structure. Austral Ecology 18: 117–143.
- 70. Clarke KR, Ainsworth M (1993) A method of linking multivariate community structure to environmental variables. Marine Ecology Progress Series 92: 205–219.
- 71. Ridgeway G Generalized boosted regression models. Documentation on the R package “gbm” v15–7.
- 72. De'ath G (2007) Boosted trees for ecological modeling and prediction. Ecology 88: 243–251.
- 73. Cappo M, De'ath G, Boyle S, Aumend J, Olbrich R, et al. (2005) Development of a robust classifier of freshwater residence in barramundi (Lates calcarifer) life histories using elemental ratios in scales and boosted regression trees. Marine and Freshwater Research 56: 713–723.
- 74. Leathwick JR, Elith J, Francis MP, Hastie T, Taylor P (2006) Variation in demersal fish species richness in the oceans surrounding New Zealand: an analysis using boosted regression trees. Marine Ecology Progress Series 321: 267–281.
- 75. Williams GJ, Aeby GS, Cowie ROM, Davy SK (2010) Predictive Modeling of Coral Disease Distribution within a Reef System. PLoS ONE 5: e9264.
- 76. Myers RA, Baum JK, Shepherd TD, Powers SP, Peterson CH (2007) Cascading Effects of the Loss of Apex Predatory Sharks from a Coastal Ocean. Science 315: 1846–1850.
- 77. Bellwood DR (1995) Direct estimate of bioerosion by two parrotfish species, Chlorurus gibbus and C. sordidus, on the Great Barrier Reef, Australia. Marine Biology 121: 419–429.
- 78. Maragos JE (1993) Impact of coastal construction on coral reefs in the U.S.-affiliated Pacific Islands. Coastal Management 21: 235–269.
Roberts CM (2007) The Unnatural History of the Sea. Island Press. Washington, D.C..
- 80. Williams ID, Walsh WJ, Schroeder RE, Friedlander AM, Richards BL, et al. (2008) Assessing the importance of fishing impacts on Hawaiian coral reef fish assemblages along regional-scale human population gradients. Environmental Conservation 35: 261–272.
- 81. Sandin SA, Smith JE, DeMartini EE, Dinsdale EA, Donner SD, et al. (2008) Baselines and degradation of coral reefs in the Northern Line Islands. PLoS ONE 3: e1548.
- 82. Stallings CD (2009) Fishery-Independent Data Reveal Negative Effect of Human Population Density on Caribbean Predatory Fish Communities. PLoS ONE 4: e5333.
- 83. Williams ID, Richards BL, Sandin SA, Baum JK, Schroeder RE, et al. (2011) Differences in Reef Fish Assemblages between Populated and Remote Reefs Spanning Multiple Archipelagos Across the Central and Western Pacific. Journal of Marine Biology 14:
- 84. Mora C, Aburto-Oropeza O, Ayala B, Arturo , Ayotte PM, Banks S, et al. (2011) Global Human Footprint on the Linkage between Biodiversity and Ecosystem Functioning in Reef Fishes. PLoS Biology 9: e1000606.
- 85. Francis MP (1993) Does water temperature determine year class strength in New Zealand snapper (Pagrus auratus, Sparidae)? Fisheries Oceanography 2: 65–72.
- 86. Worm B, Sandow M, Oschlies A, Lotze HK, Myers RA (2005) Global Patterns of Predator Diversity in the Open Oceans. Science 309: 1365–1369.
Magnuson JJ, Brandt SB, Stewart DJ (1980) Habitat Preference and Fisheries Oceanography. In: Bardach JE, Magnuson JJ, May RC, Reinhart JM, editors. Fish behavior and its use in the capture and culture of fishes. Manilia: International center for living and aquatic resources management. pp. 371–382.
- 88. Friedlander AM, Sandin SA, DeMartini EE, Sala E (2010) Spatial patterns of the structure of reef fish assemblages at a pristine atoll in the central Pacific. Marine Ecology Progress Series 410: 219–231.
- 89. Luckhurst BE, Luckhurst K (1978) Analysis of the influence of substrate variables on coral reef fish communities. Marine Biology 49: 317–323.
- 90. Chabanet P, Ralambondrainy H, Amanieu M, Faure G, Galzin R (1997) Relationships between coral reef substrata and fish. Coral Reefs 16: 93–102.
- 91. Friedlander AM, Brown EK, Monaco ME (2007) Defining reef fish habitat utilization patterns in Hawaii: comparisons between marine protected areas and areas open to fishing. Marine Ecology Progress Series 351: 221–233.
- 92. Sale PF (1972) Effect of Cover on Agonistic Behavior of a Reef Fish, A Possible Spacing Mechanism. Ecology 53: 753–758.
Levins R (1968) Evolution in Changing Environments: Some Theoretical Explorations. Princeton, New Jersey: Princeton University Press. 120 p.
WPacFIN (2011) Western Pacific Fisheries Information Network. Available: http://www.pifsc.noaa.gov/wpacfin/ via the Internet.
- 95. Biro PA, Dingemanse NJ (2009) Sampling bias resulting from animal personality. Trends in Ecology and Evolution 24: 66–67.
- 96. Koslow JA, Hanley F, Wicklund R (1988) Effects of fishing on reef fish communities at Pedro Bank and Port Royal Cays, Jamaica. Marine Ecology Progress Series 43: 201–212.
- 97. Hughes TP (1994) Catastrophes, phase shifts, and large-scale degradation of a Caribbean coral reef. Science 265: 1547–1551.
- 98. Sheppard C (1995) The Shifting Baseline Syndrome. Marine Pollution Bulletin 30: 766–767.
- 99. Dayton PK, Thrush SF, Agardy MT, Hofman RJ (1995) Environmental effects of marine fishing. Aquatic Conservation: Marine and Freshwater Ecosystems 5: 205–232.
- 100. Myers RA, Hutchings JA, Barrowman NJ (1997) Why do fish stocks collapse? The example of cod in Atlantic Canada. Ecological Applications 7: 91–106.
- 101. Jackson JBC (1997) Reefs since Columbus. Coral Reefs 16: S23–S32.
- 102. Jackson JBC (2001) What was natural in the coastal oceans? Proceedings of the National Academy of Sciences of the United States of America 98: 5411–5418.
- 103. Bohnsack JA (2003) Shifting Baselines, marine reserves, and Leopold's biotic ethic. Gulf and Caribbean Research 14: 1–7.
- 104. Bellwood DR, Hughes TP, Nyström M (2004) Confronting the coral reef crisis. Nature 429: 827–833.
- 105. Jennings S, Blanchard JL (2004) Fish abundance with no fishing: predictions based on macroecological theory. Journal of Animal Ecology 73: 632–642.
- 106. Halpern BS, Walbridge S, Selkoe KA, Kappel CV, Micheli F, et al. (2008) A Global Map of Human Impact on Marine Ecosystems. Science 319: 948–952.
Amesbury J, Hunter-Anderson R, Wells E (1989) Native fishing rights and limited entry in the CNMI. Western Pacific Regional Fishery Management Council.
- 108. Pate FD, Craib JL, Heathcote GM (2001) Stable isotopic analysis of prehistoric human diet in the Mariana Islands, western Pacific. Australian Archaeology 52: 1–4.
- 109. Wetherbee BM, Crow GL, Lowe CG (1997) Distribution, reproduction and diet of the gray reef shark Carcharhinus amblyrhynchos in Hawaii. Marine Ecology Progress Series 151: 181–189.
- 110. Papastamatiou YP, Wetherbee BM, Lowe CG, Crow GL (2006) Distribution and diet of four species of carcharhinid shark in the Hawaiian Islands: evidence for resource partitioning and competitive exclusion. Marine Ecology Progress Series 320: 239–251.
- 111. Hobson ES, Chess JR (1978) Trophic relationships among fishes and plankton in the lagoon at Enewetok atoll, Marshall Islands. Fisheries Bulletin 76: 133–153.
- 112. Thresher RE, Colin PL (1986) Trophic structure, diversity and abundance of fishes of the deep reef (30–300 m) at Enewetak, Marshall Islands. Bulletin of Marine Science 38: 410–426.
- 113. Meekan MG, Carleton JH, McKinnon AD, Flynn K, Furnas M (2003) What determines the growth of tropical reef fish larvae in the plankton: food or temperature? Marine Ecology Progress Series 256: 193–204.
- 114. Humston R, Ault JS, Larkin MF, Luo J (2005) Movements and site fidelity of the bonefish Albula vulpes in the northern Florida Keys determined by acoustic telemetry. Marine Ecology Progress Series 291: 237–248.
- 115. Sponaugle S, Grorud-Colvert K, Pinkard D (2006) Temperature-mediated variation in early life history traits and recruitment success of the coral reef fish Thalassoma bifasciatum in the Florida Keys. Marine Ecology Progress Series 308: 1–15.
- 116. Song L, Zhou J, Zhou Y, Nishida T, Jiang W, et al. (2009) Environmental preferences of bigeye tuna, Thunnus obesus, in the Indian Ocean: an application to a longline fishery. Environmental Biology of Fishes 85: 153–171.
- 117. Carpenter KE, Miclat RI, Albaladejo VD, Corpus VT (1981) The influence of substrate structure on the local abundance and diversity of Philippine reef fishes. Proceedings of the 4th International Coral Reef Symposium 2: 497–502.
- 118. DeMartini EE, Anderson TW (2007) Habitat associations and aggregations of recruit fishes on Hawaiian coral reefs. Bulletin of Marine Science 81: 139–152.
- 119. Kemp JM (1998) Zoogeography of the coral reef fishes of the Socotra Archipelago. Journal of Biogeography 25: 919–933.
- 120. Nakamura Y, Sano M (2004) Overlaps in habitat use of fishes between a seagrass bed and adjacent coral and sand areas at Amitori Bay, Iriomote Island, Japan: importance of the seagrass bed as juvenile habitat. Fisheries Science 70: 788–803.
- 121. Pittman SJ, Caldow C, Hile SD, Monaco ME (2007) Using seascape types to explain the spatial patterns of fish in the mangroves of SW Puerto Rico. Marine Ecology Progress Series 348: 273–284.
Jennings S, Kaiser MJ, Reynolds JD (2001) Marine fisheries ecology. Oxford, United Kingdom: Blackwell Science.
- 123. Reynolds JD, Dulvy NK, Goodwin NB, Hutchings JA (2005) Review. Biology of extinction risk in marine fishes. Proceedings of the Royal Society B: Biological Sciences 272: 2337–2344.
- 124. Grigg RW (1994) Effects of sewage discharge, fishing pressure and habitat complexity on coral reef ecosystems and reef fishes in Hawaii. Marine Ecology Progress Series 103: 25–34.