Size-dependant mortality influences the recolonization success of juvenile corals transplanted for reef restoration and assisting juvenile corals attain a refuge size would thus improve post-transplantation survivorship. To explore colony size augmentation strategies, recruits of the scleractinian coral Pocillopora damicornis were fed with live Artemia salina nauplii twice a week for 24 weeks in an ex situ coral nursery. Fed recruits grew significantly faster than unfed ones, with corals in the 3600, 1800, 600 and 0 (control) nauplii/L groups exhibiting volumetric growth rates of 10.65±1.46, 4.69±0.9, 3.64±0.55 and 1.18±0.37 mm3/week, respectively. Corals supplied with the highest density of nauplii increased their ecological volume by more than 74 times their initial size, achieving a mean final volume of 248.38±33.44 mm3. The benefits of feeding were apparent even after transplantation to the reef. The corals in the 3600, 1800, 600 and 0 nauplii/L groups grew to final sizes of 4875±260 mm3, 2036±627 mm3, 1066±70 mm3 and 512±116 mm3, respectively. The fed corals had significantly higher survival rates than the unfed ones after transplantation (63%, 59%, 56% and 38% for the 3600, 1800, 600 and 0 nauplii/L treatments respectively). Additionally, cost-effectiveness analysis revealed that the costs per unit volumetric growth were drastically reduced with increasing feed densities. Corals fed with the highest density of nauplii were the most cost-effective (US$0.02/mm3), and were more than 12 times cheaper than the controls. This study demonstrated that nutrition enhancement can augment coral growth and post-transplantation survival, and is a biologically and economically viable option that can be used to supplement existing coral mariculture procedures and enhance reef restoration outcomes.
Citation: Toh TC, Ng CSL, Peh JWK, Toh KB, Chou LM (2014) Augmenting the Post-Transplantation Growth and Survivorship of Juvenile Scleractinian Corals via Nutritional Enhancement. PLoS ONE 9(6): e98529. doi:10.1371/journal.pone.0098529
Editor: Brian Gratwicke, Smithsonian’s National Zoological Park, United States of America
Received: March 1, 2014; Accepted: May 2, 2014; Published: June 4, 2014
Copyright: © 2014 Toh et al. This is an open-access article distributed under the terms of the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original author and source are credited.
Funding: Funding for the research was provided by Wildlife Reserves Singapore Conservation Fund awarded to TCT. TCT was supported by the National University of Singapore Research Scholarship and the SingHaiyi Scholarship. The funders had no role in study design, data collection and analysis, decision to publish, or preparation of the manuscript.
Competing interests: The authors have declared that no competing interests exist.
The global decline of coral reefs and the loss of associated ecological services have necessitated immediate intervention measures to reverse their further deterioration , . Active coral reef restoration initiatives have increasingly been incorporated into coastal management frameworks to supplement existing measures of rehabilitating impacted reefs , . Of the myriad techniques which have been developed, coral transplantation remains one of the most widely used, largely due to its ability to promote rapid colonization of the reefs and its ease of application , . The potential for generating large quantities of coral material via the “coral gardening” approach  for eventual transplantation to degraded reefs led to a greater emphasis on coral mariculture techniques. Asexual propagation techniques such as fragmentation allow coral material to be generated easily , but the drawbacks of this approach include a lack of genetic diversity of the clonal fragments and susceptibility of the donor colonies to stress arising from the fragmentation process, hence impeding large-scale production , , . Recent developments have enabled the use of sexually derived coral juveniles as material for transplantation onto degraded reefs , . As scleractinian corals are highly fecund, this ensures that large numbers of genetically diverse coral propagules would be generated. While direct artificial seeding of coral larvae onto reefs can enhance initial recruitment , early post-settlement mortality of the recruits is exceedingly high due to competition by fouling communites and predation .
The use of ex situ coral mariculture in reef restoration can improve coral post-settlement survivorship. The rearing conditions can be carefully monitored and regulated to minimize the impacts of disturbances from fouling communities, temperature fluctuations and predator infestations by allowing the timely introduction of mitigative measures , . In spite of these benefits, the cost of setting up and operating ex situ mariculture facilities can be very expensive . For instance, the cost of maintaining juvenile coral culture in the Philippines for six months constitutes 42.9% of the total project expenditure  and this inevitably increases with labour costs . Unfortunately, such detailed financial estimates are rarely reported in the existing scientific literature due to the complexities involved and the rigorous efforts required to provide a reliable estimate. Cost-effectiveness analyses of cost-per-coral reveal clearly that as mortality rate increases, so does the cost of each colony . Given that the highest mortality rates occur during the early developmental phases of the coral life cycle , augmenting the survivorship of juvenile corals would improve cost-effectiveness and increase the availability of source material for transplantation.
Size is an important determinant of survivorship in scleractinian corals and thus affects the rate of establishment of coral transplants on degraded reefs . Smaller colonies tend to be more vulnerable since the refuge size required for surviving injuries arising from predation and incidental grazing is not yet attained , . Increasing coral colony size prior to transplantation is thus advantageous for enhancing post-transplantation growth, survivorship and promoting sexual maturity – factors which are essential for the maintenance of a viable coral community , , .
Scleractinian corals exhibit substantial inter- and intra-specific variations in growth rates , , and one potential approach to promote rapid colony growth is to facilitate colony fusion . However tissue resorption and somatic germ-cell parasitism may instead retard colony growth , , . Another strategy involves enhancing the autotrophic and heterotrophic modes of coral nutrition by adjusting the conditions in ex situ mariculture prior to transplantation. Various studies have demonstrated that photosynthetic and feeding rates could be increased by the manipulation of light intensity, flow rate and nutrient levels , , . Although information on the effects of these manipulations on long-term coral growth rates is limited, the effects of nutritional enhancement are remarkably consistent for coral species from the families Faviidae, Acroporidae and Pocilloporidae. Compared to non-live feeds, live feeds were particularly useful for inducing faster coral growth , as were increments in ex situ feeding densities , . With heterotrophy in scleractinian corals commencing as early as two to seven days post-settlement , , enhancing nutrition in the early stages should be explored as this would assist coral juveniles in attaining a size refuge as early as possible and reduce mortality.
The present study aims to evaluate the feasibility of nutritional enhancement as a strategy to improve the post-transplantation growth and survivorship of juveniles of the scleractinian coral Pocillopora damicornis. We hypothesize that the growth and survivorship of fed corals would be augmented both during the ex situ mariculture phase and after transplantation to the reef. To assess the economic viability of this approach for both coral mariculture and reef restoration efforts, we also determined the cost estimates for the study and examined the cost-effectiveness of ex situ nutritional enhancement. The findings of this study will facilitate planning of future coral mariculture and reef restoration initiatives.
Materials and Methods
Study Species and Planulae Collection
Pocillopora damicornis (Linnaeus, 1758) is a hermaphroditic scleractinian coral commonly found inhabiting shallow coastal areas within the Indo-Pacific region . The reproductive and feeding biology of this coral has been well-studied , ,  and it has been used extensively as a model species for developmental studies . Pocillopora damicornis is also highly fecund and broods monthly , making it a popular candidate for propagation for the aquarium trade and reef restoration. This research was conducted with permission from Singapore National Parks Board (permit number NP/RP13-016), and no permit is required for collecting coral propagules in Singapore. Ten donor colonies of P. damicornis were collected from the fringing reef off Kusu Island, Singapore (1°13′25′′N, 103°51′38′′E) two days before the new moon in July 2012. Only colonies spaced 5 m apart and at least 20 cm in diameter were collected to ensure that they were sexually mature and to minimize the chances of collecting identical genets . The colonies were then transported to the Tropical Marine Science Institute on St. John’s Island, Singapore (1°13′44′′N, 103°50′73′′E) and maintained in aerated outdoor aquaria (190×100×40 cm) with flow-through filtered seawater , which functioned as an ex situ coral nursery.
Biologically conditioned ‘plugs’, made of plastic wall plugs embedded in cement hemispheres (40 mm diameter), were fabricated and used as settlement substrates . These allowed the P. damicornis recruits to be handled easily and facilitated their eventual transplantation onto the reef. One day before the new moon, all donor colonies were transferred and isolated in polyethylene planulation tanks (45 cm×30 cm×30 cm) with flow-through filtered seawater. Five centimetres below the rim of each tank, an outlet (3 cm diameter) was created to ensure water exchange. It was also covered with 100 µm plankton mesh (Sefar Pte. Ltd., Singapore) which helped to retain the coral planulae within the tanks. The tanks were filled with approximately 8 cm of sand which the conditioned plugs were inserted into, leaving only their hemispherical surfaces exposed for planulae settlement. Each plug was monitored daily for newly settled recruits, and plugs with at least three recruits were removed from the tank and maintained in the outdoor aquaria. In this study, all the colonies planulated within one to six days after the new moon, and the planulae were observed to settle within a day after planulation.
Feeding Regime in ex situ Coral Nursery
A total of 288 plugs with live juvenile corals were used for this study. On each plug, one primary polyp which had settled at least 10 mm away from the rest of the recruits was identified, measured and tagged by mapping the coral’s position on the plug. This served to reduce the chances of colony fusion which would affect growth rates . The plugs were randomly assigned among 16 holding tanks, each tank corresponding to one of the four feeding densities (0, 600, 1800 and 3600 nauplii/L following Petersen et al. (2008); n = 4 tanks). In each replicate tank, 18 plugs spaced 5 cm apart were secured on an elevated PVC frame. All plugs were maintained in the outdoor aquaria for one week before the start of the feeding regime .
The juvenile corals were fed with cultured day-old Artemia salina (approximately 400 µm; Bio-Marine Inc., California, U.S.A.), wherein each nauplius provided around 9.77 µcal , for 4 hours (between 12∶00 to 16∶00) twice every week for 24 weeks (from August 2012 to February 2013). During each feeding session, all the plugs were transferred to 10 L polyethylene feeding tanks containing 6 L of filtered sea water with gentle aeration. The corresponding volume of nauplii stock solution was added to make up the required densities for each treatment tank. The positions of the feeding tanks were randomised during each feeding session to minimize potential spatial influences on heterotrophic rates. After feeding, the plugs were gently flushed with filtered seawater to remove any remaining nauplii, and subsequently transferred back to the holding tanks. Fouling macroalgae were physically removed twice a week as these would otherwise rapidly overgrow the coral juveniles and compromise colony health .
The survivorship and growth – length (l), width (w) and height (h) – of the 18 tagged coral juveniles in each replicate tank were measured using vernier calipers every four weeks and the ecological volume of each coral was estimated following the calculation for right cylindrical volumes, V = πr2h, where r = (l+w)/4 . Weekly radial and volumetric growth were calculated by dividing the respective differences in colony radii and ecological volumes at the start of the ex situ feeding regime and at the end of the ex situ feeding regime (24 weeks). The data obtained for all the surviving corals in each replicate tank was then averaged. The mean daily temperature and light irradiance (Onset Computer Corporation Inc., Massachusetts, U.S.A.) in the aquaria were 29±0.01°C (n = 168 days) and 128.7±18.1 Lux (n = 168 days) respectively.
Transplantation and Monitoring
After 24 weeks, eight plugs with live corals were randomly selected from each holding tank to be transplanted back to the donor reef at Kusu Island. Four limestone outcrops (approximately 3.5 m in diameter and 2.5 m in height) that were at least 5 m apart were identified for the transplantation of the juvenile corals. Four sets of eight holes were then drilled on each outcrop and each replicate treatment was randomly assigned to one set of holes, such that the corals belonging to the same replicate holding tank were transplanted on the same outcrop (n = 4 outcrops). The plugs were inserted into the holes and stabilized using two-part marine epoxy .
The survivorship and colony dimensions of the tagged coral juveniles on each plug were recorded every four weeks for 24 weeks (from February to August 2013). Weekly radial and volumetric growth were calculated by dividing the respective differences in colony radii and ecological volumes at the start of the ex situ feeding regime and at the end of the entire study with the duration of the entire study (48 weeks). The data obtained for all the surviving corals in each replicate outcrop was then averaged. The mean daily temperature (Onset Computer Corporation Inc., Massachusetts, U.S.A.) in the transplant site was 29.9±0.07°C (24 readings per day, n = 168 days).
Cost-estimates were tabulated for each of the five phases of this study: (1) Collection of source materials and establishment of coral culture, (2) Maintenance and ex situ monitoring, (3) Feeding, (4) Transplantation and (5) In situ monitoring, and further itemized into equipment costs, labour costs and boat trips following Edwards et al. (2010) and Villanueva et al. (2012). The cost per coral produced before and after transplantation to the reef were then calculated. In addition, the cost per unit volumetric growth of each treatment group for both the ex situ feeding and post-transplantation phases was also estimated based on the total production costs, the mean weekly volumetric growth rates, duration and the number of tagged colonies alive at the end of each phase.
Data for the final ecological volume, weekly radial and volumetric growth rates were first tested for homogeneity of variances using Levene’s test and normality using Shapiro-Wilk test, followed by one-factor ANOVA with Tukey’s HSD (Honestly Significant Difference) post-hoc test for all possible pairwise comparisons. As the variances for post-transplantation volumetric growth rates were heterogenous and not normally distributed, a non-parametric Kruskall-Wallis analysis was used. Subsequent pairwise comparisons were analysed using Mann-Whitney U test. These analyses were computed using SPSS v 17.0 (SPSS Inc). Data for the survivorship was analyzed using Cox Proportional-Hazards regression model and logrank test (R 2.14.2), using the independent factors initial colony radius, treatment and the interaction between radius and treatment for analysis. The model that best explained the trend was then selected using Akaike Information Criteria (AIC).
Growth of Pocillopora damicornis Juveniles in ex situ Feeding Phase
The initial mean colony volume of the coral juveniles (approximately 3.5 mm3) did not differ significantly among the treatment groups (F3,12 = 0.687, p = 0.557). The mean colony volume across the treatments increased monotonically over the ex situ feeding phase of the study (Fig. 1a; Fig. 2). Juvenile corals in the 3600 nauplii/L treatment group grew by more than 74 times their initial sizes and attained a mean final ecological volume of 248.38±33.44 mm3 (mean ± S.E.; 4.03±0.18 mm radius). The final volumes of the colonies in the 1800, 600 and 0 nauplii/L were 111.66±20.8 mm3 (34 times the initial volume; 3.63±0.25 mm radius), 87.18±12.91 mm3 (24 times the initial volume; 2.78±0.12 mm radius) and 30.65±8.65 mm3 (8 times the initial volume; 2.13±0.05 mm radius), respectively.
Graphs show the (a) mean ecological volumes, (b) mean weekly radial and (c) volumetric growth rates (± S.E.) of the corals in the 0 (control), 600, 1800 and 3600 nauplii/L treatment groups. The symbols *, **, and *** denote statistical significance at p = 0.05, p = 0.01, p = 0.001 respectively.
Pocillopora damicornis juveniles in the 0 (control), 600, 1800 and 3600 nauplii/L treatment groups (a, c, e, g) after the 24-week ex situ feeding regime, and (b, d, f, h) 24 weeks after transplantation to the reef. Scale bar = 1 cm, arrows indicate the positions of the corals.
The weekly radial growth rates of the colonies (Fig. 1b) significantly differed among treatments (F3,12 = 30.8, p<0.001). Colonies in the 3600 and 1800 nauplii/L treatment groups grew at rates of 0.13±0.008 mm/week (mean ± S.E.) and 0.11±0.009 mm/week respectively, and were significantly faster than those in the 600 nauplii/L (0.08±0.005 mm/week, p<0.001) and control (0.05±0.002 mm/week, p<0.001) groups. Weekly volumetric growth rates (Fig. 1c) were also significantly different among treatments (F3,12 = 19.2, p<0.001) with the colonies in the 3600 nauplii/L treatments growing significantly faster (10.65±1.46 mm3/week) than colonies in the 1800 nauplii/L (4.69±0.9 mm3/week, p = 0.003), 600 nauplii/L (3.64±0.55 mm3/week, p = 0.001) and control (1.18±0.37 mm3/week, p<0.001) groups.
Growth of Pocillopora damicornis Juveniles after Transplantation
The mean colony sizes of all juvenile corals continued to increase steadily after transplantation to the reef (Fig. 2; Fig. 3a), with the colonies in the 3600 nauplii/L treatment group exhibiting the largest increase in size (1534 times the initial size at the start of the study). Final mean colony volumes for the 0, 600 1800 and 3600 nauplii/L groups were 512±116 mm3 (mean ± S.E.; 137 times the initial volume; 5.03±0.49 mm radius), 1066±70 mm3 (284 times the initial volume; 6.35±0.14 mm radius), 2036±627 mm3 (486 times the initial volume; 7.25±0.80 mm radius) and 4875±260 mm3 (10.5±0.29 mm radius), respectively.
Graphs show the (a) mean ecological volumes, (b) mean weekly radial and (c) volumetric growth rates (± S.E.) of juvenile Pocillopora damicornis in the 0 (control), 600, 1800 and 3600 Artemia nauplii/L treatment groups. The symbols *, **, and *** denote statistical significance at p = 0.05, p = 0.01, p = 0.001 respectively.
Weekly radial growth rates (Fig. 3b) differed among the treatment groups (F3,12 = 26.05, p<0.001). Colonies in the 3600 nauplii/L group (mean ± S.E.; 0.198±0.005 mm/week) had significantly faster growth rates than the colonies in the 1800 nauplii/L (0.128±0.016 mm/week; p = 0.001), 600 nauplii/L (0.109±0.003; p<0.001) and the control (0.082±0.01 mm/week; p<0.001) groups. A significant difference between the 1800 nauplii/L and control groups was also present (p<0.05). The weekly volumetric growth rates (Fig. 3b) were also significantly different (p = 0.006), displaying a similar trend as that of the radial growth rates. The mean volumetric growth rates (Fig. 3c) were 101.5±5.4 mm3/week, 42.3±13.1 mm3/week, 22.1±1.5 mm3/week and 10.6±2.4 mm3/week for the 3600, 1800, 600 and 0 nauplii/L groups respectively.
Survivorship of Juvenile Pocillopora damicornis in ex situ Feeding Phase and after Transplantation
In the ex situ feeding phase (Fig. 4a), there were no significant differences in survivorship across treatments (logrank test = 1.22, d.f. = 1, p = 0.27). Survival rates of the P. damicornis juveniles in the control, 600, 1800 and 3600 nauplii/L groups at the end of 24 weeks were 45%, 54%, 58% and 47% respectively, and the overall survival was 51%. Corals in the control, 600, 1800 and 3600 nauplii/L groups had post-transplantation survival rates of 38%, 56%, 59% and 63% respectively (overall survival of 54%), and these were significantly different across treatments (Fig. 4b).
Survival curves of Pocillopora damicornis juveniles in the 0 (control), 600, 1800 and 3600 nauplii/L groups (a) in the ex situ feeding phase (24 weeks, n = 72) and (b) after transplantation (24 weeks, n = 32).
Post-hoc pairwise comparisons revealed that the corals in the 3600 and 1800 nauplii/L groups (p = 0.016 and p = 0.044, respectively) had significantly higher survival rates than the control. The difference in survivorship was accounted for by both the initial radius prior to transplantation (logrank test = 6.86, A.I.C. value = 535, d.f. = 1, p = 0.009) and treatment (logrank test = 6.26, A.I.C. value = 536, d.f. = 1, p = 0.012), and both factors were highly correlated (r = 0.6).
The total cost for producing 288 coral plugs in the ex situ feeding phase and transplanting 128 corals to the reef was an estimated US$10467 (see Table S1 for detailed cost estimates). Over 40% was attributed to the cost of establishing the coral culture, which included the harvesting of donor colonies, setting up of culture tanks and the collection of planulae (Table 1). 34.3% of the total costs arose from transplanting and subsquent monitoring of the coral transplants, while feeding and maintenance of the coral juveniles contributed the remaining 9.6% and 7.2% respectively.
The cost of propagating 288 corals was estimated at US$20.90/coral. Upon taking into account the mean survival rate of 51% at the end of the ex situ feeding phase, the cost per coral was US$40.98 (Table 1). The cost of each transplanted coral was estimated at US$81.78. With a 54% mean survival rate 24 weeks after transplantation, the cost per coral was US$151.44 (Table 1). In the ex situ feeding phase, the cost per unit growth decreased with increasing feeding densities (Table 2), making the 3600 nauplii/L treatment group the most cost-effective. The cost per unit volumetric growth was US$0.18/mm3, which was more than seven times cheaper than that of the control group. A similar trend was observed for the corals after transplantation – the cost per unit volumetric growth for the 3600 nauplii/L treatment was US$0.02/mm3, which was more than 12 times cheaper than the control treatments.
Scleractinian corals supplement up to 35% of their daily metabolic requirements with a wide range of items such as dissolved organic matter, suspended particulate matter and zooplankton , , . While corals reared in ex situ systems are routinely supplied with zooplankton, microalgae and commercial dry food , those fed with live zooplankton – a highly nutritious feed – consistently grow faster , . The use of Artemia nauplii as coral feed in this study significantly augmented the growth of P. damicornis juveniles. Coral volumetric growth rates increased by up to 9 times with the addition of higher densities of Artemia nauplii, leading to final ecological volumes that were 2.9 to 8.8 times greater than those in the control groups after 24 weeks (Fig. 1). These results were comparable to work by Petersen et al. (2008), who reported that Acropora tenuis juveniles fed with 3750 Artemia nauplii/L and Favia fragum juveniles fed with 300 nauplii/L respectively grew eight and five times larger than those in the control group. Since juvenile coral growth was proportionate to feed densities and the growth rates did not slow down even at 3600 nauplii/L, further increment of feeding densities and frequency would likely augment coral growth further. Additionally, as heterotrophy is known to play an important role in mitigating effects during stress events such as coral bleaching , introducing live feed during the early life stages can assist juvenile corals in attaining the required refuge size faster and cope with the effects of acute environmental stress.
Although ex situ mariculture can help to enhance the survivorship of coral fragments (>98%) ,  and sexual propagules (60–75%) , ,  by providing a conducive environment for the coral material to grow, the facilities are usually expensive to run , inadvertently placing limits on the duration of rearing as well as the potential for any improvements to survivorship . As survivorship increases with colony size , it is important to explore ways of accelerating the growth of juvenile corals in the least possible time. In this study, coral survivorship did not improve substantially despite significant increases in growth, as was consistent with that observed by Petersen et al. (2008). However, at 51%, the mean survival rate across treatments were more than four times higher than if juvenile corals of the same size class were to be transplanted to the field , underscoring the usefulness of feeding corals in ex situ mariculture to optimise restoration outcomes.
Twenty-four weeks after transplantation, the juvenile coral transplants were 1.5 to 2.1 times larger than their initial sizes (Fig. 3). This corroborated with other studies wherein 6-months-old and 18-months-old branching juvenile corals grew 1.5 to five times their initial diameters six months after transplantation , . More importantly, the growth rates of fed corals remained consistently higher than those of the unfed corals even after transplantation to the reef, suggesting the possibility that benefits obtained from the ex situ feeding regime will continue even after feeding has stopped.
Interestingly, the enhancement in growth from the ex situ feeding regime improved the post-transplantation survivorship of the juvenile corals. Both size and feeding regimes were able to account for the survivorship patterns observed, supporting the observations of size-dependant mortality in scleractinian corals . Since nutrition enhancement was a direct causative agent of the coral growth and both the effects of size and feeding regime on survivorship were highly correlated, it exerted a concomitant effect of augmenting post-transplantation survival. Clearly, size was a key determinant of post-transplantation survival. However, the average post-transplantation mortality rate of all P. damicornis juveniles in this study (46%) was higher than that reported from other studies (11–34%) , , , likely due to the high sediment levels in Singapore waters, which have been estimated to limit scleractinian recruitment to two individuals m−2 . As was observed during monthly visits to the study site, most juvenile colonies were smothered by fine particulate sediment, with obvious damage to the coral tissue. Post-transplantation survivorship can thus be expected to be lower in areas experiencing chronic sedimentation such as Singapore. It is clearly advantageous to boost the survival chances of juvenile corals by implementing an ex situ nutritional enhancement regime to increase colony size prior to transplantation.
While nutritional enhancement confers significant ecological advantages to juvenile corals in ex situ mariculture, the process should still be thoroughly assessed and reviewed to boost its economic viability. In the current study, nutritional enhancement constituted only 9% of total production costs. Of this amount, 99% was attributed to the labour required for transferring the corals from the holding tanks to the feeding tanks. Such costs can be reduced further in commercial mariculture systems where the corals do not need to be transferred elsewhere for feeding. The results also showed that corals supplied with the highest density of feed (3600 nauplii/L) attained ecological volumes close to that of the corals in the control group at the end of the 24-week feeding phase, in as early as eight weeks. This corresponds to a one-third reduction in ex situ rearing time and translates to significant reductions in operational costs. Additionally, the cost-effectiveness of the method was apparent as the cost per unit volumetric growth of the corals fed with 3600 nauplii/L was more than seven and twelve times cheaper than the controls in both the ex situ rearing and post-transplantation phases, respectively. However, it must be noted that directly comparing project costs among localities leads to inaccuracies. For example, costs per coral can be as low as US$11 in the Philippines  to as high as US$151 in Singapore (this study), mainly due to differences in manpower and equipment costs – labour costs differed by almost six-fold while the cost of boat hire differed by nearly ten-fold. Exploring other options such as recruiting volunteers to reduce labour costs  or increasing production for economies of scale  would help to improve cost-effectiveness.
The current study showed that supplying live Artemia salina nauplii as coral feed enhanced juvenile coral growth rates and survivorship in both the ex situ nursery phase as well as six months after they had been transplanted to a reef. These findings are important, because even though sexually-derived corals are increasingly used as material for reef restoration , , the high mortality rates of the juvenile propagules is often a stumbling block in such projects. Since long rearing periods are infeasible due to high operational costs, nutritional enhancement may be considered as a means of reducing the time and cost required for the coral material to be reared in mariculture facilities. The approach is simple, cost-effective, and harbours the potential for large-scale application.
Detailed cost estimates. Cost estimates of producing 288 plugs with live Pocillopora damicornis juveniles under four ex situ feeding regimes (0, 600, 1800, 3600 nauplii/L) for 24 weeks, followed by the transplantation of 128 coral plugs and subsequent monitoring for 24 weeks.
We would like to thank the staff and students of the NUS Reef Ecology Laboratory and the Tropical Marine Science Institute, for their administrative and logistical support. We would also like to acknowledge K.Y. Chong, A.T.K. Yee, X. Giam, J.R. Guest and A.J. Underwood for their valuable suggestions, and S.K.G. Lo for fabricating the settlement substrates used in this study. The comments provided by four anonymous reviewers greatly enhanced the manuscript. This study was part of T.C. Toh’s Ph.D. dissertation work.
Conceived and designed the experiments: TCT. Performed the experiments: TCT JWKP CSLN. Analyzed the data: TCT JWKP CSLN KBT. Contributed reagents/materials/analysis tools: TCT JWKP CSLN KBT LMC. Wrote the paper: TCT JWKP CSLN KBT LMC.
- 1. Bridge TC, Hughes TP, Guinotte JM, Bongaerts P (2013) Call to protect all coral reefs. Nat Clim Chang 3(6): 528–530.
- 2. Graham NA, Bellwood DR, Cinner JE, Hughes TP, Norström AV, et al. (2013) Managing resilience to reverse phase shifts in coral reefs. Front Ecol Environ 11(10): 541–548.
- 3. Rinkevich B (1995) Restoration strategies for coral reefs damaged by recreational activities: the use of sexual and asexual recruits. Restoration Ecology 3(4): 241–251.
- 4. Edwards AJ (2010) Reef Rehabilitation Manual. Coral Reef Targeted Research & Capacity Building for Management Program, St Lucia, Australia. 166 p.
- 5. Edwards AJ, Clark S (1999) Coral transplantation: a useful management tool or misguided meddling? Mar Pollut Bull 37(8): 474–487.
- 6. Shafir S, Van Rijn J, Rinkevich B (2006) Steps in the construction of underwater coral nursery, an essential component in reef restoration acts. Mar Biol 149(3): 679–687.
- 7. Yap HT, Alvarez RM, Custodio III HM, Dizon RM (1998) Physiological and ecological aspects of coral transplantation. J Exp Mar Biol Ecol 229(1): 69–84.
- 8. Shearer TL, Porto I, Zubillaga AL (2009) Restoration of coral populations in light of genetic diversity estimates. Coral Reefs 28(3): 727–733.
- 9. Toh TC, Guest J, Chou LM (2012) Coral larval rearing in Singapore: Observations on spawning timing, larval development and settlement of two common scleractinian coral species. In Tan KS, editor. Contributions to Marine Science. National University of Singapore, Republic of Singapore. 81–87.
- 10. Omori M, Iwao K, Tamura M (2008) Growth of transplanted Acropora tenuis 2 years after egg culture. Coral Reefs 27(1): 165–165.
- 11. Villanueva RD, Baria MVB, dela Cruz DW (2012) Growth and survivorship of juvenile corals outplanted to degraded reef areas in Bolinao-Anda Reef Complex, Philippines. Mar Biol Res 8(9): 877–884.
- 12. Heyward AJ, Smith LD, Rees M, Field SN (2002) Enhancement of coral recruitment by in situ mass culture of coral larvae. Mar Ecol Prog Ser 230: 113–118.
- 13. Guest JR, Heyward AJ, Omori M, Iwao K, Morse A, et al.. (2010) Rearing coral larvae for reef rehabilitation. In: Edwards AJ editor. Reef Rehabilitation Manual. Coral Reef Targeted Research & Capacity Building for Management Program, St Lucia, Australia. 73–92.
- 14. Forsman ZH, Rinkevich B, Hunter CL (2006) Investigating fragment size for culturing reef-building corals (Porites lobata and P. compressa) in ex situ nurseries. Aquaculture 261(1): 89–97.
- 15. Toh TC, Ng CSL, Guest J, Chou LM (2013) Grazers improve the health of scleractinian coral juveniles in ex situ mariculture. Aquaculture 414–415: 288–293.
- 16. Nakamura R, Ando W, Yamamoto H, Kitano M, Sato A, et al. (2011) Corals mass-cultured from eggs and transplanted as juveniles to their native, remote coral reef. Mar Ecol Prog Ser 436: 161–168.
- 17. Raymundo LR, Maypa AP (2004) Getting bigger faster: Mediation of size-specific mortality via fusion in juvenile coral transplants. Ecol Appl 14(1): 281–295.
- 18. Wood R (1993) Nutrients, predation and the history of reef-building. Palaios: 526–543.
- 19. Hughes TP (1984) Population dynamics based on individual size rather than age: a general model with a reef coral example. Am Nat: 778–795.
- 20. Wallace CC (1985) Reproduction, recruitment and fragmentation in nine sympatric species of the coral genus Acropora. Mar Biol. 88: 21–233.
- 21. Bak RPM, Engel MS (1979) Distribution, abundance and survival of juvenile hermatypic corals (Scleractinia) and the importance of life history strategies in the parent coral community. Mar Biol 54(4): 341–352.
- 22. Buss LW (1982) Somatic cell parasitism and the evolution of somatic tissue compatibility. Proc Nat Acad of Sci U S A 79: 5337–5341.
- 23. Rinkevich B, Weissman IL (1992) Chimeras vs. genetically homogeneous individuals: potential fitness costs and benefits. Oikos 63: 119–124.
- 24. Pancer Z, Gershon H, Rinkevich B (1995) Coexistence and possible parasitism of somatic and germ cell lines in chimeras of the colonial urochordate Botryllus schlosseri. Biol Bull 189: 106–112.
- 25. Sebens KP, Witting J, Helmuth B (1997) Effects of water flow and branch spacing on particle capture by the reef coral Madracis mirabilis (Duchassaing and Michelotti). J Exp Mar Biol Ecol 211(1): 1–28.
- 26. Marubini F, Barnett H, Langdon C, Atkinson MJ (2001) Dependence of calcification on light and carbonate ion concentration for the hermatypic coral Porites compressa. Mar Ecol Prog Ser 220: 153–162.
- 27. Hii YS, Soo CL, Liew HC (2009) Feeding of scleractinian coral, Galaxea fascicularis, on Artemia salina nauplii in captivity. Aquac Int 17(4): 363–376.
- 28. Petersen D, Wietheger A, Laterveer M (2008) Influence of different food sources on the initial development of sexual recruits of reefbuilding corals in aquaculture. Aquaculture 277(3): 174–178.
- 29. Ferrier-Pagès C, Witting J, Tambutté E, Sebens KP (2003) Effect of natural zooplankton feeding on the tissue and skeletal growth of the scleractinian coral Stylophora pistillata. Coral Reefs 22(3): 229–240.
- 30. Cumbo VR, Fan T-Y, Edmunds PJ (2012) Scleractinian corals capture zooplankton within days of settlement and metamorphosis. Coral Reefs 31: 1155.
- 31. Toh TC, Peh JWK, Chou LM (2013) Early onset of zooplanktivory in equatorial reef coral recruits. Mar Biodivers 43(3): 177–178.
- 32. Veron JEN (2000) Corals of the world. Townsville: Australian Institute of Marine Science.
- 33. Harii S, Kayanne H, Takigawa H, Hayashibara T, Yamamoto M (2002) Larval survivorship, competency periods and settlement of two brooding corals, Heliopora coerulea and Pocillopora damicornis. Mar Biol 141(1): 39–46.
- 34. Toh TC, Peh JWK, Chou LM (2013) Heterotrophy in recruits of the scleractinian coral Pocillopora damicornis. Mar Freshw Behav Physiol 46(5): 313–320.
- 35. Chou LM, Quek ST (1993) Planulation in the scleractinian coral Pocillopora damicornis in Singapore waters. In: Proceedings of the 7th International Coral Reef Symposium. Mangilao (GU): University of Guam: p. 500.
- 36. Harriott VJ (1983) Reproductive seasonality, settlement, and post-settlement mortality of Pocillopora damicornis (Linnaeus), at Lizard Island, Great Barrier Reef. Coral Reefs 2: 151–157.
- 37. Benijts F, Vanvoorden E, Sorgeloos P (1976) Changes in the biochemical composition of the early larval stages of the brine shrimp, Artemia salina L. In Proceedings of the 10th European Symposium on Marine Biology Volume 1: p. 1–9.
- 38. Levy G, Shaish L, Haim A, Rinkevich B (2010) Mid-water rope nursery–Testing design and performance of a novel reef restoration instrument. Ecol Eng 36(4): 560–569.
- 39. Sorokin YI (1973) On the feeding of some scleractinian corals with bacteria and dissolved organic matter. Limnol Oceanogr 18(3): 380–385.
- 40. Anthony K (1999) Coral suspension feeding on fine particulate matter. J Exp Mar Biol Ecol 232(1): 85–106.
- 41. Houlbrèque F, Ferrier-Pagès C (2009) Heterotrophy in tropical scleractinian corals. Biol Rev Camb Philos Soc 84(1): 1–17.
- 42. Shaish L, Levy G, Katzir G, Rinkevich B (2010) Employing a highly fragmented, weedy coral species in reef restoration. Ecol Eng 36(10): 1424–1432.
- 43. Ng CSL, Ng SZ, Chou LM (2012) Does an ex situ coral nursery facilitate reef restoration in Singapore’s waters? In Tan KS, editor. Contributions to Marine Science. National University of Singapore, Republic of Singapore. 95–100.
- 44. Van Moorsel GWNM (1985) Disturbance and growth of juvenile corals (Agaricia humilis and Agaricia agaricites, Scleractinia) in natural habitats on the reef of Curacao. Mar Ecol Prog Ser 24: 99–112.
- 45. Dikou A, Van Woesik R (2006) Survival under chronic stress from sediment load: spatial patterns of hard coral communities in the southern islands of Singapore. Mar pollut bull 52(11): 1340–1354.