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Severe Impact and Subsequent Recovery of a Coral Assemblage following the 1997–8 El Niño Event: A 17-Year Study from Bahia, Brazil

Severe Impact and Subsequent Recovery of a Coral Assemblage following the 1997–8 El Niño Event: A 17-Year Study from Bahia, Brazil

  • Francisco Kelmo, 
  • Martin J. Attrill
PLOS
x

Abstract

The coral reefs of northern Bahia evolved in isolation from other Atlantic systems and under conditions of high environmental stress, particularly high turbidity. We have monitored the scleractinian assemblage of four shallow bank reefs (Praia do Forte, Itacimirim, Guarajuba and Abai) annually for 17 years since 1995, collecting quantitative data on diversity and density of coral colonies. As the sampling period included the 1997–8 El Niño event, the most severe on record, for the first time these results allow a quantitative assessment of the long-term impact of this major environmental stressor on such a coral assemblage. After El Niño, most species showed significantly reduced densities of colonies, this decline occurring for the subsequent two years without evidence of any new settlement until 2001. From 2000 to 2007 the species Porites astreoides went unrecorded. Recovery was slow, and multivariate analysis revealed that assemblages had not returned to the pre-El Niño state until 2011. It therefore took 13 years for full recovery of the coral assemblage to occur, which has consequences for reef systems if such El-Niño events become more frequent in the future.

Introduction

The 1997–8 El Niño Southern Oscillation (hereafter ENSO) was the most extensive global ENSO event [1], [2], [3] and was associated with record global high seawater temperatures [4], [5], [6], [7], other ENSO events having had a clear impacts regionally [8], [9], but not at such a severe global scale. The evolution of ocean temperature anomalies in the Southern Hemisphere began several months earlier than the envelope of prior ENSO events and had exceptional amplitude, lasting for approximately 18 months [10]. This event followed a similar pattern in terms of the timing of its maximum development [11] and thus was similar in magnitude and duration to the 1982–3 [12] and 1986–7 events. However, it had differential effects throughout the Brazilian region [13] with increased rainfall and flooding experienced by the southernmost and central states, whilst northeastern states experienced devastating droughts [14] because of abnormally reduced rainfall in the region. Coral reefs are considered vulnerable to tipping points because of their narrow thermal and water quality tolerances, heavy reliance on key framework species and high susceptibility to nutrient runoff and eutrophication [15]. The large-scale effects during 1982–3 and 1986–7 were a tipping point for coral reefs (e.g. [16], [17]), but the most severe 1997–8 ENSO event had a more extensive impact globally on coral reefs [18], [19], [20], [21], the climatic features linked to this event causing severe coral bleaching and mortality in Panama and Ecuador [10], Indian ocean [22], Arabian Gulf [23], tropical Pacific [24], South Africa [25] and Brazil [26].

The coral reefs from northern Bahia, Brazil, have evolved and developed under natural conditions of high temperatures and high turbidity [27]. Together with the likely impact of the Amazon biogeographical barrier [28], [29], these environmental stressors have prevented the colonization of large numbers of coral taxa that are common elsewhere in the Atlantic, resulting in the Brazilian reefs having a comparatively low diversity coral fauna distinct from that of the Caribbean. Additionally, the scleractinians recorded from the northern Bahian reefs therefore have a relatively narrow geographical and environmental range and almost 40% of the species are endemic to Brazilian waters.

A long-term monitoring of these coral reefs was initiated in 1995 along northern coast of the State of Bahia, the main objective being to record temporal and spatial patterns of biodiversity and community structure of the reef-associated biota on four reef systems along this coast. The sampling period therefore included the 1997–8 ENSO event allowing, for the first time, a quantitative assessment of the long-term impact of this major environmental stressor on the biodiversity of the scleractinian assemblage and any subsequent recovery trends.

Considering that any impact on scleractinian corals has major repercussions for the reef ecosystem [30], [31], this paper reports the results of the ongoing long-term study on the scleractinian assemblage from the shallow-bank reefs of northern Bahia, using data collected over the last 17 years. We describe for the first time how the individual scleractinian coral species and the overall coral assemblage have responded to the stress imposed by the 1997–8 ENSO event, and document the time required for recovery, giving a clear indication of the temporal scale of such climatic impacts.

Methods

Study Area

The four studied reefs (termed Abaí, Guarajuba, Itacimirim and Praia do Forte), exist on the narrowest part of the Eastern Brazilian Continental Shelf (average width 15 km between the Sao Francisco and Doce Rivers) and extend 20 km. The reefs of interest (Fig. 1) are Abai (12°40′04′′S/38°04′47′′W), Guarajuba (12°39′22′′S/38°03′18′′W), Itacimirim (12°37′20′′S/38°01′40′′W) and Praia do Forte (12°34′42′′S/37°58′59′′W). They are complex elongated structures varying from 500 to 1,800 m in length, from 400 to 500 m in width and in water depths between 10 and 40 m. The Pojuca River discharges near the reefs of interest; the river’s mean annual flow of 32 m3/s was reduced to 20 m3/s during the 1997–8 ENSO. The reefs are made up mainly of discrete coral heads that have developed either on rock outcrops of various ages or on lines of Holocene beachrock [32]. Their lateral contour is irregular, sometimes presenting well-developed, spur-and-groove systems on the fore-reef side, while the back-reef is usually less irregular (see [33] for details).

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Figure 1. Location map showing the coral reefs of Northern Bahia Region (After Leão et al., 1997).

https://doi.org/10.1371/journal.pone.0065073.g001

The coastal belt of the State of Bahia has a tropical humid climate. Annual average rainfall ranges between 1,300 mm in the north of the study area to 1,900 mm around Salvador City to the south, with no marked seasonal rainfall pattern. Average daily air temperatures range from 23° (winter) to 28°C (summer), with mean daily sea-surface temperatures ranging from 25° (winter) to 28°C (summer); the maximum SST occurs between December and February each year. Annual average salinity varies little (35–36), although within reef-top shallow pools, salinity can range from 35 to 39. The pH of seawater varies only between 8.1 and 8.2, with no clear seasonal patterns (see [34]). The coast is influenced by winds arising from the NE and E during the spring-summer, and winds coming from the SE and E during the autumn-winter season. Moreover, during the autumn-winter period, the winds arising from the SSE, associated with the periodic advance of the Atlantic Polar Front, reinforce the trade winds from the SE [35]. This pattern of wind circulation is disrupted by the quasi-cyclic environmental phenomenon known as the El Niño/La Niña and includes changes in the Atlantic Polar Front [35], with several climatic perturbations recorded [14], [36].

Sampling

We collected density data on the scleractinian community from the four shallow bank reefs annually (between April and May) from 1995 to 2011 by SCUBA diving. Quantitative samples of the coral colonies were taken with 35 1m2 quadrats positioned haphazardly on each reef (depths 10–20 m) giving a total of 140 quadrats per year, and 2,380 in total over the survey period. The majority of hard coral in Bahia is present as comparatively small, isolated coral heads rather than extensive reefs, so individual colonies would be easily enumerated using this quadrat size. All corals (live and dead colonies) were counted in situ and any visual bleaching of the colony documented as normal, fully or partially bleached. We annotated data on color and colony size in the field along with photographic records. No specific permits were required for the described field studies as we did not need to remove any biological material from the reefs. No specific permissions were required due to the fact that this was an entirely field based study with all data being recorded on site through the in-situ identification and counting of coral colonies. The location is not privately-owned or protected in any way, as the beaches surveyed are public spaces. We did not kill or damage any of the studied organisms. These were just counted, so our methods represent no threat to the species we assessed and none is, as yet, endangered. Relative abundance analysis was assessed using the progressive scale proposed by Peixinho and Peso-Aguiar [37], resulting in density values per m2.

Our environmental data were from two sources: direct measurements from the sites during the survey period and data obtained from the Brazilian Meteorological Office (INMET website. http://www.inmet.gov.br/portal/index.php?r=home/page&page=rede_estacoes_conv_graf. Accessed 2013 Mar 20). As it was not logistically possible to sample water over the whole year from the site, the wider Meteorological Office data were used to look at annual patterns. Wide-scale environmental parameters for the survey area (sea surface temperature, solar irradiance, air temperature, rainfall, and cloud cover) were obtained from the INMET: these data are collected three times a day and the values presented in this paper represent the annual period around sampling. INMET data are classified internationally in ISO9001. We recorded local physicochemical data (seawater temperature, salinity, pH, and turbidity) across the four reef sites (10 replicates/reef giving 40 measurements spread over the sampling period April/May)], which was considered adequate to allow comparison between years (see 27). Temperature, salinity, and pH were recorded using a YSI63 (Yellow Spring Industries) electronic field meter (1995–2000), while turbidity was assessed using a Secchi disk, all deployed from a boat.

Since 2001 we also recorded turbidity and other local data using a Multiparameter Water Quality Meter (U5210); however, for reasons of uniformity we present the same type of measurement throughout the years. Depth (below low tide) was recorded at each sampling station.

Previous analysis has demonstrated no significant effect of location on community data collected from within each reef [38], so the significance of differences between years was assessed using either ANOVA [log (x+1) transformed coral densities, normally distributed environmental variables] or Kruskall-Wallis (non-normal environmental data, no transformation) tests (α = 0.05). Post-hoc pairwise comparisons were undertaken using either Tukey-Kramer or Dunn’s multiple comparison tests.

For multivariate analysis, the coral density data were normalized and log(x+1)-transformed in order to reduce the influence of dominant species [39]. A triangular matrix of similarities between samples was computed using the similarity coefficient of Bray and Curtis [40]. The similarity matrix was subjected to ordination analyses using the PRIMER (Plymouth Routines in Multivariate Ecological Research) package [41]. Ordination was by non-metric multidimensional scaling (MDS). We examined the contribution of species to dissimilarities between the groupings observed in the ordination analyses using the SIMPER procedure (similarity percentages; [42]). We used the BIOENV method [43] to investigate the relationship between environmental variables (pre- and post- ENSO) and the coral community data. This method is used as an exploratory tool in ways analogous to multiple regression [43] and correlates the similarity matrix derived for the coral communities with an equivalent for the suite of environmental measurements taken at each site. Results are expressed as a Spearmans correlation coefficient (r), ranked in the order of which single variable or combination of variables best explains the observed community patterns [43]. The results (maximum of 1) indicate the proportion of variance in the community data explained by these environmental variables (see [43] for full details). We tested for significance difference in coral community composition between years using Two-way crossed ANOSIM [44].

Results

The 1997–8 ENSO had a significant influence on most of the measured environmental parameters (Table 1). Mean air and seawater temperatures and hours of sunlight increased significantly in 1998 compared with all other years, the latter due to lower cloud cover. Rainfall was significantly lower during ENSO conditions and this resulted in reduced freshwater and sediment outflow from the local rivers (the mean annual discharge of the São Francisco River was reduced from 32,980 to 1,768 m3s−1 and that of Doce River from 80.5 to 50.2 m3s−1) and, thus, significantly clearer water. 1998 was therefore characterized by warmer air and sea temperatures, reduced cloud cover and rainfall, higher incoming solar radiation, and reduced turbidity (due mainly to reduced river runoff following decreased precipitation). Similar, but not so intense, conditions were observed in 2007 and 2010. In contrast, 1999–2000, and to a lesser extent, 1995–6 represented relatively strong La Niña conditions, as indicated by high rainfall and cloud cover (Table 1).

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Table 1. Summary of wide-scale and locally measured physico-chemical data recorded from the shallow bank Reefs throughout the sampling period.

https://doi.org/10.1371/journal.pone.0065073.t001

We recorded eight species of scleractinian corals (Fig. 2a–h) from the four shallow bank reefs of northern Bahia: Agaricia agaricites (Linnaeus, 1758); Favia gravida Verrill,1868; Montastraea cavernosa (Linnaeus, 1766); Mussismilia braziliensis (Verril, 1868); Mussismilia harttii (Verrill, 1868); Mussismilia hispida (Verrill, 1901); Porites astreoides Lamark, 1816 and Siderastrea stellata Verrill, 1868. Each species was recorded from all four locations (Praia do Forte, Itacimirim, Guarajuba and Abai) during the investigation period. There was no significant variation in species composition between reefs.

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Figure 2. Changes in density and % of bleaching (mean ± sd) of the eight coral species recorded over a 17 year period 1995–2011 in Bahia, Brazil.

Vertical coloured bar represents the time period of the 1997–8 severe El Niño;

https://doi.org/10.1371/journal.pone.0065073.g002

We observed partially bleached corals in each year of the survey. Only the colonies of Porites astreoides were fully bleached between 1997–8. The percentage of bleached corals was significantly higher in 1997–8 (Fig. 2a–h) than during 1995–96 (Two-way ANOVA, F16,527 = 22.351, p<0.001) remaining comparatively high for the following two years (strong La Niña).

The percentage of colony mortality, recorded in each year, was relatively low during pre-ENSO, but increased for all species in 1998 (Fig. 3a–d). Highest initial mortality was suffered by M.brasiliensis (from 18.8±1.88% in 1995 to 43.24±3.82% in 1998), followed by P.astreoides (7.52±0.43%–39.4±1.98%), A.agaricites (15.8±1.13%–36.9±3.27%) and M.cavernosa (14.7±1.47%–35.5±1.25%). The percentage of dead colonies decreased continuously until 2007 when we recorded increased mortality to P.astreoides (30.76±1.56%), M.braziliensis (30.95±1.51%) and A.agaricites (26.2±1.66%). We recorded an increase of mortality in 2010 for all species but S.stellata. During the whole investigation lowest mortality was experienced by S.stellata (5.92±0.82%–20.78±0.53%), but its recovery was evident by 2000 (only 5,95±0.41% mortality). Since then mortality has fluctuated within 10%.

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Figure 3. Trends over 17 years in % mortality for the eight coral species recorded from Bahia, Brazil.

a. A.agaricites & S. stellata. b. P. astreoides & F.gravida. c. M. cavernosa & M. brasiliensis. d. M. hispida & M.harttii. Data expressed as % dead colonies, vertical bar represents the 1997–8 El Niño event.

https://doi.org/10.1371/journal.pone.0065073.g003

A further consequence of the ENSO event was the significant reduction in coral density in 1998 (Two-way ANOVA, F16,527 = 6.043, p<0.0001), the decline continuing during the strong La Niña cycle in 1999–2000 (Fig. 2a–h) which resulted in local disappearance of P.astreoides in the year 2000; it was then absent from the reefs for seven years (see supporting information). From 2001 coral density increased continuously until 2007 to a maximum mean of 8.67±0.03 colonies m−2 (Fig. 2a–h). Conversely, in the same period the percentage of bleached colonies (Fig. 3a–h) decreased to values below 20% and this coincided with the reappearance of P. astreoides on all four reefs in 2007 after its absence. Since 2007 all eight species recorded during the pre-ENSO period have been present across the four studied reefs. Over recent years, we have documented some density reduction trends, but for most species these seem to be returning to values similar to those recorded during the pre-ENSO years of monitoring (1995–7). As of 2011, however, densities of M. hispida, F. gravida and P. astreoides are below the pre-ENSO state.

MDS ordination illustrates three different periods in the progression of the studied coral assemblage (Fig. 4): (i) Years from 1995–7, i.e. pre-ENSO years [SIMPER average similarity 94.21]; (ii) Years from 1998–2000, termed ENSO-impact years [average similarity 87.00] and, (iii) Years 2001–11, post-ENSO years (average similarity [82.80]). Through this ordination analysis, it is clear that the studied coral assemblage has changed significantly over these seventeen years (two-way crossed ANOSIM, r = 0.637, p<0.01), first suffering the devastating impacts of the 1997–8 ENSO/1999–2000 La Niña events and eventually recovering from it, with little apparent influence from any other further low intensity ENSO events that have occurred since 2001. By 2011, samples were similar to those from the 1995–7 pre-ENSO period. Coral assemblage recovery from such an ENSO event therefore has taken 13 years.

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Figure 4. Non-metric multidimensional scaling ordination of the coral assemblage data from the four assessed shallow-bank reefs from northern Bahia (Praia do Forte, Itacimirim, Guarajuba and Abai) throughout the sampling period, 1995–2011.

Arrows indicate cyclical direction of change. Codes refer to year of sampling (i.e. 00 = 2000). The nearer the data labels, the more similar the assemblages between those two samples.

https://doi.org/10.1371/journal.pone.0065073.g004

Finally, BIOENV analysis indicated that variation in turbidity (r = 0.32) was the main environmental factor best explaining the coral community differences on the assessed reefs in non-ENSO years. However, a combination of turbidity (r = 0.65), mean temperature (r = 0.64), and cloud cover (r = 0.56) best explained the changes in the community in 1998, and again in 2007 and 2010.

Discussion

The impact of the 1997–8 ENSO event on the coral reef fauna of Bahia has been well documented [45], [46], [47], [48]. Such impacts are in common with other studies [27], [49] as well as other reef systems around the globe (e.g. [50], [51]); however, there are few data on recover patterns from Brazil (but see [52 and 53).

Multivariate analysis demonstrated that the coral community from the shallow bank reefs became significantly different from 1998 onwards, compared with previous years. Considering the documented large-scale effects of the 1997–8 ENSO on coral reefs [54], it is reasonable to connect these clear changes in the coral community from 1998 onwards with this stressing event, as they are linked with differences in abiotic variables that year [increased temperature, reduced turbidity and cloud cover (Table 1)]. In addition, as there was bleaching in each studied year and diversity remained comparatively unaffected, we consider decline in density of live colonies (increase of mortality) as the main initial response of the Bahian coral community to ENSO events [38].

The decline in productivity, and subsequent reduction of the food supply following the ENSO stress period [55], leads to the disruption of many trophic links in coral reef communities [27], [55]. The effects of this nutritional deficit [56], [57], [58], [59], [60], [61], [62], [63] reduces the capacity of corals to compete favorably for space with other reef associated organisms, leading to the coral decline we documented during the 1997–8 ENSO.

Apart from P. astreoides, the hermatypic corals from the study reefs appeared comparatively resistant to ENSO events. There was a decrease in density of live colonies, but the response to ENSO conditions was similar for all reefs. In the past [48], comparisons between densities of bleached and non-bleached corals along the study area reflected the resistance of the Bahian corals to prolonged environmental stress. There was significant increase in the percentage of bleached colonies between 1998–2000; however, the average overall bleaching (36.5%) and subsequent mortality (33.3%) was lower than expected for such a strong ENSO event when compared with other areas such as Micronesia [64], Pacific [65] and Indian Ocean [66], [67], where the occurrence of bleaching was abnormally high.

It is important to highlight that a peculiar coralline fauna exists in the Northern Bahia shallow bank Reefs, as half of the recorded species are endemic. Some relevant aspects that increase survival rate of scleractinian corals (see [68] and references therein) includes phenotypic plasticity, which confers them tolerance to various environmental conditions and, resistance to changing habitat conditions, efficiency in removal of accumulated sediment and high energy investment to protect and reduce possible inter-specific competition for potential growth space [69]. Rapid colonisation of available substrata can be as result of higher investment in sexual reproduction and periodic release of planulae resistant to limiting resources [68], [70]. Although it is energy demanding, corals attempt to clean themselves of sediments by a combination of ciliary action and the production and sloughing off of mucus layers [71] and references therein. More detailed studies are needed, however, before it can be verified whether the size of the corallites and the ciliar mechanism of the corals may be held responsible for the settlement success of these species in south Atlantic [72], thus favoring the colonisation of turbid waters or facilitating prey capture. In addition, all species recorded in this study form massive colonies (high metabolic rates), that acclimatize more effectively to environmental changes than those with low metabolic rates [73]. This ability is partly due to these coral skeletons having a high absorbance of solar ultraviolet radiation [74], which seems to be crucial for the success of corals in the tropics. Therefore, it is likely that the coralline fauna from northern Bahia displays evolutionary modifications in behavior, morphology and physiology, enabling them to acclimate to changing climatic conditions [775]. However, despite some efforts in the last decade [76], [77], [78], [79] the taxonomy of Brazilian corals has not been fully addressed, and a detailed taxonomic review is required to verify the distinctiveness of these endemics, including data on molecular biology and ecology, endosymbionts and behavior.

As reviewed by Jokiel and Coles [80], individual coral colonies living in high temperature environments (in our study, F.gravida and S.stellata also exist in hot reef top pools), can survive and photosynthesize at temperatures a few degrees higher than their congeners in lower temperature environments [56], [12]. Depending upon the area, they tolerate sustained temperatures of 30°C for several weeks [81], [82], or 32–34°C from several days to a few weeks [83]. Therefore, according to Clausen and Roth [84], many species are able to acclimate physiologically to increased temperatures, a suggestion validated by recent studies [85], [86] as well as by the response displayed by F. gravida and S. stellata, which seemed quite resistant to the elevated temperatures recorded in northern Bahia during the ENSO period. However, even endemic species (M.hispida and M.harttii) or widely distributed [87], disease resistant [88] corals, such as P.astreoides, succumbed to excessive and prolonged periods of warming, such as the strong 1997–8 ENSO followed by the 1999–2000 strong La Niña-related conditions of increased rainfall and therefore increased runoff of terrestrial nutrients [34]. No significant step change in the studied community was noticed between 2001–2005 when thermal anomalies varying from 0.25°C to 0.75°C were reported for the coast of Bahia [26], nor during the 2009–10 ENSO that caused bleaching in another regions [89]. This reinforces the idea of heat-adaptability [86], [90] and that the studied corals are locally adapted to such fluctuations [27], [38]. There are evidences that exposure to high levels of photosynthetically active radiation (PAR) [91] or ultraviolet radiation (UVR) are damaging the coral community [92], [93]. Therefore, we suggest that abnormally prolonged high temperature changes [85], [90], [94] associated with increased intense exposure to solar radiation [91] and subsequent mortality should be held responsible for the significant loss of density, observed in this study.

It has also been suggested that increased water flow causes coral bleaching and all its consequences (for Montastraea annularis; [95], [96]), but this does not seem a contributory mechanism in Bahia as there was no significant change in water flow in the region of the studied reefs. Additionally, although fine scale data on such water quality parameters were not available, we have no indication that other factors causing coral bleaching, disease or mortality, such as pollution or viruses, were influencing Bahian reefs during the studied period. Our data, and BIOENV analysis performed in previous studies [34], [46], supports our hypothesis that the large-scale impacts of the 1997–8 ENSO on these reefs are linked with factors additional to the abnormally high seawater temperatures. These included reduced cloud cover and increased clarity of the water due to reduced land runoff, resulting in increased levels of solar radiation reaching the reefs, which has been reported to have negative effects on corals ([91], [97], [98], [99] and many others).

Finally, rapid evolution, including differentiation into new species, may occur in corals with large genetic variability, relatively short life spans, and limited back crossing with older individuals [56]. Potts and Garthwaite [100] suggested that these attributes in Caribbean species of Porites are responsible for their apparently rapid evolution during late Quaternary time. However, the impact on Porites from the change in the environment associated with the 1997–8 ENSO, followed by the strong 1999–2000 La Niña, was so severe that the entire local population died out in 2000 and the species remained unrecorded for seven years. Conversely, it has been stated that Porites is not as susceptible as other genera to heat-light stress-induced mortality [101], [102], and that their gene expression patterns are responsible to stress, rendering them to a consistent reliable indicator [103]. This reinforces the idea that the coral fauna from Northern Bahia, mostly endemic relics, are more locally adapted to the natural environmental stress than any other species, even the genus Porites that has a wide distribution across the Atlantic.

Supporting Information

Table S1.

Total density (140 m-2) per year of the corals from the reefs of interest.

https://doi.org/10.1371/journal.pone.0065073.s001

(DOCX)

Acknowledgments

We thank all FK students for their help and assistance. Gratitude is expanded to S.Moraes, R.Gomes and C.B.Castro for encouragement of this research for a number of years.

Author Contributions

Analyzed the data: FK MJA. Contributed reagents/materials/analysis tools: FK MJA. Wrote the paper: FK MJA. Coordinated the overall research objectives and organised the sampling, identification of organisms and data collation throughout the survey, developed sampling methodology, input information on species biology and wrote the paper: FK. Led data analysis and interpretation and wrote the paper: MJA.

References

  1. 1. McPhaden MJ (1999a) El-Niño - The child prodigy of 1997–98. Nature 398: 559–561.
  2. 2. Mo KC, Hakkinen S (2001) Decadal variations in the tropical South Atlantic and linkages to the Pacific. Geoph Res Lett 28: 2065–2068.
  3. 3. Eakin CM (2001) A tale of two ENSO events: carbonate budgets and the influence of two warming disturbances and intervening variability, Uva Island, Panama. Bull Mari Sci 69: 171–186.
  4. 4. McPhaden MJ (1999b) Climate oscillations - Genesis and Evolution of the 1997–98 El-Niño. Sci 283: 950–954.
  5. 5. Enfield DB (2001) Evolution and historical perspective of the 1997–1998 El Niño-Southern Oscillation event. Bull Mar Sci 69: 7–25.
  6. 6. Elliot JR, Jewson SP, Sutton RT (2001) The impact of the 1997/98 El Nino event on the Atlantic Ocean. Jour Clim 14: 1069–1077.
  7. 7. Pezzi LP, Cavalcanti IFA (2001) The relative importance of ENSO and tropical Atlantic sea surface temperature anomalies for seasonal precipitation over South America: a numerical study. Clim Dyn 17: 205–212.
  8. 8. Berkelmans R, De’ath G, Kininmonth S, Skirving WJ (2004) A comparison of the 1998 and 2002 coral bleaching events on the Great Barrier Reef: spatial correlation, patterns, and predictions. Coral Reefs 23: 74–83.
  9. 9. Lee T, McPhaden MJ (2010) Increasing intensity of El-Niño in the central-Equatorial Pacific. Geophys Res Lett 37: L14603 Doi:10.1029/2010GL044007.
  10. 10. Dunbar RB (2000) Clues from corals. Nature 407: 956–959.
  11. 11. Hansen DV (1990) Physical aspects of the El-Niño events of the 1982–1983. In: Glynn, PW (editor) Global ecological consequences of the 1982–1983 El-Niño Southern Oscillation. Elsevier. P.1–21.
  12. 12. Glynn PW, Matt JL, Baker AC, Calderon MO (2001) Coral bleaching and mortality in Panama and Ecuador during the 1997–1998 El Niño Southern Oscillation event: Spatial/Temporal patterns and comparison with the 1982–1983 event. Bull Mar Sci 69: 79–109.
  13. 13. Evangelista H, Godiva D, Sifeddine A, Leão ZMAN, Rigozo NR, et al. (2007) Evidences linking ENSO and coral growth in the Southwestern-South Atlantic. Clim Dyn 29: 869–880 DOI:––– 10.1007/S00382–007–0271–8.
  14. 14. Rodrigues RR, Haarsma R, Campos EJD, Ambrizzi T (2011) The Impacts of Inter–El Niño Variability on the Tropical Atlantic and Northeast Brazil Climate. J Clim 24: 3402–3422.
  15. 15. Laurance WF, Dell B, Turton SM (2011) The 10 Australian ecosystems most vulnerable to tipping points. Biol Conserv 144: 1472–1480.
  16. 16. Glynn PW (1991) Coral reef bleaching un the 1980s and possible connectiuns with global warming. Trends Ecology 6: 175–179.
  17. 17. Goreau TF, Hayes RM (1994) Coral bleaching and ocean ‘hot spot’. Ambio 23: 176–180.
  18. 18. McPhaden MJ (1999) Genesis and evolution of the 1997–1998 El Niño. Science 283: 950–954.
  19. 19. Wilkinson C, Hodgson G (1999) Coral reefs and the 1997–1998 mass bleaching and mortality. UNESCO. Nat Res 35: 16–25.
  20. 20. Goreau TF, McClanahan T, Hayes RM, Strong A (2000) Conservation of coral reefs after the 1998 coral bleaching event. Cons Biol 14: 5–15.
  21. 21. Kelmo F, Attrill MJ, Jones MB (2006) Mass mortality of coral reef ascidians following the 1997/1998 El Niño event. Hydrobiologia 555: 231–240.
  22. 22. McClanahan TR, Maine JM, Muthiga NA (2011) Associations between climate stress and coral reef diversity in the western Indian Ocean. Glob Change Biol 17: 2023–2032.
  23. 23. Burt J, Bartholomew A, Usseglio P (2008) Recovery of corals a decade after a bleaching event in Dubai, United Arab Emirates. Mar Biol 154: 27–36.
  24. 24. Berkelmans R, Oliver JK (1999) Large-scale bleaching of corals on the Great Barrier Reef. Coral Reefs 18: 55–60.
  25. 25. Celliers L, Schleyer MH (2002) Coral bleaching on high-latitude marginal reefs at Sodwana Bay, South Africa. Mar Pollut Bull 44: 1380–1387.
  26. 26. Leão ZMZN, Kikuchi RKP, Oliveira MDM (2008) Coral bleaching in Bahia reefs and its relation with sea surface temperature anomalies. Biota Neotrop 8(3):http://www.biotaneotropica.org.br/v8n3/pt/abstract?articlebn00808032008 (in Portuguese).
  27. 27. Kelmo F, Attrill MJ, Jones MB (2003) Effects of the 1997/98 El Niño on the cnidarian community of a high turbidity coral reef system (Northern Bahia, Brazil). Coral Reefs 22: 541–550.
  28. 28. Luiz OJ, Mandin JS, Robertson DR, Rocha LA, Wirtz P et al. (2011) Ecological traits influencing range expansion across large oceanic dispersal barriers: insights from tropical Atlantic reef fishes. Proc R Soc B. DOI: https://doi.org/10.1098/rspb.2011.1525.
  29. 29. Floeter SR, Rocha LA, Robertson DR, Joyeux JC, Smith-Vaniz WFet al (2008) Atlantic reef fish biogeography and evolution. J Biogeogr 35: 22–47.
  30. 30. Glynn PW (1988a) El Niño-Southern Oscillation 1982–1983: nearshore population, community, and ecosystem responses. Ann Rev Ecol Syst 19: 309–345.
  31. 31. Glynn PW (1988b) Coral bleaching and mortality in the tropical eastern pacific during the 1982–83 El Niño warming event. In: J Ogden, R Wicklund, editors. Mass bleaching of coral reefs in Caribbean: A research strategy. NOAA’s Undersea Research Program. St. Croix, US Virgin Islands Research reports. 42–45.
  32. 32. Nolasco MC, Leão ZMAN (1986) The carbonate buildups along the northern coast of the State of Bahia, Brazil. In:Rabassa, J. (ed), Quaternary of South America and Antarctic Peninsula. Balkema Publishers, The Netherlands, 159–190.
  33. 33. Leão ZMAN, Kikuchi RKP, Maia MP, Lago RAL (1997) A catastrophic coral cover decline since 3000 years B.P., Northern Bahia, Brazil. In: Proceedings of the 8th International Coral Reef Symposium. Panama. 583–588.
  34. 34. Kelmo F, Hallock P (2013) Responses of foraminiferal assemblages to ENSO climate patterns on bank reefs of northern Bahia, Brazil: A 17-year record. Ecol Indic 30: 148–157 DOI:https://doi.org/dx.doi.org/10.1016/j.ecolind.2013.02.009 35.
  35. 35. Bittencourt ACSP, Dominguez JML, Martin L, Silva IR (2000) Patterns of Sediment Dispersion Coastwise the State of Bahia – Brazil. An Acad Bras Cienc 72, 271–287.
  36. 36. Kumar A, Wang WQ, Hoerling MP, Leetmaa A (2001) The sustained North American warming of 1997 and 1998. J Clim 14, 345–353.35.
  37. 37. Peixinho S, Peso-Aguiar MC (1989) Marine sponges as biomonitors: an ecological approach at Todos os Santos Bay, Bahia, Brazil. In: Proc Int Workshop on Biomonitors, MARC UFBA, London. 128–132.
  38. 38. Kelmo F, Attrill MJ (2001) Cnidarian community structure of coastal reefs from northern Bahia, Brazil. Bull Mar Sci 69: 547–557.
  39. 39. Clarke KR, Warwick RM (1994) Change in marine communities: an approach to statistical analysis and integration. Natural Environment Research Council, Swindon, UK. 144 p.
  40. 40. Bray JR, Curtis JT (1957) An ordination of the upland forest communities of southern Wisconsin. Ecol Monogr 27: 325–349.
  41. 41. Carr MR (1996) Plymouth Routines in Multivariate Analysis. Primer User Manual. Natural Environment Research Council, Swindon, UK. 45 p.
  42. 42. Clarke KR (1993) Non-parametric multivariate analysis of changes in community structure. Aust J Ecol 18: 117–143.
  43. 43. Clarke KR, Ainsworth M (1993) A method of linking multivariate community structure to environmental variables. Mar Ecol Prog Ser 92: 205–219.
  44. 44. Clarke KR, Green RH (1988) Statistical design and analysis for a ‘biological effects’ study. Mar Ecol Prog Ser 46: 213–226.
  45. 45. Kelmo F, Attrill MJ, Gomes RCT, Jones MB (2004) El Niño induced local extinction of coral reef bryozoan species from Northern Bahia, Brazil. Biol Conserv 118: 609–617.
  46. 46. Kelmo F, Attrill MJ, Jones MB (2006) Mass mortality of coral reef ascidians following the 1997/1998 El Niño event. Hydrobiologia 555: 231–240.
  47. 47. Attrill MJ, Kelmo F, Jones MB (2004) Impact of the 1997–8 El Niño event on the coral reef-associated echinoderm assemblage from Northern Bahia, NE Brazil. Clim Res 26: 151–158.
  48. 48. Attrill MJ, Kelmo F (2007) Opportunistic responses of Diadema antillarum (Echinodermata: Echinoidea) populations following the 1997–98 El Niño event in Bahia, Brazil. Est Coast Shelf Sci 73: 243–248.
  49. 49. Leão ZMAN, Kikuchi RKP, Oliveira MDM, Vasconcellos V (2010) Status of Eastern Brazilian coral reefs in time of climate changes. Pan-American Jour Aquat Sci 5(2): 224–235.
  50. 50. Linden O (1999) Coral mortality in the tropics: Massive causes and effects. Ambio 27: 588.
  51. 51. Aronson R, Pecht W, MacIntyre IG, Murdoch TT (2000) Coral reef bleach-out in Belize. Nature 405: 36.
  52. 52. Migotto AE (1997) Anthozoa bleaching on the southeastern coast of Brazil in the summer of 1994. Proceedings of the 6th Coelenterate Biology 1995: 329–335.
  53. 53. Castro CB, Pires DO (1999) A bleaching event on a Brazilian coral reef. Rev Bras Oceanogr 47(1): 87–90.
  54. 54. Wilkinson C, Hodgson G (1999) Coral reefs and the 1997–1998 mass bleaching and mortality. UNESCO. Nat Res 35: 16–25.
  55. 55. Lo-Yat A, Simpson SD, Meekans M, Lecchini D, Martinez E, et al. (2011) Extreme climatic events reduce ocean productivity and larval supply in a tropical reef ecosystem. Global Chan Biol 17: 1695–1702.
  56. 56. Glynn PW (1993) Coral reef bleaching: ecological perspectives. Coral Reefs. 12: 1–17.
  57. 57. Brown BE, Ogden JC (1993) Coral bleaching. Sci Am. January: 44–50.
  58. 58. Glynn PW, D’Croz L (1990) Experimental evidence for high temperature stress as the cause of El Niño-coincident coral mortality. Coral Reefs. 8: 181–191.
  59. 59. Goreau TJ, Macfarlane AH (1990) Reduced growth rate of Montastrea annularis following the 1987–1988 coral bleaching event. Coral Reefs. 8: 211–215.
  60. 60. Szmant AM, Gassman NJ (1990) The effects of prolonged “bleaching” on tissue biomass and reproduction of the reef coral Montastrea annularis. Coral Reefs 8: 217–224.
  61. 61. Borell EM, Yuliantri AR, Bischof K, Richter C (2008) The effect of heterotrophy on photosynthesis and tissue composition of two scleractinian corals under elevated temperature. J Exp Mar Biol ecol 364: 116–123.
  62. 62. Anthony KRN, Kline DI, Diaz-Pulido G, Dove S, Hoegh-Guldberg O (2008) Ocean acidification causes bleaching and productivity loss in coral reef builders. Proc Natl Acad Sci USA 105: 17442–17446.
  63. 63. Godinot C, Houlbrèque F, Grover R, Ferrier-Pagès C (2011) Coral uptake of inorganic phosphorus and nitrogen negatively affected by simultaneous changes in temperature and pH. PLoS ONE 6(9): e25024 DOI:https://doi.org/ 10.1371/journal.pone.00250024.
  64. 64. Bruno JF, Siddon CE, Witman JD, Colin PL (2001) El-Niño related coral bleaching in Palau, Western Caroline Islands. Coral Reefs 20: 127–136.
  65. 65. Lindahl ULF, Ohman MC, Schelten CK (2001) The 1997/1998 mass mortality of corals: Effects of fish communities on Tanzania Coral Reef. Mar Pollut Bull 42(2): 127–131.
  66. 66. Wilkinson C (1998) Status of Coral Reefs of the world. Australian Institute of Marine Science. Townsnville. Internal Report.
  67. 67. McClanaham TR (2000) Bleaching damage and recovery potential of Maldivian coral reefs. Mar Pollut Bull 40(7): 587–597.
  68. 68. Bernal-Sotelo C, Acosta A (2012) The relationship between physical and biological habitat conditions and hermatypic coral recruits abundance within insular reefs (Colombian Caribbean). Rev Biol Trop 60(3): 995–1014.
  69. 69. Green DH, Edmunds PJ, Carpenter RC (2008) Increasing relative abundance of Porites astreoides on Caribbean reefs mediated by an overall decline in coral cover. Mar. Ecol. Progr. 359: 1–10.
  70. 70. Kramer PA (2003) Synthesis of coral reef health indicators for the Western Atlantic: results of the AGRRA program (1997–2000). Atoll. Res. Bull. 496: 1–57.
  71. 71. Erftemeijer PLA, Riegl B, Hoeksema B, Todd P (2012) Environmental impacts of dredging and other sediment disturbances on corals: a review. Mar Pollut Bull 64: 1737–1765.
  72. 72. Leão ZMAN, Ginsburg RN (1997) Living reefs surrounded by siliciclastic sediments: the Abrolhos coastal reefs, Bahia, Brazil. Proceedings of the 8th International Coral Reef Symposium. Panama. 2: 1767–1772.
  73. 73. Gates RD, Edmunds PJ (1999) The physiological mechanisms of acclimatization in tropical reef corals. Am Zool 39: 30–43.
  74. 74. Reef R, Kaniewska P, Hoegh-Guldberg O (2009) Coral skeletons defend against ultraviolet radiation. Plos One 4: e7995.
  75. 75. Yakob L, Mumby PJ (2011) Climate change induces demographic resistance to disease in novel coral assemblages. Proc Natl Acad Sci 108: 1967–1969.
  76. 76. Neves EG, Andrade SCS, Silveira FL, Solferine VN (2008) Genetic variation and population structuring in two brooding coral species (Siderastrea stellata and Siderastrea radians) from Brazil. Genetica 132: 243–254.
  77. 77. Nunes F, Fukami H, Vollmer SV, Norris RD, Knowlton N (2008) Re-evaluation of the systematics of the endemic corals of Brazil by molecular data. Coral Reefs 27: 423–432.
  78. 78. Nunes F, Norris RD, Knowlton N (2009) Implications of isolation and low genetic diversity in peripheral populations of an amphi-Atlantic coral. Mol Ecol 18: 4283–4297.
  79. 79. Nunes FLD, Norris RD, Knowlton N (2011) Long Distance Dispersal and connectivity in Amphi-Atlantic Corals at Regional and Basin Scales. PLoS ONE 6(7): e22298 DOI:https://doi.org/10.1371/journal.pone.0022298.
  80. 80. Jokiel PL, Coles SL (1990) Response of Hawaiian and other Indo Pacific reef corals to elevated temperature. Coral Reefs 8: 155–162.
  81. 81. Coles SL, Jokiel PL, Lewis CR (1976) Thermal tolerance in tropical versus subtropical Pacific reef corals. Pac Sci 30: 159–166.
  82. 82. Coles SL, Jokiel PL (1977) Effects of temperature on photosynthesis and respiration in hermatypic corals. Mar Biol 43: 209–216.
  83. 83. Coles SL (1988) Limitations on reef coral development in the Arabian Gulf: temperature or algal competition? Proceedings of the 6th International Coral Reef Symposium, Townsville. Australia 3: 211–216.
  84. 84. Clausen CD, Roth AA (1975) Effect of temperature and temperature adaptation on calcification rate in the hermatypic coral Pocillopora damicornis. Mar Biol 33: 93–100.
  85. 85. Kvitt H, Rosenfeld H, Zandbank K, Tchernov D (2011) Regulation of apoptotic pathways by Stylophora pistillata (Anthozoa, Pocilloporidae) to survive thermal stress and bleaching. Plos ONE 6: e28665.
  86. 86. Riegl BM, Purkis SJ, Al-Cibahy AS, Abdel-Moati MA, Hoegh-Guldberg O (2011) Present Limits to Heat-Adaptability in Corals and Population-Level Responses to Climate Extremes. PLoS ONE 6: e24802.
  87. 87. Veron JEN (2000) Corals of the world. Australian Institute of Marine Science. 3: 1382.
  88. 88. Palmer CV, McGinty ES, Cummings DJ, Smith SM, Bartels E, et al. (2011) Patterns of coral ecological immunology: variation in the responses of Caribbean corals to elevated temperature and a pathogen elicitor. J Exp Biol 214: 4240–4249.
  89. 89. Vargas-Angel B, Looney EE, Vetter OJ, Coccagna EF (2011) Severe, widespread El Niño associated coral bleaching in the US Phoenix Islands. Bull Mar Scie 87: 623–638.
  90. 90. Pernice M, Dunn SR, Miard T, Dufour S, Dove A, et al. (2011) regulation of apoptotic mediators reveals dynamic responses to thermal stress in the reef building coral Acropora Millepora. Plos One 6: e16095.
  91. 91. Fitt WK, Brown BE, Warner ME, Dunne RP (2001) Coral bleaching: interpretation of thermal tolerance limits and thermal thresholds in tropical corals. Coral Reefs 20: 51–65.
  92. 92. Aranda M, Banaszak AT, Bayer T, Luyten JR, Medina M at al (2011) Differential sensitivity of coral larvae to natural levels of ultraviolet radiation during the onset of larval competence. Mol Ecol 20: 2955–2972.
  93. 93. Nesa B, Baird AH, Harii S, Yakovleva I, Hidaka M (2012) Algal symbionts increase DNA damage in coral planulae exposed to sunlight. Zool Stud 51: 12–17.
  94. 94. Gleason D, Hofmann DK (2011) Coral larvae: from gametes to recruits. J Exp Mar Biol Ecol 408: 42–57.
  95. 95. Carpenter LW, Patterson MR (2007) Water flow influences the distribution of photosynthetic efficiency within the scleractinian Montastrea annularis (Ellis and Solander, 1786). Can water flow modulate coral reef bleaching? J Exp Mar Biol Ecol 351: 10–26.
  96. 96. Carpenter LW, Patterson MR, Bromage ES (2010) Water flow influences the spatiotemporal distribution of heat shock protein 70 within colonies of the scleractinian coral Montastrea annularis (Ellis and Solander, 1786) following heat stress: implications for coral bleaching. J Exp Mar Biol Ecol 387: 52–59.
  97. 97. Shick M, Lesser MP, Jokiel PL (1996) Effects of ultraviolet radiation on corals and other coral reef organisms. Glob Chang Biol 2: 527–545.
  98. 98. Lyons MM, Aas P, Pakulski JD, Van-Waasbergen L, Miller RV, et al. (1998) DNA damage induced by ultraviolet radiation in coral-reef microbial communities. Mar Biol 130: 537–543.
  99. 99. Häder DP, Helbing EW, Williamson CE, Worrest RC (2011) Effects of UV radiation on aquatic ecosystems and interactions with climate change. Photoch Photobiol Sci 10: 242–260.
  100. 100. Potts DC, Garthwaite RL (1991) Evolution of reef-building corals during periods of rapid global change. In: Dudley EC, editor. The unity of evolutionary biology. Syst Evol Biol 170–178.
  101. 101. Marshall PA, Baird AH (2000) Bleaching of corals on the Great Barrier Reef: differential susceptibilities among taxa. Coral Reefs 19: 155–163.
  102. 102. Brandt ME (2009) The effect of species and colony size on the bleaching response of the reef-building corals in the Florida Keys during the 2005 mass bleaching event. Coral Reefs 28: 911–924.
  103. 103. Kenkel CD, Aglyamova G, Alamaru A, Bhagooli R, Capper R (2011) Development of gene expression. Markers of acute heat-light stress in reef-building corals of the genus Porites. PLoS ONE 6: e26914.