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Sci Rep. 2017; 7: 44101.
Published online 2017 March 10. doi:  10.1038/srep44101
PMCID: PMC5345069

Cumulative effects of suspended sediments, organic nutrients and temperature stress on early life history stages of the coral Acropora tenuis


Coral reproduction is vulnerable to both declining water quality and warming temperatures, with simultaneous exposures likely compounding the negative impact of each stressor. We investigated how early life processes of the coral Acropora tenuis respond to increasing levels of suspended sediments in combination with temperature or organic nutrients. Fertilization success and embryo development were more sensitive to suspended sediments than to high temperatures or nutrient enrichment, while larval development (after acquisition of cilia) and settlement success were predominantly affected by thermal stress. Fertilization success was reduced 80% by suspended sediments, and up to 24% by temperature, while the addition of nutrients to suspended sediments had no further impact. Larval survivorship was unaffected by any of these treatments. However, settlement success of larvae developing from treatment-exposed embryos was negatively affected by all three stressors (e.g. up to 55% by suspended sediments), while exposure only during later larval stages predominantly responded to temperature stress. Environmentally relevant levels of suspended sediments and temperature had the greatest impacts, affecting more processes than the combined impacts of sediments and nutrients. These results suggest that management strategies to maintain suspended sediments at low concentrations during coral spawning events will benefit coral recruitment, especially with warming climate.

Increasing levels of turbidity and sedimentation are contributing to coral reef degradation worldwide1,2 and are a major concern for environmental managers3. The introduction, resuspension and deposition of sediments in coastal marine ecosystems can be caused by natural factors (e.g., waves and currents, river discharges) or human activities (e.g., dredging, or enhanced terrestrial runoff of sediments due to coastal development, deforestation or poor agricultural practices). Once reaching the ocean, the fate of newly imported sediments depends on their grain size and geochemical properties4. Large particles are frequently deposited near the river mouth, whereas fine particles (i.e., silts and clays) either flocculate or are deposited, but can also easily be resuspended, traveling 10’s of km from the source to reach inshore and mid-shelf coral reefs5,6.

Since European settlement in 1850, the development of Australia’s North Queensland catchments adjacent to the Great Barrier Reef (GBR) has led to significant changes in the quantity and quality of water discharging into the GBR lagoon7,8. Expansion of agriculture, clearing of vegetation and grazing have led to widespread soil erosion which together with increasing fertilizer application have increased river discharges of sediments, dissolved and particulate organic and inorganic nutrients, and trace elements5,7,9. Modelled estimates indicate that the mean annual loads of sediments delivered to the GBR lagoon have increased 5.5-fold since 1850 to 14,000 ktonnes yr−1 7. Correspondingly, mean annual total nitrogen loads have increased 5.7 times to 66,000 tonnes yr−1, and mean annual phosphorus loads have increased 8.9 times to 14,000 tonnes yr−1 7.

River discharges from catchments with significant cropping area are characterised by high concentrations of dissolved and particulate inorganic nutrients, especially nitrogen and phosphorus7. Inorganic nutrients from anthropogenic sources generally only persist in the GBR lagoon for periods of days to weeks9, as they are rapidly taken up by microbial and phytoplankton communities. They are then transformed into organic matter and undergo complex cycling between particulate and dissolved organic and inorganic forms and undergo repeated deposition-resuspension events9,10. Particulate organic nutrients reduce water clarity, stimulate microbial communities that exude mucopolysaccharides11 and form aggregates with sediments, thereby contributing to biological oxygen demand12, causing oxidative stress at the sediment/seawater interface. Organically-enriched sediments are known to increase the detrimental effects of turbidity and sedimentation on the physiology and survival of corals2. Decreased light availability for photosynthesis13, which reduces calcification14, productivity and growth rates, increases partial mortality, and disrupts the Symbiodinium-coral symbiosis2,15, are among the more serious effects that nutrient enriched sediments have on adult corals.

In addition to stress induced by elevated concentrations of sediments and nutrients, inshore coral reefs are exposed to increasing sea surface temperatures (SST) during the summer monsoonal periods16, compromising the health and replenishment of hard coral populations17. Since the beginning of the 20th century, SST has risen by a global average of ~1 °C18 and is projected to increase by a further 2 to 3 °C by the end of the century under a moderate Representative Concentration Scenario of the Intergovernmental Panel on Climate Change (IPCC RCP 4.519). Such increases in SST alone would endanger many coral species, which typically live close to their upper thermal tolerance limits20. It has been hypothesized that the effects of high temperatures on adult corals are ameliorated when co-occurring with suspended sediments due to reductions in light irradiance levels through shading and the provision of alternative food resources by suspended particles21,22.

The early life-history stages of corals are particularly susceptible to water quality and climate pressures23,24, and a clear understanding of the cumulative effects of these stressors on these life stages is critically important for management initiatives aimed at maintaining the resilience of reef communities25,26. Most scleractinian corals are broadcast-spawners, simultaneously releasing buoyant eggs and sperm into the water column for external fertilization27. Spawning and larval development of the majority of species on the GBR takes place in early austral summer (October to December)28, and can coincide with nutrient discharges typically driven by major river flood events during the summer monsoonal wet season (October to April)29. Heat stress, floods and wind-driven resuspension events of sediments can therefore co-occur and overlap with broadcast spawning, placing the sensitive early life history stages of hard corals (gametes, embryos, larvae and recruits) at risk. Despite the perception that early life history stages of corals are more sensitive to environmental change and pollution than adult stages2, few studies have empirically addressed their susceptibility to individual and multiple co-occurring pressures30,31,32,33,34,35,36,37.

To fill this knowledge gap, we conducted controlled experiments to examine the effects of suspended sediments, with and without nutrient enrichment, and at different temperatures, on gamete fertilization, larval survival and larval settlement of the broadcast spawning coral Acropora tenuis. Experiments were designed to mimic the impact of environmentally-relevant concentrations of suspended sediments originating from runoff events29, dredging23 or coastal activities38 under two different scenarios: i) elevated temperatures typical of those experienced during summer months16, and ii) nutrients typical of those produced by agricultural or coastal development activities39 that promote plankton blooms10,40. Results enabled the identification of differences in the sensitivity of processes that take place during the early life history stages of A. tenuis to single and combined effects of suspended sediments, nutrient enrichment and temperature, and allowed us to explore their potential implications for inshore coral reefs exposed to river floods, dredging and high temperatures.


Monitoring suspended sediment, temperature and nutrient enrichment treatments

Suspended sediments remained at or very near the 5 targeted levels (0, 5, 10, 30 and 100 mg l−1), and seawater temperature at the 3 targeted levels (27, 30 and 32 °C) throughout four experiments (Supplementary Material Tables S1, S2, S3, S4 and S5). Organic nutrients [derived from inshore plankton and added to filtered seawater (FSW) to produce 3 levels of enrichment (+0, +0.3, and +0.6 mg organic carbon l−1 FSW], increased concentrations of multiple nutrients and trace elements in environmentally relevant stoichiometric ratios (Supplementary Material Table S6). Nutrient concentrations varied after incubations and among experiments, therefore the terms ‘low’, ‘medium’ and ‘high’ nutrient enrichment are used to indicate the addition of +0, +0.3, and +0.6 mg OC l−1 FSW.

Experiment 1: Effects of cumulative stress conditions on gamete fertilization

At suspended sediment concentrations <10 mg l−1, mean fertilization success was high (70 ± 21%, mean ± s.d.) across all nutrient and temperature combinations (Fig. 1). In the absence of nutrient enrichment, the highest suspended sediment concentration (100 mg l−1) reduced fertilization by 59% compared to controls (pSuspended sediments = <0.001, Table 1, Fig. 1a). The addition of nutrients and their interaction with suspended sediments had no significant effect on fertilization success (pNutrient enrichment = 0.113, pSuspended sediments and nutrient enrichment = 0.329, Table 1, Fig. 1a). Increases in suspended sediments and temperature both had significant detrimental effects on fertilization success (pSuspended sediments = <0.001, pTemperature = 0.039, Table 1, Fig. 1b). No interactive effects were observed (pSuspended sediments and temperature = 0.588, Table 1, Fig. 1b), indicating that when eggs were simultaneously exposed to elevated suspended sediments and temperature, impacts on fertilization were additive on a log scale. Declines in fertilization success for independent stressors in comparison to the controls ranged from ~24% in the high temperature treatment (32 °C) to 80% in the high suspended sediments treatment (100 mg l−1 suspended sediments). Thus suspended sediments had a greater impact on fertilization success than temperature (Supplementary Material Table S7). Suspended sediments and temperature in combination resulted in a ~89% decline in fertilization in comparison to control conditions. The concentration of suspended sediments that caused fertilization success to be reduced by 50% (IC50) decreased ~2-fold (from 37 to 18 mg l−1 suspended sediments, Supplementary Material Fig. S8, Table S9) as temperatures were increased from 27 to 32 °C.

Figure 1
Percentage fertilization success for eggs of Acropora tenuis exposed to five levels of suspended sediments (0, 5, 10, 30 and 100 mg l−1) and either (a) nutrient enrichment [3 levels: low (open circles), medium (grey circles), high ...
Table 1
Treatment effects on processes occurring during early life history stages of Acropora tenuis.

Experiment 2: Larval settlement after embryo and larval exposures to cumulative stress conditions

Exposure of 8-h to 36 hours old embryos during 28 hours to suspended sediments, in combination with either elevated temperatures or nutrient enrichment, during their embryological and larval development did not compromise their survivorship between the age of 36 h and settlement on day 5 (p > 0.05 for all factors and interactions, Table 1, Supplementary Material Table S7). On average, 95 ± 6% of larvae survived across all treatments in the suspended sediment and nutrient enrichment treatments, and 84 ± 15% survived in the suspended sediments and temperature treatments.

Settlement was significantly reduced for embryos exposed to high suspended sediments, temperature or nutrient enrichment (p < 0.001 for all individual factors Table 1, Fig. 2, Supplementary Material Table S7). None of the interactions were significant (p > 0.05 for both interactions, Table 1, Fig. 2, Supplementary Material Table S7), indicating that the responses of larvae exposed as embryos simultaneously to these cumulative stressors were additive on a log scale. Suspended sediments reduced settlement by up to 43 and 55% (at 100 mg l−1 of suspended sediments at either high nutrient enrichment or 32 °C respectively), nutrient enrichment reduced settlement by up to 33% (Fig. 2a), while temperature reduced settlement by up to 14% (Fig. 2b). Under both combinations of factors, suspended sediments had the greatest effect on larval settlement (Supplementary Material Table S7). The concentration of suspended sediments that caused a reduction in larval settlement by 50% (IC50) decreased with elevated nutrients and temperatures (Supplementary Material Fig. S8, Table S9). A ~5-fold decrease in IC50 (from suspended sediments >100 to 18 mg l−1) was obtained when nutrient levels increased from low to high enrichment levels (Supplementary Material Fig. S8, Table S9), while temperature caused a ~1.5-fold decrease in IC50 (from suspended sediments 29 to 20 mg l−1) with increasing temperature (from 27 to 32 °C, Supplementary Material Fig. S8, Table S9).

Figure 2
Percent larval settlement success for Acropora tenuis after 8-h old embryos were reared for 28 h (until ciliated) in a suspended sediment treatment (0, 5, 10, 30 or 100 mg l−1) combined with either (a) nutrient enrichment ...

Experiment 3: Larval survivorship and settlement following exposure of 3-d old larvae to cumulative stress conditions

On average, high proportions of 3-d old ciliated larvae survived the 48 h treatment exposures (97 ± 4% in the highest suspended sediment and nutrient enrichment treatments; 84 ± 22% in the highest suspended sediment and temperature treatments). Overall, there were no significant effects of suspended sediments, nutrient enrichment or temperature on larval survivorship (p > 0.05 for each individual factors and interaction, Table 1, Supplementary Material Table S7).

In contrast, subsequent larval settlement success was affected by high temperatures (pTemperature = 0.003, Table 1, Fig. 3a, Supplementary Material Table S7), reducing it by 18% at 32 °C in comparison to control conditions. Neither suspended sediments nor nutrient enrichment, nor the combination of these two pressures had a significant effect on larval settlement (p > 0.05 for both factors and their interaction, Table 1, Supplementary Material Table S7).

Figure 3
(a) Settlement of 3-d old larvae previously exposed for 48 h to combined suspended sediments (0, 5, 10, 30 or 100 mg l−1) and contrasting temperature (27, 30, or 32 °C) treatments (Experiment 3). After the ...

Experiment 4: Larval settlement of 5-d old larvae under cumulative stress conditions

Mean settlement success of 5-d old larvae decreased significantly when exposed to elevated temperature (pTemperature= 0.001, Table 1, Fig. 3b, Supplementary Material Table S7), whereas settlement success was not affected by suspended sediments or nutrient enrichment, nor by interactions between any of these three factors (p > 0.05 for both factors and all interactions, Table 1, Supplementary Material Table S7). The maximum settlement success (74 ± 16%) was obtained at 27 °C, while the minimum success (57 ± 19%) was observed at 32 °C, decreasing by 23% at the highest temperature in comparison to control conditions.

Comparison of the effects of suspended sediments, temperature and nutrient enrichment among processes occurring in early life stages of A. tenuis

The effects of suspended sediments and temperature on key processes in early life history stages of A. tenuis were additive (i.e., interactions were not significant), when both factors had a significant effect (Table 1). Similarly, the effects of suspended sediments and nutrient enrichments were additive when both factors were significant (Table 1). Fertilization success and larval settlement when embryos were exposed to treatments during part of their development were the most affected processes, with suspended sediments causing the greatest impacts (Fig. 4a). Nutrient enrichment only affected settlement when larvae had previously been exposed to stress levels during part of their embryo development (Fig. 4b), and effect sizes were modest compared with those caused by suspended sediments. Temperature affected more processes (Fig. 4c: fertilization, settlement when embryos and larvae were exposed to elevated temperatures) than the other pressures, but the sizes of these effects were less than those caused by suspended sediments (Fig. 4a). Overall, the combination of suspended sediments aggravated by high temperatures posed the greatest risk to population replenishment of A. tenuis, since more processes were affected by these two stressors, and their effects were additive.

Figure 4
Comparative impacts of these three stressors on processes occurring during the early life history processes of Acropora tenuis exposed to: (a) suspended sediments (0, 5, 10, 30 or 100 mg l−1), and either high nutrients or high ...


This study illustrates that developmental processes occurring during the early life history stages of Acropora tenuis differ considerably in their sensitivity to increasing levels of suspended sediments, nutrient enrichment and temperature. Fertilization and embryo development were more sensitive to suspended sediments than to high temperatures and nutrient enrichment, while larval development (following cilia acquisition) and settlement were only affected by thermal stress. No significant interactions were detected when early life history stages were exposed to two stressors simultaneously, for any of the processes evaluated, indicating additivity of responses when more than one factor had a significant effect. The effects of suspended sediments, nutrient enrichment and temperature were most pronounced on processes occurring during (i) the earliest life history stages (fertilization and embryo development), when cell division, specialization and embryo development takes place41, and (ii) larval settlement and the metamorphosis of motile larvae to sessile polyps, which involves extensive tissue remodeling42. These results suggest that environmentally realistic elevated levels of suspended sediments or high temperatures during the nights of spawning can have considerable negative impacts on the reproductive success of A. tenuis. Unfavorable conditions due to local (i.e., wind, waves, currents, flooding or dredging) or global (i.e., ocean warming) factors that increase suspended sediments and temperatures during the narrow time window when gamete fertilization, embryo development and larval settlement occur could result in reduced reproductive success of A. tenuis populations for that year.

Studies examining the effects of suspended sediments on coral gamete fertilization have reported decreases in fertilization success for several species30,43,44,45. The primary mechanism has recently been described for A. tenuis, whereby sperm coagulates with suspended particles, lowering sperm concentrations in the vicinity of eggs, hence reducing the number of sperm-egg encounters and subsequently reducing fertilization success45. The silt-clay sediments used in the present study are extremely cohesive and colloidal due to their physical and chemical characteristics (e.g. small grain sizes), readily forming flocs6 that are likely to attract and capture coral sperm, explaining their observed impact on fertilization success.

The effects of high temperatures on fertilization success reported here are consistent with previous studies that documented reduced fertilization success under elevated temperatures46,47. The mechanisms involved may include a reduced sperm flagella motility, which would reduce the number of sperm-egg interactions46, or impairment of biochemical processes involved in early cell division48. Nutrient enrichment had no significant effect on fertilization success in this study. Detrimental effects of nutrient enrichment on fertilization success of A. tenuis after exposure to combined nutrient enrichment and temperature stress have previously been reported34. However, the only nutrient treatments that were common between studies (suspended sediments: 0 mg l−1, temperature: 27 °C, nutrient enrichment: low, medium and high) had no significant effects on fertilization success in either study (Supplementary Material Table S10).

Larval survivorship was the only process that was not affected by the exposure to the treatments, even when exposures occurred before they developed cilia (8 to 36-h old). However, larval settlement success was significantly reduced when embryos were exposed to suspended sediments, revealing the latent effects that treatments can have on later developmental processes. A possible mechanism by which suspended sediments act on coral embryo development has recently been described35, whereby sediments cause the production of mucus by early embryos (~6-24-h old) of A. tenuis and A. millepora; however, that study did not detect subsequent effects on larval survivorship or settlement35. A difference between the two studies was that carbonate sediments were used in ref. 35, with an order of magnitude lower total organic carbon content than the silt-clay based sediments used in this study. Furthermore, studies are only comparable if similar embryo ages, sediment types and exposure times are investigated. Our results suggest that stressors that affect cellular function, increase energy demands, or cause mechanical abrasion during embryo development may be negative for larval settlement.

Past studies of larval settlement under conditions of sediment deposition indicate that sedimentation can mask settlement cues, obstruct settlement substrata and smother recruits (reviewed in ref. 23). Therefore, most recruits are found on vertical and downward facing surfaces or on the walls of cracks in the substrata in sediment-rich environments49,50. Since field studies record coral recruitment over time frames varying from several weeks up to 12 months after spawning51, it has remained unresolved whether suspended sediments reduce settlement or decrease post-settlement survivorship2,52. Our results show that under experimental conditions, high concentrations of suspended sediments (i.e., 100 mg l−1) do not affect larval survival and settlement success if sediments are not allowed to accumulate on the available substrata. However, although there may be no direct effect of high turbidity on settlement, sediment deposition is likely to reduce the availability of suitable substrata and lower overall settlement and recruitment success53,54.

Suspended sediments together with temperature were the factors that affected the greatest number of reproductive processes for hard corals and had the greatest proportional impacts on most early life stages. In addition, the co-occurrence of temperature with suspended sediments reduced thresholds for suspended sediments impacts (IC50). Similarly, elevated sediments are likely to affect thermal thresholds for early coral stages (unless these impacts are ameliorated by shading, which is uncertain for aposymbiotic gametes and larvae). These experiments were conducted under highly controlled conditions in the National Sea Simulator, allowing us to confidently assign responses to stress treatment. However, directly translating these results to field situations should be done with caution, as conditions in the field are far less consistent and may be complicated by additional factors that can affect the reproductive and recruitment process (i.e., waves, pH, salinity30,55,56,57).

Since ocean warming affects marine ecosystems at a global scale, management strategies should be directed towards minimizing dredging activities in coastal areas during periods of coral spawning, and improving water quality (i.e., suspended sediments) associated with river discharges, in order to maintain population replenishment success in inshore reefs. Assessing the risks associated with the simultaneous effects of suspended sediments and high temperatures on inshore reefs of the GBR requires further studies to determine the impacts of other sediment types in combination with temperature stress on thresholds for sensitive early life stages of corals and other tropical species. These climate-adjusted thresholds could then be incorporated into improved spatial models in order to generate effective risk maps for identification of vulnerable habitats and opportunities for management intervention.

Our results confirm that high levels of suspended sediments during periods of coral spawning affect the final reproductive success of A. tenuis, and indeed, are likely to affect the reproductive success of the majority of reef-building corals, which are broadcasters that release gametes synchronously during a few nights each year. We found that a high concentration of suspended sediments in the presence of high temperatures was the most detrimental combination of stressors. The effects of suspended sediments and high temperatures are likely to further increase in magnitude and change from additive to synergistic if co-occurring with additional stressors56 (e.g., organic nutrient enrichment58). Complex interactions among cumulative stressors are becoming more common on inshore reefs affected by local and global stressors3, and pose a significant risk for maintaining successful reproductive output required for ongoing replenishment of hard coral populations.

Materials and Methods

Obtaining coral gametes

Colonies of the broadcast spawning coral Acropora tenuis (Dana, 1846) were collected at ~6 m depth, from Davies Reefs (18°48′53′′S, 147°38′03′′E) and Esk Island (18°45′52′′S, 146°31′05′′E), both in the central mid-shelf region of the Great Barrier Reef. Gravid colonies were collected a few days before coral spawning under the permit G12/35236. Colonies were maintained in outdoor flow-through, temperature-controlled aquaria, set at the ambient seawater temperature recorded on the day of collection (27 °C), in the National Sea Simulator (SeaSim) at the Australian Institute of Marine Science (AIMS). Following spawning by seven colonies, eggs were separated from sperm using a 100 μm mesh filter and washed five times in 0.2 μm filtered sea water (FSW), as described by Negri and Heyward59. Gametes separated in this way were used in Experiment 1, while the remainder of the gametes were fertilized and raised in bulk flow-through cultures59 for Experiments 2, 3 and 4.

Preparation of suspended sediments, temperature and nutrient enrichment treatments

Sediments were collected at Orpheus Island (18°36′39′′S, 146°29′18′′E) at 2 m depth, wet-sieved (mean ± s.d. particle size 7.3 ± 1.5 μm, 95% <20 μm) and kept in 60 l tanks with flow-through seawater at 27 °C. Suspended sediment treatments (0, 5, 10, 30 or 100 mg l−1) were prepared through dilution with FSW and adjusted with a nephelometer (TPS 90FL-T). Two replicate Schott bottles (2 l) per treatment, containing the sediments, were incubated for 3 h at the treatment temperatures prior to the start of each experiment (Supplementary Material Table S5).

For the organic nutrient treatments, FSW was enriched with decaying natural inshore plankton and suspended detritus to maintain a realistic stoichiometric composition of nutrients and trace elements. Plankton was collected at reefs around Orpheus Island with a 100-μm plankton net, sieved to remove >26 μm fragments, blended and frozen until use. After determination of total organic carbon (OC) in the stock solution, three nutrient enrichment treatments were prepared with nominal concentrations of +0, +0.3, or +0.6 mg OC l−1 FSW. The nutrients were added to two replicate Schott bottles (2 l) per treatment, which contained the suspended sediments. Bottles were incubated for 48 h at 200 μmol photons m−2 s−1 light intensity (12 h:12 h diurnal cycle) at 27 °C to promote development of natural microbial communities, uptake of bioavailable fraction of inorganic nutrients and their transformation into organic nutrients. Decaying plankton was previously used to study nutrient effects on corals15,34, and incubations were long enough to stimulate microbial community development, uptake of dissolved inorganic nutrients and conversion into organic matter during natural suspension events60,61,62.

Experimental suspended sediment concentrations were within the range of conditions measured on inshore GBR reefs during wind suspension or associated with dredging projects. Concentrations up to 5 mg l−1 occur under calm conditions on inshore reefs63, concentrations between 5–30 mg l−1 are typical after storms and river plumes, and concentrations up to 100 mg l−1 have been recorded close to seafloor dredging activities38,45,64,65. Nutrient enrichment concentrations were based on measurements in the inshore GBR7,39,66 (Table S3).

Control treatments were 0 mg l−1 suspended sediments without addition of OC (+0 mg OC l−1 FSW) at 27 °C. To characterize the different treatments, concentrations of suspended sediments, total organic carbon, dissolved organic carbon, total dissolved phosphorus, dissolved organic nitrogen, total particulate nitrogen, ammonium, phosphate, nitrate and nitrite, were measured once in duplicate subsamples at the end of each incubation in each replicate (Schott bottles). Water samples were analyzed by the Analytical Services laboratory at AIMS following Schaffelke et al.39.

Experiment 1: Effects of cumulative stress conditions on gamete fertilization

To test the impacts of suspended sediments, nutrients and temperature on gamete fertilization, 5 levels of suspended sediments (0, 5, 10, 30 or 100 mg l−1) were combined with either 3 levels of nutrients (+0, +0.3, or +0.6 mg OC l−1 FSW), or 3 levels of temperature (27, 30, or 32 °C) to produce 30 experimental treatments (15 for the suspended sediments and nutrient enrichment experiment; and 15 for the suspended sediments and temperature experiment; Fig. 5). For each treatment combination, twelve replicate 50 ml clear polypropylene chambers were prepared, each containing 25 ml of the modified seawater. Eggs were added to half of the chambers (~200 eggs per chamber), and sperm aliquots to the other half. Chambers were transferred into temperature incubators at the designated temperature (Supplementary Material Table S5). After 30 min, sperm and egg chambers were combined to initiate fertilization, resulting in a total of 180 chambers across the 30 treatments (6 per treatment). The final sperm concentration was 5 × 104 ml−1, being slightly suboptimal for maximum fertilization67, thereby increasing the sensitivity of the assay45,68. Chambers were returned into incubators, and gently shaken every 30 minutes to maintain sediments suspended (Supplementary Material Table S1). When the second cleavage was observed (1.5 h after fertilization), 2 ml of zinc formalin fixative (Z-fix preservative, Anatech Limited) were added to terminate embryo development. Fertilization success (proportion of eggs fertilized, Supplementary Material Table S11) was assessed under a stereomicroscope.

Figure 5
Experiments performed with early life history stages of Acropora tenuis exposed to suspended sediments (SS: 0, 5, 10, 30 or 100 mg l−1) in combination with either (a) a nutrient enrichment treatment (low, medium, high), or (b) ...

Experiment 2: Larval settlement after embryo and larval exposures to cumulative stress conditions

Embryos fertilized under control conditions were exposed to the 30 treatment combinations from the early gastrula stage (8-h old) until they were ciliated larvae (~36-h old; Fig. 5). Six water baths (400 l) were used to maintain seawater temperatures (Supplementary Material Table S2). For each treatment, four replicate experimental systems (Supplementary Material S12 and Fig. S13) were set up and ~250 embryos added to each experimental tank. Suspended sediment concentrations were derived from turbidity readings taken every 6 h in each experimental tank (Supplementary Material Table S2). After 28 h larvae were transferred to six-well polystyrene tissue culture plates (NuncTM, Denmark) maintained at 27 °C in a temperature-controlled room. Each well contained 10 ml FSW at 27 °C and 10 larvae (n = 12 wells for each suspended sediment and nutrient enrichment combination, and n = 24 wells for each suspended sediment and temperature combination). When larvae where 5-d old, 2-mm2 chips of live crustose coralline algae (CCA) Porolithon onkodes were added to induce larval settlement69. After 24 h, the number of settled larvae in each well was recorded (Supplementary Material Table S11).

Experiment 3: Larval survivorship and settlement following exposure of 3-d old larvae to cumulative stress conditions

For each of the 30 treatment combinations, six replicate 100 ml clear polystyrene chambers were prepared containing 80 ml of the appropriately modified seawater and 3-d old larvae (n = 20 larvae per replicate, Fig. 5). Chambers were placed in mechanical rollers to keep sediments suspended (Supplementary Material Table S3). Rollers were kept in temperature incubators to maintain target temperatures (Supplementary Material Table S5). Larvae were exposed to treatment conditions for 48 h, with one water change after 24 h. After exposure, larvae from each replicate were counted and transferred to six-well polystyrene tissue culture plates (NuncTM, Denmark, n = 6 replicate wells per treatment, n = 10 larvae per well). CCA chips were added to each well and settlement success was assessed after 24 h (Supplementary Material Table S11).

Experiment 4: Larval settlement of 5-d old larvae under cumulative stress conditions

The experimental setup from Experiment 2 was used to expose 5-d old larvae to each of the 30 treatment combinations (Fig. 5, Supplementary Material Tables S4, S5). Larvae (n = 150) were added to each experimental tank, which also contained 15 aragonite substrata (~20 mm diameter) previously conditioned with CCA (Supplementary Material S12 and Fig. S13). The aragonite plugs were suspended in the experimental tanks, with the CCA-colonized surface facing downwards to prevent sediment accumulation. After 24 h, the number of settlers per plug was assessed under a stereomicroscope (Supplementary Material Table S11).

Data analysis

Generalized linear models (GLM) were used to assess changes in fertilization success, larval survivorship and settlement as a function of the three fixed factors: suspended sediments (numerical factor: 0, 5, 10, 30 or 100 mg l−1), nutrient enrichment (categorical factor: low, medium or high organic nutrients) or temperature (categorical factor: control, low stress or moderate stress). Quasi-binomial errors and the log-link function were used when the model had overdispersion. All calculations were conducted using the package lme4 in R (R Development Core Team, 2016).

Data were further analyzed when more than one factor was significant (GLM), using nonlinear regression curves (four-parameter logistic models) using GraphPad Pism (v.7), to derive effective concentration point intercepts (i.e. EC50 values) for the various treatment combinations70. All curves were tested for normality of the residuals and a replicate test was applied to assess goodness-of-fit. Absolute EC50 values were determined using a four-parameter logistic model. All models were interpolated to 50% of the ‘top’ (EC50) of the control temperature (27 °C) or control nutrient concentration (low) treatments. In Experiment 2, 95% confidence intervals could not be determined for larval settlement success in the medium nutrient enrichment treatment because of ambiguity in the estimation of parameters.

Additional Information

How to cite this article: Humanes, A. et al. Cumulative effects of suspended sediments, organic nutrients and temperature stress on early life history stages of the coral Acropora tenuis. Sci. Rep. 7, 44101; doi: 10.1038/srep44101 (2017).

Publisher's note: Springer Nature remains neutral with regard to jurisdictional claims in published maps and institutional affiliations.

Supplementary Material

Supplementary Material:


We would like to thank Catia de Carvalho, Florita Flores, Marion Hliscs, Heidi Luter, Helios Martinez, Sam Noonan, Joy Smith, and the staff of the National Sea Simulator (AIMS Townsville) for assistance with experimental work. This study was funded by the Australian Institute of Marine Science and the Australian Government’s National Environmental Research Program and the Australian Government’s National Environmental Science Programme. The funders had no role in study design, data collection and analysis, decision to publish, or preparation of the manuscript. Adriana Humanes also expresses gratitude for financial support from AIMS@JCU, and to the Australian Research Council for support through AusAID.


The authors declare no competing financial interests.

Author Contributions A.H., B.L.W., K.E.F. and A.P.N. designed the study, A.H. and G.F.R. performed the study, A.H. and G.F.R. analyzed the data with input from B.L.W., K.E.F. and A.P.N. A.H., with contribution from all other authors, wrote the manuscript.


  • Erftemeijer P. L., Riegl B., Hoeksema B. W. & Todd P. A. Environmental impacts of dredging and other sediment disturbances on corals: a review. Marine Pollution Bulletin 64, 1737–1765 (2012). [PubMed]
  • Fabricius K. E. Effects of terrestrial runoff on the ecology of corals and coral reefs: review and synthesis. Marine Pollution Bulletin 50, 125–146 (2005). [PubMed]
  • Great Barrier Reef Marine Park Authority. Great Barrier Reef Outlook Report 2014. (Great Barrier Reef Marine Park Authority, Townsville, 2014).
  • Storlazzi C. D., Norris B. K. & Rosenberger K. J. The influence of grain size, grain color, and suspended-sediment concentration on light attenuation: why fine-grained terrestrial sediment is bad for coral reef ecosystems. Coral Reefs 34, 967–975 (2015).
  • Devlin M. J. & Brodie J. Terrestrial discharge into the Great Barrier Reef Lagoon: nutrient behavior in coastal waters. Marine Pollution Bulletin 51, 9–22 (2005). [PubMed]
  • Bainbridge Z. T., Wolanski E., Alvarez-Romero J. G., Lewis S. E. & Brodie J. E. Fine sediment and nutrient dynamics related to particle size and floc formation in a Burdekin River flood plume, Australia. Marine Pollution Bulletin 65, 236–248 (2012). [PubMed]
  • Kroon F. J. et al. . River loads of suspended solids, nitrogen, phosphorus and herbicides delivered to the Great Barrier Reef lagoon. Marine Pollution Bulletin 65, 167–181 (2012). [PubMed]
  • McCulloch M. et al. . Coral record of increased sediment flux to the inner Great Barrier Reef since European settlement. Nature 421, 727–730 (2003). [PubMed]
  • Brodie J. et al. . Dispersal of suspended sediments and nutrients in the Great Barrier Reef lagoon during river-discharge events: conclusions from satellite remote sensing and concurrent flood-plume sampling. Marine and Freshwater Research 61, 651–664 (2010).
  • Grossart H. P. & Ploug H. Microbial degradation of organic carbon and nitrogen on diatom aggregates. Limnology and Oceanography 46, 267–277 (2001).
  • Angly F. E. et al. . Marine microbial communities of the Great Barrier Reef lagoon are influenced by riverine floodwaters and seasonal weather events. PeerJ, e1511 (2016). [PMC free article] [PubMed]
  • Murphy J. W. & Richmond R. H. Changes to coral health and metabolic activity under oxygen deprivation. PeerJ 4, e1956 (2016). [PMC free article] [PubMed]
  • Anthony K. R. N., Ridd P. V., Orpin A. R., Larcombe P. & Lough J. Temporal variation of light availability in coastal benthic habitats: effects of clouds, turbidity, and tides. Limnology and Oceanography 49, 2201–2211 (2004).
  • Marubini F., Barnett H., Langdon C. & Atkinson M. J. Dependence of calcification on light and carbonate ion concentration for the hermatypic coral Porites compressa. Marine Ecology Progress Series 220, 153–162 (2001).
  • Weber M. et al. . Mechanisms of damage to corals exposed to sedimentation. Proceedings of the National Academy of Sciences 109, E1558–E1567 (2012). [PubMed]
  • Lough J. M. Variations of sea-surface temperatures off north-eastern Australia and associations with rainfall in Queensland: 1956–1987. International Journal of Climatology 12, 765–782 (1992).
  • Ban S. S., Graham N. A. J. & Connolly S. R. Evidence for multiple stressor interactions and effects on coral reefs. Global Change Biology 20, 681–697 (2014). [PubMed]
  • Brohan P., Kennedy J. J., Harris I., Tett S. F. B. & Jones P. D. Uncertainty estimates in regional and global observed temperature changes: A new data set from 1850. Journal of Geophysical Research - Atmospheres 111, D12106 (2006).
  • Meissner K. J., Lippmann T. & Sen Gupta A. Large-scale stress factors affecting coral reefs: open ocean sea surface temperature and surface seawater aragonite saturation over the next 400 years. Coral Reefs 31, 309–319 (2012).
  • Berkelmans R. & Willis B. L. Seasonal and local spatial patterns in the upper thermal limits of corals on the inshore Central Great Barrier Reef. Coral Reefs 18, 219–228 (1999).
  • Anthony K. R. N., Connolly S. R. & Hoegh-Guldberg O. Bleaching, energetics, and coral mortality risk: Effects of temperature, light, and sediment regime. Limnology and Oceanography 52, 716–726 (2007).
  • Cacciapaglia C. & van Woesik R. Climate-change refugia: shading reef corals by turbidity. Global Change Biology 22, 1145–1154 (2016). [PubMed]
  • Jones R., Ricardo G. F. & Negri A. P. Effects of sediments on the reproductive cycle of corals. Marine Pollution Bulletin (2015). [PubMed]
  • Hoegh-Guldberg O. et al. . in Climate change and the Great Barrier Reef (eds Johnson J. & Marshall P.) 273–307 (Great Barrier Reef Marine Park Authority, 2007).
  • Harrison P. L. et al. . Mass spawning in tropical reef corals. Science 223, 1186–1189 (1984). [PubMed]
  • Hughes T. P. et al. . Supply-side ecology works both ways: the link between benthic adults, fecundity, and larval recruits. Ecology 81, 2241–2249 (2000).
  • Baird A. H., Guest J. R. & Willis B. L. Systematic and biogeographical patterns in the reproductive biology of scleractinian corals. Annual Review of Ecology, Evolution, and Systematics 40, 551–571 (2009).
  • Babcock R. C. et al. . Synchronous spawnings of 105 scleractinian coral species on the Great Barrier Reef. Marine Biology 90, 379–394 (1986).
  • Devlin M., Waterhouse J., Taylor J. & Brodie J. Flood plumes in the Great Barrier Reef: spatial and temporal patterns in composition and distribution. (Great Barrier Reef Marine Park Authority, Research Publication, Townsville, 2001).
  • Humphrey C., Weber M., Lott C., Cooper T. & Fabricius K. Effects of suspended sediments, dissolved inorganic nutrients and salinity on fertilisation and embryo development in the coral Acropora millepora (Ehrenberg, 1834). Coral Reefs 27, 837–850 (2008).
  • Harrison P. L. & Ward S. Elevated levels of nitrogen and phosphorus reduce fertilization success of gametes from scleractinian reef corals. Marine Biology 139, 1057–1068 (2001).
  • Bassim K. M. & Sammarco P. W. Effects of temperature and ammonium on larval development and survivorship in a scleractinian coral Diploria strigosa. Marine Biology 142, 241–252 (2003).
  • Negri A. P. & Hoogenboom M. O. Water contamination reduces the tolerance of coral larvae to thermal stress. PLoS ONE 6, e19703 (2011). [PMC free article] [PubMed]
  • Humanes A., Noonan S., Willis B. L., Fabricius K. E. & Negri A. P. Cumulative effects of nutrient enrichment and elevated temperature compromise the early life history stages of the coral Acropora tenuis. PLoS ONE 11, e0161616 (2016). [PMC free article] [PubMed]
  • Ricardo G. F., Jones R. J., Clode P. L. & Negri A. P. Mucous secretion and cilia beating defend developing coral larvae from suspended sediments PLoS ONE 11, e0162743 (2016). [PMC free article] [PubMed]
  • Ricardo G. F., Jones R. J., Negri A. P. & Stocker R. That sinking feeling: Suspended sediments can prevent the ascent of coral egg bundles. Scientific Reports 6, 21567 (2016). [PMC free article] [PubMed]
  • Berry K. L., Hoogenboom M. O., Brinkman D. L., Burns K. & Negri A. P. Effects of coal contamination on early life history processes of a reef-building coral, Acropora tenuis. Marine Pollution Bulletin, Accepted (2016).
  • Thomas S., Ridd P. V. & Day G. Turbidity regimes over fringing coral reefs near a mining site at Lihir Island, Papua New Guinea. Marine Pollution Bulletin 46, 1006–1014, doi: (2003).10.1016/s0025-326x(03)00122-x [PubMed] [Cross Ref]
  • Schaffelke B., Carleton J., Skuza M., Zagorskis I. & Furnas M. J. Water quality in the inshore Great Barrier Reef lagoon: Implications for long-term monitoring and management. Marine Pollution Bulletin 65, 249–260, doi: (2012).10.1016/j.marpolbul.2011.10.031 [PubMed] [Cross Ref]
  • Kaltenböck E. & Herndl G. J. Ecology of amorphous aggregations (marine snow) in the Northern Adriatic Sea. IV. Dissolved nutrients and the autotrophic community associated with marine snow. Marine Ecology Progress Series 87, 147–159 (1992).
  • Harrison P. L. & Wallace C. C. in Coral Reefs (Ecosystems of the World; 25) (ed. Dubinsky Z.) 133–207 (Elsevier Science Publishing Company, 1990).
  • Grasso L. C. et al. . The biology of coral metamorphosis: molecular responses of larvae to inducers of settlement and metamorphosis. Developmental Biology 353, 411–419 (2011). [PubMed]
  • Gilmour J. Experimental investigation into the effects of suspended sediment on fertilisation, larval survival and settlement in a scleractinian coral. Marine Biology 135, 451–462 (1999).
  • Erftemeijer P. L. A., Hagedorn M., Laterveer M., Craggs J. & Guest J. R. Effect of suspended sediment on fertilization success in the scleractinian coral Pectinia lactuca. Journal of the Marine Biological Association of the United Kingdom 92, 741–745 (2012).
  • Ricardo G. F., Jones R. J., Clode P. L., Humanes A. & Negri A. P. Suspended sediments limit coral sperm availability. Scientific Reports 5, 18084 (2015). [PMC free article] [PubMed]
  • Omori M., Fukami H., Kobinata H. & Hatta M. Significant drop in fertilization of Acropora corals in 1999: an after effect of coral bleaching? Limnology and Oceanography 46, 704–706 (2001).
  • Negri A. P., Marshall P. A. & Heyward A. J. Differing effects of thermal stress on coral fertilization and early embryogenesis in four Indo Pacific species. Coral Reefs 26, 759–763 (2007).
  • Lam E. K. Y. et al. . High levels of inorganic nutrients affect fertilization kinetics, early development and settlement of the scleractinian coral Platygyra acuta. Coral Reefs 34, 837–848 (2015).
  • Mizrahi D., Navarrete S. A. & Flores A. A. V. Uneven abundance of the invasive sun coral over habitat patches of different orientation: an outcome of larval or later benthic processes? Journal of Experimental Marine Biology and Ecology 452, 22–30 (2014).
  • Doropoulos C., Ward S., Roff G., González-Rivero M. & Mumby P. J. Linking demographic processes of juvenile corals to benthic recovery trajectories in two common reef habitats. PLoS ONE 10, e0128535 (2015). [PMC free article] [PubMed]
  • Humanes A. & Bastidas C. In situ settlement rates and early survivorship of hard corals: a good year for a Caribbean reef. Marine Ecology Progress Series 539, 139–151 (2015).
  • Te F. Effects of two petroleum products on Pocillopora damicornis planulae. Pacific Science 45, 290–298 (1991).
  • Perez r. K., Rodgers K. S., Jokiel P. L., Lager C. V. & Lager D. J. Effects of terrigenous sediment on settlement and survival of the reef coral Pocillopora damicornis. PeerJ 2, e387, doi: (2014).10.7717/peerj.387 [PMC free article] [PubMed] [Cross Ref]
  • Hodgson G. Sediment and the settlement of larvae of the reef coral Pocillopora damicornis. Coral Reefs 9, 41–43 (1990).
  • Chui A. P. Y. & Ang P. Jr Elevated temperature enhances normal early embryonic development in the coral Platygyra acuta under low salinity conditions. Coral Reefs 34, 461–469, doi: (2015).10.1007/s00338-014-1247-x [Cross Ref]
  • Albright R. & Mason B. Projected near-future levels of temperature and pCO2 reduce coral fertilization success. PLoS ONE 8, e56468, doi: (2013).10.1371/journal.pone.0056468 [PMC free article] [PubMed] [Cross Ref]
  • Heyward A. J. & Negri A. P. Turbulence, cleavage, and the naked embryo: a case for coral clones. Science 335, 1064, doi: (2012).10.1126/science.1216055 [PubMed] [Cross Ref]
  • Crain C. M., Kroeker K. & Halpern B. S. Interactive and cumulative effects of multiple human stressors in marine systems. Ecology Letters 11, 1304–1315 (2008). [PubMed]
  • Negri A. P. & Heyward A. J. Inhibition of fertilization and larval metamorphosis of the coral Acropora millepora (Ehrenberg, 1834) by petroleum products. Marine Pollution Bulletin 41, 420–427 (2000).
  • McCarren J. et al. . Microbial community transcriptomes reveal microbes and metabolic pathways associated with dissolved organic matter turnover in the sea. Proceedings of the National Academy of Sciences 107, 16420–16427, doi: (2010).10.1073/pnas.1010732107 [PubMed] [Cross Ref]
  • Bryson S. et al. . Proteomic stable isotope probing reveals taxonomically distinct patterns in amino acid assimilation by coastal marine bacterioplankton. mSystems 1, e00027–00015, doi: (2016).10.1128/mSystems.00027-15 [PMC free article] [PubMed] [Cross Ref]
  • Fabricius K. E. in Coral Reefs: An Ecosystem in Transition (ed. Dubinsky Z. and Stambler N.) 493–505 (2011).
  • Macdonald R. K., Ridd P. V., Whinney J. C., Larcombe P. & Neil D. T. Towards environmental management of water turbidity within open coastal waters of the Great Barrier Reef. Marine Pollution Bulletin 74, 82–94 (2013). [PubMed]
  • Stoddart J. A. & Anstee S. Water quality, plume modeling and tracking before and during dredging in Mermaid Sound, Dampier, Western Australia. 13–33 (Perth, Western Australia, 2005).
  • Jones R., Fisher R., Stark C. & Ridd P. Temporal patterns in seawater quality from dredging in tropical environments. PLoS ONE 10, e0137112, doi: (2015).10.1371/journal.pone.0137112 [PMC free article] [PubMed] [Cross Ref]
  • Waters D. K. et al. . Modelling reductions of pollutant loads due to improved management practices in the Great Barrier Reef catchments – Whole of GBR. (Queensland Department of Natural Resources and Mines, Toowoomba, Queensland, 2014).
  • Willis B. L., Babcock R. C., Harrison P. L. & Wallace C. C. Experimental hybridization and breeding incompatibilities within the mating systems of mass spawning reef corals. Coral Reefs 16, S53–S65 (1997).
  • Marshall D. J. Reliably estimating the effect of toxicants on fertilization success in marine broadcast spawners. Marine Pollution Bulletin 52, 734–738 (2006). [PubMed]
  • Heyward A. J. & Negri A. P. Natural inducers for coral larval metamorphosis. Coral Reefs 18, 273–279 (1999).
  • Warne M. S. et al. . Revisions to the derivation of the Australian and New Zealand guidelines for toxicants in fresh and marine waters. Environmental Science and Pollution Research 21, 51–60 (2014). [PubMed]

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