In recent decades, large pelagic and coastal shark populations have declined dramatically with increased fishing; however, the status of sharks in other systems such as coral reefs remains largely unassessed despite a long history of exploitation. Here we explore the contemporary distribution and sighting frequency of sharks on reefs in the greater-Caribbean and assess the possible role of human pressures on observed patterns.
We analyzed 76,340 underwater surveys carried out by trained volunteer divers between 1993 and 2008. Surveys were grouped within one km2 cells, which allowed us to determine the contemporary geographical distribution and sighting frequency of sharks. Sighting frequency was calculated as the ratio of surveys with sharks to the total number of surveys in each cell. We compared sighting frequency to the number of people in the cell vicinity and used population viability analyses to assess the effects of exploitation on population trends. Sharks, with the exception of nurse sharks occurred mainly in areas with very low human population or strong fishing regulations and marine conservation. Population viability analysis suggests that exploitation alone could explain the large-scale absence; however, this pattern is likely to be exacerbated by additional anthropogenic stressors, such as pollution and habitat degradation, that also correlate with human population.
Human pressures in coastal zones have lead to the broad-scale absence of sharks on reefs in the greater-Caribbean. Preventing further loss of sharks requires urgent management measures to curb fishing mortality and to mitigate other anthropogenic stressors to protect sites where sharks still exist. The fact that sharks still occur in some densely populated areas where strong fishing regulations are in place indicates the possibility of success and encourages the implementation of conservation measures.
Citation: Ward-Paige CA, Mora C, Lotze HK, Pattengill-Semmens C, McClenachan L, Arias-Castro E, et al. (2010) Large-Scale Absence of Sharks on Reefs in the Greater-Caribbean: A Footprint of Human Pressures. PLoS ONE 5(8): e11968. doi:10.1371/journal.pone.0011968
Editor: Steven J. Bograd, National Oceanic and Atmospheric Administration/National Marine Fisheries Service/Southwest Fisheries Science Center, United States of America
Received: January 12, 2010; Accepted: June 16, 2010; Published: August 5, 2010
Copyright: © 2010 Ward-Paige et al. This is an open-access article distributed under the terms of the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original author and source are credited.
Funding: Financial support was provided by the Natural Sciences and Engineering Research Council of Canada, the Census of Marine Life Future of Marine Animal Populations Program, the Lenfest Ocean Program and The Pew Charitable Trusts to R.A. Myers, H.K. Lotze. These funders did not play a role in conducting the study or in preparing the manuscript.
Competing interests: The authors have declared that no competing interests exist.
Strong declines in the abundance of many large pelagic sharks have been described worldwide and repeatedly linked to industrial fishing –. The extent of these declines and some of their ecosystem consequences have been described with the use of long-term catch datasets, mostly in pelagic systems . Unfortunately, the status of shark populations in other ecosystems, such as coral reefs, remains poorly known because both modern and historical data are very limited . This uncertainty, in combination with the high vulnerability of sharks to fishing ,  has motivated the use of alternative sources of data to shed light on temporal and spatial trends in shark populations. These sources of data include historical fisheries and market records of sharks in the Mediterranean , trophy photographs of fishing tournaments in Florida , archaeological and historical records on coral reef ecosystem changes worldwide , and ecological surveys of fish communities across spatial gradients of exploitation –, among others. Although these analyses have been opportunistic and restricted to few regions they have been valuable in describing changes in populations. Here, we explore another source of data based on observations made by trained scuba divers to examine patterns of distribution and sighting frequency of sharks on reefs in the greater-Caribbean, which includes sites in the western central Atlantic from northern Florida to northern Brazil, the Gulf of Mexico and the Caribbean Sea (Fig. 1).
Shown are sampled 1 km2 cells for A) all species combined, and B) all species excluding nurse sharks (Ginglymostoma cirratum). Note that cells were enlarged for the patterns of distribution to be seen at this scale.
Data collected by trained recreational divers can be a reliable and valuable source of data for describing large-scale patterns on the status of sharks. Trained scuba divers have been shown to collect data that is comparable to scientific divers across a range of biological metrics –. Although trained divers are instructed in the identification of a broad-range of fish species, the identification of sharks may be poor since many species are morphologically similar; however, data can still be reliable when looking at patterns of sharks as a group given the ease of differentiating sharks from other fish. Recreational divers travel to many sites providing data from a range of locations and allowing an overview of trends over large-spatial scales while the robustness of the emerging patterns can be supported by the sheer number of observations (i.e. number of divers and dives). Because recreational divers survey a wide range of habitats, depths, and times of the year, they also maximize the sighting probability of less common taxa such as sharks. This non-extractive sampling technique allows data to be obtained for animals that are at risk and from areas where fishing is prohibited. Sites preferred by recreational divers generally have more abundant large fish  and are likely inversely related to commercial fishing pressure, therefore providing a conservative look at the state of sharks.
Sharks on reefs can be particularly vulnerable to the growth and spatial expansion of human populations. As a group, sharks are susceptible to even mild levels of fishing mortality given their late age of maturity, slow growth, and slow reproductive rate , . In the greater-Caribbean, there has been a long and ongoing history of exploitation of sharks (see Table 1), which accelerated during the 20th century , . Reef sharks, including tiger (Galeocerdo cuvier), lemon (Negaprion brevirostris), sandtiger (Carcharias taurus) and silky (Carcharhinus falciformis) began to be targeted intensively in the early 20th century for their liver, skins, meat and fins  and commercial catches increased after 1950 , , . Landings of sharks more than tripled in the Gulf of Mexico between 1980 and 1989 and Caribbean elasmobranch landings peaked at more than 9 million metric tons in 1990 . Excessive harvesting of juveniles in recent years likely has exacerbated the effects of decades of fishing ,  – a trend which coincides with the increased demand for shark fins in Asian markets . Beyond direct exploitation, the presence of human settlements can lead to habitat degradation and destruction , which can reduce the area that is suitable for sharks and their survival rates . Similarly, overfishing of reef fish, which is related to human population density , may reduce the prey population available to sharks. As well, other anthropogenic stressors often occur simultaneously and likely act synergistically to exacerbate the loss of sharks; however, this has not been adequately quantified and trends in abundance and distribution of sharks on reefs are urgently needed to substantiate the establishment of conservation strategies.
In the greater-Caribbean, poor knowledge of the status of sharks on reefs is worrisome given the long history of reef exploitation (Table 1) , the extensive distribution of human settlements in the region  and the need to substantiate the establishment of conservation strategies. Here, we used a broad and comprehensive collection of underwater surveys conducted by trained divers in the greater-Caribbean to explore contemporary patterns in shark distribution and sighting frequency. We then assessed the role of anthropogenic stressors by comparing the sighting frequency of contemporary sharks to human population density. Finally, we used population viability analysis to assess the specific effect of fishing mortality on the distribution and sighting frequency of sharks.
Determining the distribution and sighting frequency of sharks
We used underwater visual censuses to describe the contemporary distribution and sighting frequency of sharks on reefs in the greater-Caribbean. Surveys were conducted by trained volunteer divers between 1993 and 2008 for the Reef Environmental Education Foundation (REEF, www.reef.org). Using the Roving Diver Technique (RDT)  divers survey a wide variety of habitats within a particular site and record all fish, including sharks, that are observed throughout the water column during their regular dive activities. This database contains ~100,000 surveys broadly distributed throughout the greater-Caribbean.
For the purpose of this study habitats were limited to reefs (high and low profile), slopes (dropoff, wall, ledge) and flats (grass, sand, rubble) – termed ‘reef’ from here on (for more habitat information see www.reef.org). Open water and artificial habitats were excluded. Sites with geo-referenced locations (latitude and longitude) were allocated into 1 km2 cells. In the REEF database abundance is recorded as binned values (e.g. 1 = 1, 2 = 2–10, 3 = 11–100) and original counts are unknown. Therefore, to eliminate any error associated with the number counted we limited our analyses to presence or absence of sharks on each dive. For each cell with more than 5 dives, we quantified the sighting frequency as the number of dives where sharks were reported divided by the total number of dives within that cell. To determine if there was a consistent bias in our results due to preference or indifference for diving with sharks, we used a regression model to compare the sighting frequency of sharks with survey effort (i.e. number of dives).
We limited our analyses to species that are described as reef-dwelling or reef-associated in Compagno et al.  and included bonnethead (Sphyrna tiburo Linnaeus), blacknose (Carcharhinus acronotus Poey), Atlantic sharpnose (Rhizoprionodon terraenovae Richardson), sandtiger (Carcharias taurus Rafinesque), blacktip (Carcharhinus limbatus Müller and Henle), tiger (Galeocerdo cuvier), spinner (Carcharhinus brevipinna Péron and Lesueur), silky (Carcharhinus falciformis Müller and Henle), lemon (Negaprion brevirostris Poey), bull (Carcharhinus leucas Müller and Henle), sandbar (Carcharhinus plumbeus Nardo), nurse (Ginglymostoma cirratum Bonnaterre), whale (Rhincodon typus Smith), Caribbean reef (Carcharhinus perezii Poey), scalloped hammerhead (Sphyrna lewini Griffith and Smith), great hammerhead (Sphyrna mokarran Rüppell), and smooth hammerhead (Sphyrna zygaena Linnaeus). Compagno  does not refer to the dusky shark (Carcharhinus obscurus) as reef associated, and was therefore excluded from our analyses. If this species had been misidentified and was one of the species that we analyzed, its inclusion would have had a negligible effect on our results as all data for this species consisted of only 16 observations at one site in the Texas Flower Garden Banks, in the northern Gulf of Mexico. Many shark species overlap in distribution, habitat use, and have similar morphologies, which can make identification difficult during field observations. We therefore used a cautionary approach, assuming all species could be misidentified, and combined the records for all these species. As such, our patterns should be interpreted for all sharks on reefs in general. However, we performed an additional analysis excluding nurse sharks, which are stationary, relatively common and reasonably easy to identify, and is the species with the least commercial value today . We performed this additional analysis because the differences introduced by this single, relatively unexploited species may reveal the effects of targeted fishing on the loss of sharks due to their commercial value.
Comparing patterns of shark sightings to human population density
The growth and spatial expansion of human populations have been accompanied by changes in land use, pollution and exploitation of natural resources . As such human population density can serve as a proxy for multiple anthropogenic stressors and was used here as a metric to assess the potential effect of human pressures on sharks. Specifically, we compared the sighting frequency of i) all sharks, ii) all sharks excluding nurse sharks and iii) only nurse sharks to the number of humans nearby. Data on human population were available at a resolution of 2.5′ (~5 km2 cells) for the year 2000 and were obtained from http://sedac.ciesin.columbia.edu/gpw/global.jsp. For each of the one km2 cells where the dive surveys were grouped, we added a 10 km buffer and obtained the maximum number of people within that buffer. The 10 km buffer was chosen as an easy to travel distance for fishers and a distance where reef habitats may be strongly influenced by land-based human disturbances, such as coastal development and pollution. Correlations between human density and sighting frequency were fitted using inverse power models.
Population viability analysis and the effect of fishing mortality
To explore the possible effects of exploitation on sharks, we used population viability analysis to assess whether fishing pressure alone could explain the observed patterns of sharks. Such demographic analyses quantify the resilience of species to different levels of fishing mortality given their life history attributes. Life history attributes were obtained from different sources for each species analyzed in the sightings database (see Table 2) and included age at maturity (α), longevity (w), fecundity (b, i.e. female pups per female per year, which was calculated from data on number of pups, gestation period and reproductive frequency), and natural mortality (M). Natural mortality (M) was estimated from longevity using Hoenig's  formula:Survival to age at maturity (lα) was calculated from a variant of the Euler-Lotka equation:where lα,Z is survival to age at maturity when total mortality is equal to Z. Total mortality (Z) is set at twice the natural mortality (this condition is applied to minimize the effects of density dependence) and population growth is stable (r = 0) . The intrinsic rate of population increase (r) was calculated as the rebound potential  or the growth rate of a population in the near absence of density-dependent controls. r was calculated as the value that satisfies the following variant of the Euler-Lotka equation:Changes in population size (N) due to exploitation were calculated in relative terms for each species using density-dependent and density-independent models of population growth:where F is fishing mortality or the proportion of the population that is removed by fishing. For one of our studied species (Atlantic sharpnose shark), F has been estimated at 0.46 in the greater-Caribbean . Therefore, to assess population viability of the different species under a range of fishing mortalities, F was set from 0 to 0.5, increasing at an interval of 0.1. Given that models were run in relative terms, N0 and carrying capacity (k) were set to 1. All parameters were calculated and represented graphically in a macro in Microsoft Excel which is available upon request. As a precautionary note, population viability analyses exclude some of the complexities of real ecosystems and therefore tend to predict high risk of decline; yet, they “can be useful for screening-level assessments, which should in general be precautionary” . For reef sharks, population viability analysis may provide a good approximation of population trends because many are exploited throughout their entire life cycle , , .
Distribution and sighting frequency of sharks on reefs in the greater-Caribbean
In total we analyzed 76,340 dives across 1,382 one km2 cells, with an average of 55 (S.E. ±3.3) dives per cell. Sharks were observed in 762 cells (i.e. 55% of all cells with more than 5 dives; Fig. 1A). Of these, 441 (32%) cells contained only nurse sharks, 227 (16%) contained a mixture of nurse and other sharks and 94 (7%) contained sharks other than nurse sharks. Across all cells, the average sighting frequency of sharks (i.e. the fraction of dives in which sharks were sighted) was 10% (S.E. ±0.004) for all sharks and 3% (S.E. ±0.003) for all sharks excluding nurse sharks.
The pattern of shark distribution in the greater-Caribbean was clearly affected by the inclusion of nurse sharks. When nurse sharks are considered, sharks were observed on reefs throughout most of the greater-Caribbean at some time during the study period (Fig. 1A). The greatest concentration of cells with high sighting frequency occurred in the Bahamas, southeastern US and Belize. With the exclusion of nurse sharks, however, the number and range of cells where sharks occurred was much smaller (Fig. 1B). Notably, sharks other than nurse sharks were largely absent in cells around Cuba, Jamaica, Dominican Republic, Puerto Rico, throughout most of the Antilles and central and South America. The greatest concentration of cells with sharks, other than nurse sharks, occurred in the Bahamas.
Although there was high variability in sighting frequency at intermediate levels of effort (i.e. 50–500 dives), there were no significant trends of sighting frequency with survey effort for all sharks (slope = −0.002, S.E. = 0.003, p = 0.28) or for all sharks excluding nurse sharks (slope = −0.002, S.E. = 0.002, p = 0.41) (Fig. 2). This suggests that variation in sampling effort (dives per cell) did not affect sighting frequency and should therefore not affect our results. In other words, sighting frequencies were on average similarly low using 10 or 500 dives in a cell (Fig. 2).
Relationship between the number of dives per 1 km2 cell and the sighting frequency of A) all sharks (r2 = 0.003, p = 0.4), and B) all sharks excluding nurse sharks (r2 = 0.0005, p = 0.4). Solid lines are linear models showing there is no change in sighting frequency with effort.
Effect of human population density on the sighting frequency of sharks
Comparison of the sighting frequency of sharks and human population density showed that, with the exception of nurse sharks and a small number of cells, sharks are absent in the majority of cells and that contemporary sharks occur mostly where human population density is low (Fig. 3). The few cells with a high sighting frequency of sharks (>10%) and large human population (>1000 people) occurred in Florida (4 cells), central Bahamas (4 cells), and the U.S. Virgin Islands (3 cells), which are areas that have strong fishing regulations such as prohibition of shark finning, extensive marine protected areas, and in the case of the Bahamas, prohibition of gillnet and long-line fishing. Based on AIC model selection, we found that inverse power models fit the relationship between human population density and shark sighting frequency better than inverse exponential models. Consequently, we report the results of the former only. For all the patterns analyzed, power models were highly significant (see Fig. 3A–C) and indicate that the sighting frequency of sharks was high only in areas where human population was very low (Fig. 3A–C).
Data on the number of people was obtained from the Socioeconomic Data and Applications Center at http://sedac.ciesin.columbia.edu/gpw/global.jsp. Trends (solid red lines) were fitted using inverse power models to define the relationship between sighting frequency of sharks (y) and log of human density (x). The models were A) y = 1/[6.8*(x+1)0.09], p<0.0001; B) y = 1/[20.6*(x+1)0.11], p = 0.0002; C) y = 1/[10.2*(x+1)0.09], p<0.0001. The graded colours on the figure are used to identify the density of cells on the plots where red = high, green = intermediate, white = low. Dashed lines show human population density = 1000 and sighting frequency = 0.10.
Population viability analysis and the effect of fishing mortality
As expected, under scenarios of zero fishing mortality (F = 0) populations under density dependence remained stable at carrying capacity (Fig. 4A) and increased under density independence (Fig. 4B). Under fishing mortalities of F = 0.1, where 10% of the population is removed per year due to fishing, all species declined to between 1 and 14% of their initial population size within 50 years under density dependent conditions (Fig. 4C). With the exception of bonnethead sharks, all species showed declining trends with fishing mortalities as low as F = 0.1 under density independent conditions (Fig. 4D). For the remaining scenarios of fishing mortality and density dependence all species declined by 99% within 28 years. As fishing mortality increased (Fig. 4E–L), the time to reach 1% of the initial population was reduced markedly. Under the conservative scenario of density independence, fishing mortalities of F = 0.2 and F = 0.5 reduced the populations of all species to less than 1% of their original population sizes in less than 39 and 10 years, respectively (Fig. 4F–L)
Using an extensive database of fish surveys conducted by trained recreational divers we show that contemporary sharks, other than nurse sharks, are largely absent on reefs in the greater-Caribbean. Comparison with data on human population density suggests that such disappearance may have been related to anthropogenic pressures. Our study revealed that sharks on reefs in the greater-Caribbean occurred mostly in areas with very low human population density or in a few places where strong fishing regulations or conservation measures are in place. Population viability analysis indicates that even low levels of fishing mortality can cause shark populations to decline to a small fraction of their initial abundance within a few decades, and suggests that fishing alone could explain the absence of sharks. These patterns are similar to those observed for other coastal and reef shark populations , ,  and may be indicative of a broader trend for regions that have a long history of exploitation.
The link between human population density and the absence of sharks on reefs is likely due to anthropogenic stressors that directly and indirectly affect their populations. Of the species analyzed, the IUCN  listed 2 as endangered, 4 as vulnerable, 8 as near-threatened, 2 as least concern and 1 as data deficient (nurse shark) at the global scale. For these species, fishing was identified as the main threat , which is corroborated by studies that have demonstrated the extent of overfishing of large predators in the greater-Caribbean , , , , , . Considering the timescale of exploitation (Table 1) and the results of our population viability analysis which show that even low levels of fishing pressure cause shark populations to be reduced to a small fraction of their initial population within a few decades, it is likely that fishing pressure alone, whether targeted or incidental, could explain the observed large-scale absence of sharks. However, the high vulnerability of sharks to fishing pressure is likely exacerbated by cumulative anthropogenic factors that could reduce shark populations on reefs, such as habitat destruction or degradation , , , climate change , , , , and pollution .
High vulnerability of sharks to fishing pressure is likely exacerbated by the long history of exploitation and the cumulative human impacts in coastal waters. 2200 years ago, virtually all islands in the Caribbean were already colonized and recreational and artisanal fishing activities on reefs and nearshore habitats have increased and expanded dramatically since then , including a demand for different shark products (e.g. meat, oil, skin, fins) that extends to present times , , . Additional evidence for the role of fishing is our results on nurse sharks. This species has a low rebound potential (Table 2), suggesting that it would be very vulnerable to even mild levels of fishing. However, it is the most frequently sighted shark on reefs today and although there are some differences in the diet, behaviour and habitat use of nurse shark and other sharks, compared to the rest of our analyzed species it is the one that has had the least value for its meat or fins ,  and is often discarded with low post-capture mortality . This suggests that nurse sharks may be the least affected by fishing in our study, which would explain the presence of this species as well as highlighting the likely role of fishing on the absence of targeted sharks on reefs. Nevertheless, even nurse sharks show decreasing sighting frequency with increasing human density suggesting that other human impacts also play a role. Finally, the presence of sharks near populated areas, such as in Florida, the central Bahamas and U.S. Virgin Islands, where strong fishing regulations and large and long-established marine protected areas exist, stresses the importance of fishing as the likely main driver of the observed large-scale absence of targeted sharks as well as the possible success of management and conservation in protecting sharks.
One possible caveat to our analysis regards the quality of the data. It is possible that divers avoid sites with sharks, miss sharks while diving, or that sharks avoid divers. Although we found no bias in the number of dives for or against sites with sharks (Fig 2), if there was a spatial sampling bias it should be towards sites with sharks and other abundant large fish because of their appeal to recreational divers , , . As well, most sharks are very conspicuous, which makes it unlikely that divers would miss them on a typical dive, especially when using the Roving Diver Technique because they are meant to search the entire water column for as many species as possible. Finally, scientific diver surveys have been previously used to characterize shark populations in other reef areas of the world where sharks are abundant such as in the central Pacific Ocean , , , Andaman Sea , and Great Barrier Reef , supporting the reliability of diver data for assessing spatial trends in shark sightings. Moreover, all of these studies found a strong negative relationship of sharks across a spatial gradient of human population density or exploitation –, corroborating our results.
A second possible caveat of the interpretation of our results is that sharks never existed in these areas or that they occurred at such low densities that they were missed by divers. However, geographical ranges, based on expert opinions and fisheries data , indicate that the analyzed shark species should occur throughout the study area (Fig. 5A). Furthermore, the entire study area encompasses habitats of suitable environmental conditions for the presence of the analyzed shark species (see further details in Fig. 5B). We also found numerous records pointing out the generally high abundance of sharks in the greater-Caribbean in the past (Table 1). Although these narratives cannot be directly linked to our study sites, those records that we presume occurred within the depth range of divers and that did not use an attractant (i.e. bait) indicate that sharks, including our studied species, were markedly more abundant than what they appear to be today. Interestingly, Baughman and Springer  stated that sharks were “expected anywhere at anytime” in the west-Indian Caribbean; in contrast, our analysis of contemporary dive surveys indicate that with the exception of nurse sharks, sharks are expected anytime almost nowhere.
Here we show the number of shark species (see color code from 1 to 16) whose (A) geographical ranges and (B) suitable habitats overlap in half-degree cells across the greater-Caribbean. Geographical ranges were obtained from Compagno et al.  and suitable habitats for each species from AquaMaps . Suitable habitats are based on the envelope of the environmental conditions where each species has been reported; the variables considered include depth, temperature, salinity, primary productivity, and distance to coastal areas. Cells containing diver survey data from our study are outlined with black borders.
Overall, our results indicate that human stressors in coastal areas, potentially dominated by exploitation, have likely led to the absence of shark populations on many reefs in the greater-Caribbean. Contemporary sharks mostly occur in areas with low human populations or where strong fishing regulations or enforced marine reserves occur. Yet historical records, range maps and habitat suitability models suggest that sharks used to, and still could, occur on reefs throughout the greater-Caribbean. Preventing the complete loss of sharks on reefs in the greater-Caribbean requires urgent management measures to mitigate human pressures in coastal waters, especially directed and incidental exploitation from commercial, artisanal and recreational fishing, and protect sites from pollution and habitat destruction where sharks still exist. The fact that sharks still occur in densely populated areas where strong fishing regulations are in place indicates the possibility of success and may encourage the implementation of conservation measures that would restore sharks together with their ecological and functional roles on reefs.
We are grateful to F. Ferretti, V. Garcia, J. Hutchings, L. Lucifora, H. Whitehead and B. Worm for comments and discussion. We thank the Reef Environmental Education Foundation fish surveyors for contemporary data.
Conceived and designed the experiments: CAWP CM RAM. Analyzed the data: CAWP CM HKL EAC RAM. Contributed reagents/materials/analysis tools: CPS LM RAM. Wrote the paper: CAWP CM HKL.
- 1. Baum JK, Myers RA, Kehler DG, Worm B, Harley SJ, et al. (2003) Collapse and conservation of shark populations in the Northwest Atlantic. Science 299: 389–392.
- 2. Baum JK, Myers RA (2004) Shifting baselines and the decline of pelagic sharks in the Gulf of Mexico. Ecology Letters 7: 135–145.
- 3. Myers RA, Worm B (2005) Extinction, survival or recovery of large predatory fishes. Philosophical Transactions of the Royal Society B-Biological Sciences 360: 13–20.
- 4. Myers RA, Worm B (2003) Rapid worldwide depletion of predatory fish communities. Nature 423: 280–283.
- 5. Ward P, Myers RA (2005) Shifts in open-ocean fish communities coinciding with the commencement of commercial fishing. Ecology 86: 835–847.
- 6. Heithaus MR, Frid A, Wirsing AJ, Worm B (2008) Predicting ecological consequences of marine top predator declines. Trends in Ecology & Evolution 23: 202–210.
- 7. Dulvy NK, Baum JK, Clarke S, Compagno LJV, Cortes E, et al. (2008) You can swim but you can't hide: the global status and conservation of oceanic pelagic sharks and rays. Aquatic Conservation: Marine and Freshwater Ecosystems.
- 8. Garcia VB, Lucifora LO, Myers RA (2008) The importance of habitat and life history to extinction risk in sharks, skates, rays and chimaeras. Proceedings of the Royal Society B-Biological Sciences 275: 83–89.
- 9. Ferretti F, Myers RA, Serena F, Lotze HK (2008) Loss of large predatory sharks from the Mediterranean Sea. Conservation Biology 22: 952–964.
- 10. McClenachan L (2009) Documenting loss of large trophy fish from the Florida Keys with historical photographs. Conservation Biology 23: 636–643.
- 11. Pandolfi JM, Bradbury RH, Sala E, Hughes TP, Bjorndal KA, et al. (2003) Global trajectories of the long-term decline of coral reef ecosystems. Science 301: 955–958.
- 12. Robbins WD, Hisano M, Connolly SR, Choat JH (2006) Ongoing collapse of coral-reef shark populations. Current Biology 16: 2314–2319.
- 13. 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: 1548.
- 14. 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.
- 15. Edgar GJ, Stuart-Smith RD (2009) Ecological effects of marine protected areas on rocky reef communities-a continental-scale analysis. Marine Ecology-Progress Series 388: 51–62.
- 16. Leopold M, Cakacaka A, Meo S, Sikolia J, Lecchini D (2009) Evaluation of the effectiveness of three underwater reef fish monitoring methods in Fiji. Biodiversity and Conservation 18: 3367–3382.
- 17. Pattengill-Semmens CV, Semmens BX (1998) Fish census data generated by non-experts in the Flower Garden Bands National Marine Sanctuary. Journal of Gulf of Mexico Science 2: 196–207.
- 18. Williams ID, Polunin NVC (2000) Differences between protected and unprotected reefs of the western Caribbean in attributes preferred by dive tourists. Environmental Conservation 27: 382–391.
- 19. Commission A-AC (1945) Guide to commercial shark fishing in the Caribbean area. Washington, D.C.: Kaufmann Press, Inc. 149 p.
- 20. Bonfil R (1997) Status of shark resources in the southern Gulf of Mexico and Caribbean: implications for management. Fisheries Research 29: 101–117.
- 21. Shepherd TD, Myers RA (2005) Direct and indirect fishery effects on small coastal elasmobranchs in the northern Gulf of Mexico. Ecology Letters 8: 1095–1104.
- 22. SAUP (2010) Sea Around Us Project
- 23. Pikitch EK, Chapman DD, Babcock EA, Shivji MS (2005) Habitat use and demographic population structure of elasmobranchs at a Caribbean atoll (Glover's Reef, Belize). Marine Ecology-Progress Series 302: 187–197.
- 24. Clarke S (2004) Understanding pressures on fishery resources through trade statistics: a pilot study of four products in the Chinese dried seafood market. Fish and Fisheries 5: 53–74.
- 25. MEA (2005) Millennium Ecosystem Assessment. Ecosystems and human well-being: synthesis. Washington, D.C.: Island Press.
- 26. Jennings DE, Gruber SH, Franks BR, Kessel ST, Robertson AL (2008) Effects of large-scale anthropogenic development on juvenile lemon shark (Negaprion brevirostris) populations of Bimini, Bahamas. Environmental Biology of Fishes 83: 369–377.
- 27. Newton K, Cote IM, Pilling GM, Jennings S, Dulvy NK (2007) Current and future sustainability of island coral reef fisheries. Current Biology 17: 655–658.
- 28. Fitzpatrick SM, Keegan WF (2007) Human impacts and adaptations in the Caribbean Islands: an historical ecology approach. Transactions of the Royal Society of Edinburgh-Earth Sciences 98: 29–45.
- 29. Mora C (2008) A clear human footprint in the coral reefs of the Caribbean. Proceedings of the Royal Society B-Biological Sciences 275: 767–773.
- 30. Schmitt EF, Sluka RD, Sullivan-Sealey KM (2002) Evaluating the use of roving diver and transect surveys to assess the coral reef fish assemblage off southeastern Hispaniola. Coral Reefs 21: 216–223.
- 31. Compagno L, Dando M, Fowler S (2005) Sharks of the world. London: HarperCollins Publishers Ltd.
- 32. Castro JI (2000) The biology of the nurse shark, Ginglymostoma cirratum, off the Florida east coast and the Bahama Islands. Environmental Biology of Fishes 58: 1–22.
- 33. Hoenig JM (1983) Empirical use of longevity data to estimate mortality-rates. Fishery Bulletin 81: 898–903.
- 34. Smith SE, Au DW, Show C (1998) Intrinsic rebound potentials of 26 species of Pacific sharks. Marine and Freshwater Research 49: 663–678.
- 35. Marquez-Farias FJ, Castillo-Geniz LJ (1998) Fishery biology and demography of the Atlantic sharpnose shark, Rhizoprionodon terraenovae, in the southern Gulf of Mexico. Fisheries Research 39: 183–198.
- 36. Dunham AE, Akcakaya HR, Bridges TS (2006) Using scalar models for precautionary assessments of threatened species. Conservation Biology 20: 1499–1506.
- 37. Carlson JK, Bethea DM, Middlemiss A, Baremore IE (2004) Shark nursery grounds and essential fish habitat studies. Panama City, FL: Southeast Fisheries Science Center. pp. 1–21. SFD Contribution PCB-04-06 SFD Contribution PCB-04-06.
- 38. IUCN (2010) IUCN Red List of Threatened Species. Version 20101.
- 39. Ferretti F, Worm B, Britten GL, Heithaus MR, Lotze HK (2010) Patterns and ecosystem consequences of shark declines in the ocean. Ecology Letters. in press.
- 40. Stallings C (2009) Fishery-independent data reveal negative effect of human population density on Caribbean predatory fish communities. Plos One 4: e5333.
- 41. Heithaus MR, Burkholder D, Hueter RE, Heithaus LI, Pratt HL, et al. (2007) Spatial and temporal variation in shark communities of the lower Florida Keys and evidence for historical population declines. Canadian Journal of Fisheries and Aquatic Sciences 64: 1302–1313.
- 42. Knip DM, Heupel MR, Simpfendorfer CA (2010) Sharks in nearshore environments: models, importance, and consequences. Marine Ecology-Progress Series 402: 1–11.
- 43. Heupel MR, Carlson JK, Simpfendorfer CA (2007) Shark nursery areas: concepts, definition, characterization and assumptions. Marine Ecology-Progress Series 337: 287–297.
- 44. Perry AL, Low PJ, Ellis JR, Reynolds JD (2005) Climate change and distribution shifts in marine fishes. Science 308: 1912–1915.
- 45. Bradshaw CJA, Peddemors VM, McAuley RB, Harcourt RG (2008) Population viability of eastern Australia grey nurse sharks under fishing mitigation and climate change
- 46. Martinez JL (1947) The Cuban shark industry. Washington, D.C.: United States Department of Interior, Fish and Wildlife Service. pp. 1–27.
- 47. Viele J (1996) The Florida Keys: A history of the pioneers. Sarasota, Florida: Pineapple Press. pp. 135–139.
- 48. Davis D, Banks S, Birtles A, Valentine P, Cuthill M (1997) Whale sharks in Ningaloo Marine Park: managing tourism in an Australian marine protected area. Tourism Management 18: 259–271.
- 49. Stevenson C, Katz LS, Micheli F, Block B, Heiman KW, et al. (2007) High apex predator biomass on remote Pacific islands. Coral Reefs 26: 47–51.
- 50. Theberge MM, Dearden P (2006) Detecting a decline in whale shark Rhincodon typus sightings in the Andaman Sea, Thailand, using ecotourist operator-collected data. Oryx 40: 337–342.
- 51. Baughman JL, Springer S (1950) Biological and economic notes of the sharks of the Gulf of Mexico, with especial reference to those of Texas, and with a key for their identification. American Midland Naturalist 44: 96–152.
- 52. Kaschner K, Ready JS, Agbayani E, Rius J, Kesner-Reyes K, et al. (2008) AquaMaps: Predicted range maps for aquatic species. World wide web electronic publication, wwwaquamapsorg, Version 10/2008.
- 53. Colón F (1959) The life of the Admiral Christopher Columbus by his Son, Ferdinand. New Brunswick: Rutgers University Press.
- 54. Sloane H (1707) A voyage to the islands Madera, Barbados, Niees, S. Christophers, and Jamaica. London.
- 55. Hawkins JP, Roberts CM (2004) Effects of artisanal fishing on Caribbean coral reefs. Conservation Biology 18: 215–226.
- 56. Jordan DS (1884) List of fishes collected at Key West, Florida, with notes and descriptions. United States National Museum Proceedings.
- 57. Burdon KJ (1920) A handbook of St. Kitts-Nevis. London: The West India Company.
- 58. Watkins FH (1924) Handbook of the Leeward Islands. London: West India Company.
- 59. Citizen KW (1931) Key West Citizen, Munroe County Public Library. Key West, FL.
- 60. Casey JG, Hoey JJ (1985) Estimated catches of large sharks by US recreational fishermen in the Atlantic and Gulf of Mexico. NMFS 31: 35-19.
- 61. Frisk MG, Miller TJ, Dulvy NK (2004) Life histories and vulnerability to exploitation of elasmobranchs: Inferences from elasticity, perturbation and phylogenetic analyses. Journal of the Northwest Atlantic Fisheries Science 34: 1–19.
- 62. Froese R, Pauly D, editors. (2010) FishBase. World Wide Web electronic publication. www.fishbase.org, version (05/2010).