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Phenotypic Variance Predicts Symbiont Population Densities in Corals: A Modeling Approach

  • Robert van Woesik ,

    rvw@fit.edu

    Affiliation Department of Biological Sciences, Florida Institute of Technology, Melbourne, Florida, United States of America

  • Kazuyo Shiroma,

    Affiliation Department of Biological Sciences, Florida Institute of Technology, Melbourne, Florida, United States of America

  • Semen Koksal

    Affiliation Department of Mathematical Sciences, Florida Institute of Technology, Melbourne, Florida, United States of America

Phenotypic Variance Predicts Symbiont Population Densities in Corals: A Modeling Approach

  • Robert van Woesik, 
  • Kazuyo Shiroma, 
  • Semen Koksal
PLOS
x

Abstract

Background

We test whether the phenotypic variance of symbionts (Symbiodinium) in corals is closely related with the capacity of corals to acclimatize to increasing seawater temperatures. Moreover, we assess whether more specialist symbionts will increase within coral hosts under ocean warming. The present study is only applicable to those corals that naturally have the capacity to support more than one type of Symbiodinium within the lifetime of a colony; for example, Montastraea annularis and Montastraea faveolata.

Methodology/Principal Findings

The population dynamics of competing Symbiodinium symbiont populations were projected through time in coral hosts using a novel, discrete time optimal–resource model. Models were run for two Atlantic Ocean localities. Four symbiont populations, with different environmental optima and phenotypic variances, were modeled to grow, divide, and compete in the corals under seasonal fluctuations in solar insolation and seawater temperature. Elevated seawater temperatures were input into the model 1.5°C above the seasonal summer average, and the symbiont population response was observed for each location. The models showed dynamic fluctuations in Symbiodinium populations densities within corals. Population density predictions for Lee Stocking Island, the Bahamas, where temperatures were relatively homogenous throughout the year, showed a dominance of both type 2, with high phenotypic variance, and type 1, a high-temperature and high-insolation specialist. Whereas the densities of Symbiodinium types 3 and 4, a high-temperature, low-insolation specialist, and a high-temperature, low-insolation generalist, remained consistently low. Predictions for Key Largo, Florida, where environmental conditions were more seasonally variable, showed the coexistence of generalists (types 2 and 4) and low densities of specialists (types 1 and 3). When elevated temperatures were input into the model, population densities in corals at Lee Stocking Island showed an emergence of high-temperature specialists. However, even under high temperatures, corals in the Florida Keys were dominated by generalists.

Conclusions/Significance

Predictions at higher seawater temperatures showed endogenous shuffling and an emergence of the high-temperature Symbiodinium specialists, even though their phenotypic variance was low. The model shows that sustaining these “hidden” specialists becomes advantageous under thermal stress conditions, and shuffling symbionts may increase the corals' capacity to acclimatize but not adapt to climatechange–induced ocean warming.

Introduction

The ubiquity of modern reef-building corals in the shallow, low-nutrient tropical environments stems from their capacity to house unicellular dinoflagellates [1]. This mutually beneficial relationship depends on photosynthates that are released by the symbionts and utilized by the coral host; corals, in turn, produce organic wastes upon which the symbionts thrive [2], [3]. Coral symbionts, or Symbiodinium species, were once thought to consist of only one species [4]. However technological advances show potentially hundreds of symbiont types [5][9], and some preliminary research has shown that coral physiology is highly dependent on the type of symbionts present in the host [10][13].

Most corals seem very specific in the type of Symbiodinium they support, and most corals only support one Symbiodinium type over time [14][16]. Still, some coral species are capable of simultaneously supporting more than one Symbiodinium population, which are spread across coral colonies in accordance with down-welling irradiance [17], [18]. Symbiodinium population densities are not, however, in a steady state. Population densities vary in accordance with seasonal temperature, irradiance and nutrient concentrations [19][24]. Recently, Chen et al. [23] demonstrated seasonal dynamics in the relative densities of different Symbiodinium types, presumably upregulating the high-light, high-heat tolerant species in summer. Several key studies have also shown seasonal declines in photosynthetic efficiency that is related to high seawater temperature and irradiance [25], [26]. Corals pale, or bleach, when temperatures exceed seasonal averages for extended periods [27]. An extreme case-in-point is the 1997–98 global thermal stress event, which was an extreme manifestation of a more general impact of the El Niño-Southern Oscillation cycle. This event led to extreme coral bleaching and extensive coral mortality worldwide [28].

Symbiotic scleractinian corals live close to their thermal tolerance levels. The last two decades have seen an increase in the frequency and severity of symbiotic dysfunction (i.e., coral bleaching) in response to anomalous sea-surface temperature increases [29][33]. Yet, symbiont responses vary in accordance with the type of stress [3]. If temperature and irradiance stresses are of moderate intensity and duration, corals are capable of regaining pigmentation, both through increases in Symbiodinium pigment and population densities [34]. If stress exceeds a critical threshold, which varies among coral species and geographic locality [35], [36], [10], bleaching is inevitable, often leading to partial or whole-colony mortality [37][39].

Contemporary molecular-ecology research is interested in the dynamics of Symbiodinium in corals, their response to thermal stress events [40][42], and what role the Symbiodinium might play in acclimatization and adaptation of reef corals [43]. We note that the present study is only applicable to those corals, approximately 25% of corals worldwide [16], that naturally have the capacity to support more than one type of Symbiodinium within the lifetime of a colony, for example Montastraea annularis and Montastraea faveolata.

Models

Ware et al. [44] devised a mathematical model to examine Symbiodinium population growth during and after thermal stress events using generalized Lotka-Volterra competition equations. Although Ware's model predicts the superior Symbiodinium type, the system is set such that the differential equation that governs Symbiodinium type 1 (), the first equation in the set, will ultimately dominate the entire system. The model does not consider resources for which Symbiodinium species compete. We sought to examine the response of Symbiodinium population densities to the seasonal dynamics of solar insolation (a resource) and seawater temperature.

Recent research on adaptation to climate change and increasing thermal stresses has emphasized the need to assess phenotypic variance of organisms in general [45], [46] and corals in particular [43], [47]. We test whether the phenotypic variance of symbionts may be closely related with the capacity of Montastraea corals to acclimatize to increasing seawater temperatures. Moreover, we assess whether more specialist symbionts are lost from the coral (holobiont) under a warming ocean. The objectives are to obtain accurate time-course predictions of Symbiodinium population densities in Montastraea corals, and make valid estimates, of Symbiodinium densities, under seasonal dynamics of solar insolation and seawater temperature, and through thermal stress events.

Materials and Methods

Symbiont-Population Growth

Growth of each Symbiodinium population can be modeled by considering specific growth rates relative to specific loss rates. Population flux can be theoretically estimated (following Jones and Yellowlees [48]) using the difference equation:

(1)where is the population density of Symbiodinium (or zooxanthellae) type i, is the specific growth rate of , and is the specific loss rate of from the host coral at time (Table 1). An assumption of the model is that the resources allocated to each Symbiodinium population influences , and that down-welling solar insolation is the primary resource limiting symbiont population densities (see Table 2 for other assumptions). We note that high insolation, in early summer, leads to photoinhibition and reductions in symbiont population densities. Furthermore, increasing nutrients can have the opposite effect of increasing symbiont densities [49], [22], [14]. But nutrient concentrations are far less predictable than insolation and temperature [50], and are therefore not input into our model. Where nutrient concentrations (X) are available, then X can be defined as a function of time f(t), and inserted as a resource in Equation 3 (below).

Symbiodinium population densities were predicted for corals at Lee Stocking Island (23°N, 76°W) and Key Largo (24°N, 80°W) using solar insolation () (kW m−2 d−1) as a primary resource at each location using the general equation:

(2)where is solar insolation at time t, and ai, bi, and were locality specific coefficients, while temperature is not a resource, but rather a condition. From satellite data [51], ten-year averages of solar insolation and sea surface temperature were used to derive functions with respect to time (Figure 1). For simplicity, annual change in Sea Surface Temperature (in °C) followed the same general construct, replacing with in Equation 2 and the parameters were changed appropriately for each location.

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Figure 1. Dynamics of 10-year seasonal means of Sea Surface Temperature (SST) (solid line) and Solar Insolation (SI) (dashed line).

Panel (a) shows the dynamics for Lee Stocking Island, the Bahamas, and panel (b) shows the dynamics for Key Largo, Florida.

http://dx.doi.org/10.1371/journal.pone.0009185.g001

Competition for Resources

An average Symbiodinium is generally no more than 10 µm diameter, and 106 Symbiodinium cells can fit in 1 cm2 of coral tissue depending on tissue thickness, which can vary from 0.3 to 10 mm depending on the coral species under examination. Deeper Symbiodinium receive less light than surface Symbiodinium. Since solar insolation is the primary resource considered here, the resource becomes limiting with an increase in Symbiodinium density. Therefore, Symbiodinium proliferation rate, , (following Tilman et al. 1997 [52]) can be described as a function of time:

(3)where is a constant coefficient; is the primary resource (here solar insolation (t)); is the total number of Symbiodinium cm−2; and is the carrying capacity within the host corals. While this model examines changes in symbiont dynamics over time, it is equally appropriate to examine micro-environmental profiles, such as those reported in Rowan et al. [17]. Partitioning coral colonies into different micro-irradiance environments, for example, would be equally valid.

The specific growth rate, , of Symbiodinium is given as:

(4)where is the resource allocation to Symbiodinium proliferation at time (derived in Equation 3); is the resource requirement for ; and are optimal proliferation requirements (following Pulliam 2000 [53]) of with regard to solar insolation (SI) and sea surface temperature (SST); and are standard deviations of SI and SST (Figure 2a); and C2 is a constant coefficient. For each Zi, was set to 1, with all Symbiodinium showing equal competitive abilities for resources. If physiological studies find otherwise, Ri can be set hierarchically, with the most competitive Symbiodinium type set at i = 1, and the most inferior type set at i = n. Dynamics of the sustainable Symbiodinium density for each Zi in host corals are expressed by:

(5)

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Figure 2. Symbiodinium growth and loss rate response curves in relation to Sea Surface Temperature (SST) and Solar Insolation (SI).

Panel (a) shows specific growth rates of four Symbiodinium types, and panel (b) shows specific loss rates.

http://dx.doi.org/10.1371/journal.pone.0009185.g002

Because no data are available to the contrary, excess symbionts relative to , are assumed to be lost from the host corals randomly and independent of Symbiodinium type. The specific Symbiodinium loss rate is:

(6)where C3 is a constant coefficient (Figure 2b).

Population-Density Predictions

To predict Symbiodinium population densities, the following conditions were applied to the models:

  1. values of were 5.5/28, 5.5/26.5, 4.5/28, and 4.5/26.5, for each , respectively, which covers the range of solar insolation and seawater temperature probabilities for the Florida Keys and the Bahamas (using the units °C for sea surface temperature and kW m−2 d−1 for solar insolation) (Figure 2);
  2. the standard deviations for were 0.4, 0.8, 0.4 and 0.8 for each , respectively (Figure 2) – we define Symbiodinium types 1 and 3 as specialists because they have narrow environmental tolerances;
  3. the standard deviations for were 0.4, 1, 0.4 and 1 for each , respectively – again, Symbiodinium types 1 and 3 are defined as specialists because they have narrow environmental tolerances;
  4. and for the holobionts, were 5.5 and 27 for SI and SST respectively;
  5. standard deviations for and were 2.0 and 3.0, respectively;
  6. each Symbiodinium type had an initial population density of 1.0×106 cells cm−2;
  7. each month was set at 30 days, and one year was set at 360 days;

Since Equation 1 is a discrete time model, the solutions (i.e., population densities) were approximated in discrete time (10 yr) by numerical iteration. The SIiopt and SSTiopt (values for condition 1 above) and the values for the standard deviations (for conditions 2 and 3 above), were derived from normal distributions for each zooxanthellae type for each iteration step (with mean, μ, and the standard deviation, σ, of the distributions given in conditions 1 and 2, respectively). To introduce real-world thermal stress, Symbiodinium populations were randomly subjected to +1°C above-average temperatures in July, +1.5°C in August, and +1°C in September. The results were compared with a 4-year study, which tagged host corals and regularly monitored Symbiodinium types and their densities from 2000 to 2004, in Key Largo, Florida, and Lee Stocking Island, the Bahamas [41].

Results and Discussion

Seasonal Dynamics

Symbiodinium densities varied seasonally, showing highest densities from December to April; extreme solar insolation and temperature conditions induced high in summer for both localities (Figures 2, 3). Symbiodinium dynamics were more variable in Key Largo, Florida, than at Lee Stocking Island, the Bahamas (Figure 3). Predictions for Lee Stocking Island, the Bahamas, where temperatures were relatively homogenous throughout the year, showed a dominance of Symbiodinium type 2, which had high phenotypic variance, and a type 1 high-temperature and high-insolation specialist (type 1). The densities of Symbiodinium types 3 and 4 remained consistently low (Figure 3). In contrast, predictions for Key Largo, Florida, where environmental conditions were more seasonally variable, showed the co-dominance of two Symbiodinium populations (types 2 and 4), both with high phenotypic variance. The specialist symbionts, types 1 and 3, with low phenotypic variance, were present but in very low densities (Figure 3). At elevated temperatures, population densities showed endogeneous ‘shuffling’ at both sites and an emergence of types 1 and 3, the high-temperature specialists, with low phenotypic variance, at Lee Stocking Island (Figure 4). In contrast, the elevated temperatures allowed types 2 and, somewhat less of, type 4 to remain dominate in Key Largo corals, with extremely low densities of types 1 and 3 specialists (Figure 4).

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Figure 3. Ten-year iterations of four Symbiodinium population densities in corals modeled at two Caribbean localities.

The models were run with C1 = 0.01, and R1 =  R2 = R3 = R4 = 1. Panel (a) shows the results for Lee Stocking Island, the Bahamas and panel (b) shows the results for Key Largo, Florida.

http://dx.doi.org/10.1371/journal.pone.0009185.g003

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Figure 4. Ten-year iterations of four Symbiodinium population densities in corals that have been subjected to above-average water temperature increases.

Where panel (a) represents predictions for Lee Stocking Island, the Bahamas, subjected to above-average temperatures of +1°C July, +1.5°C August, +1°C September; and panel (b) represents predictions for Key Largo, Florida, subjected to the same above average temperatures.

http://dx.doi.org/10.1371/journal.pone.0009185.g004

In 2006, Thornhill et al. [41] noted that Symbiodinium in Montastrea annularis and Montastrea faveolata varied in accordance with locality and depth. They also showed a 2–3 year changeover from one symbiont to another in certain shallow colonies from Florida, and that M. annularis and M. faveolata supported more Symbiodinium types in Key Largo than the same hosts at Lee Stocking Island. Therefore the Thornhill et al. [41] study and the present (modeling) study agree; Key Largo corals support more Symbiodinium types than Lee Stocking Island. Thornhill et al. [41] attributed these differences to six potential factors, including environmental variation and human impacts. We suggest insolation and temperature differences between the sites may have the same effect. More interesting, however, was that both studies showed high symbiont diversity directly following extreme thermal stress, followed by stability and reduced diversity. In 2009, Thornhill and colleagues [42] showed that while the 2005 bleaching event caused compositional changes in Montastrea annularis and M. faveolata symbiont populations, they noted that the recovered genotypes were consistent with the population prior to the thermal stress. Furthermore, they demonstrated remarkable endemism and specificity within host corals. Clearly thermal stress events trigger within-host instability, which may equilibrate through time under more optimal conditions. Still, an increase in the frequency and intensity of disturbance may cause a more ‘permanent’ state of instability.

Limits

The present model uses a Gaussian distribution to represent environmental optimality. There is no information in the literature confirming or denying such a distribution, although it seems reasonable based on numerous plant-physiology studies [53]. Empirical studies may be best directed at examining physiological variance of Symbiodinium in relation to temperature, irradiance and nutrient concentrations. Yet, phenotypic variance may be best expressed as log-normal distributions (i.e., geometric normal) [Gingerich 54]. Similarly, the model assumed random, non-selective Symbiodinium loss; selective loss may also follow a Gaussian distribution, but more studies are needed to test this premise. Loss and recovery rates may even follow different distribution functions. For example, loss may follow a continuous exponential or a Weibull distribution, with loss decreasing over time after a threshold is exceeded, while recovery may follow a normal distribution that incorporates a lag-phase. Such adjustments are highly dependent on the outcomes of much needed physiological studies examining in hospite responses of Symbiodinium to environmental conditions and extremes.

Some studies have clearly shown that Symbiodinium population dynamics are influenced by nutrient concentrations [21]. Incorporating nutrient dynamics (in the water column) into the model will require a different approach, especially considering the volatility of many nutrient species and their unpredictability in the environment [50]. A more threshold-based response model may be required to reasonably estimate Symbiodinium populations with respect to nutrient dynamics. For example, seasonal extremes (i.e., wet and dry seasons), and event-driven nutrient concentrations may be best input as functions of time (in Equation 3). We input optimality at slightly different parameters; however, theoretically, multiple types of symbionts can also coexist in the same niche space, especially in benign environments where there are no differences between intra- and inter-specific competition [55][57]. Although Hutchinson [58] and Huston [59] argued for enhanced diversity at environmentally dynamic localities, because competitive displacement is prevented, the present model predicts that several Symbiodinium populations are likely to be present in locations where the physical environment is benign. We add that diversity depends on the phenotypic variance of the populations and highly dynamic localities are less likely to support specialist Symbiodinium types.

Adjustment Capacity

None of the Symbiodinium types 1–4 reached zero densities after 10 years, although some densities were extremely low (<1 cell cm−2), well below in situ levels of detectability (∼5%, which was the state-of-the-art in 2005) [15], [42]. The model showed possibilities of potentially endogenous shifts in the relative abundance of Symbiodinium populations, especially under thermal stress. This hidden, vestigial component may be non-adaptive but could become useful when conditions change, especially on reefs away from large land masses. Field studies show that survival through a thermal-stress event, of the multi-claded Stylophora pistillata on the Great Barrier Reef, is directly related to whether hosts harbor resistant symbionts [63]. Therefore, sustaining these ‘hidden’ specialists becomes advantageous under thermal stress conditions because the coral holobiont is pre-adapted to thermal stress. In other words, corals harboring multiple symbionts may a have a greater capacity to acclimate to environmental change, but only if those symbionts include thermally tolerant types. Corals harboring thermally sensitive symbionts are rapidly selected out of the gene pool through elevated temperature anomalies [63]. This contrasts with the suggested need to derive novel symbionts from the environment, implied by the adaptive-bleaching hypothesis [60][62].

But acclimation reaches a ‘dead end’ under extreme environmental stress; populations can only adjust by evolving – or adapting to the new environment. In principle, a population can adapt to gradual environmental change depending on the amount of genetic variation within a population. But because evolution is the outcome of the interaction between (i) genetic variation, and (ii) natural selection, the capacity to adapt is often limited by the first step – the capacity of a population to produce enough variation upon which selection can act [63]. The second step, in a rapidly changing environment, is ubiquitous and a natural consequence of selective pressure by the environment [64]. Is it then reasonable to assume that corals supporting multiple-species symbionts would have the genetic material to potentially become more thermally tolerant, conceivably adjusting to rapid climate change scenarios, compared with more extinction prone reef corals that strictly support only one specialist Symbiodinium type? No. Certainly the multi-symbiont hosts may have a greater capacity to acclimate, but only if they harbor temperature resistant symbionts [65]. There is no evidence that these multi-symbiont hosts have an advantage in their capacity to adapt. Adaptation requires new material, generated through recombination and mutation. Furthermore, a series of independent molecular studies have shown clear evidence of symbiont endemicity [7], [41], [42], suggesting (i) that new symbiont-coral relationships are unlikely in the short term, and (ii) shuffling symbionts is not a mechanism by which corals can adapt to rapidly warming oceans, but it is a useful acclimation mechanism.

Acknowledgments

We sincerely thank Sandra van Woesik and Todd Lajeunesse for comments on the manuscript.

Author Contributions

Conceived and designed the experiments: RvW. Performed the experiments: RvW KS. Analyzed the data: RvW KS SK. Wrote the paper: RvW KS.

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