Predation of juvenile Crassostrea virginica by two species of mud crabs found in the Chesapeake Bay.
KEY WORDS: Crassostrea virginica, Eurvpanopeus depressus, Rhithropanopeus harrisii, spat mortality, predator prey dynamics, oyster restoration
The Eastern oyster, Crassostrea virginica (Gmelin, 1791), historically created reefs throughout the mesohaline subtidal regions of the Chesapeake Bay. The heterogeneous 3-dimensional structures formed by oyster reefs provide settlement surfaces for epifauna and habitat for benthic organisms, serving as the base for a complex ecosystem (Wells 1961, Dame 1979, Kennedy 1996, Tolley & Volety 2005). In addition, oyster reefs have supported a commercial oyster industry and have been shown to improve water quality (Nelson et al. 2004, Porter et al. 2004, Grizzle et al. 2008). Although C. virginica serves an important role in the Chesapeake Bay, adult population levels have declined an estimated 100-fold in the past century as a result of a combination of disease, degraded water conditions, and overharvesting (Newell 1988, Burreson & Ragone Calvo 1996, Ford & Tripp 1996, Kemp et al. 2005, Kirby & Miller 2005). In addition, for the past 10 y, natural recruitment has been low on most Maryland oyster bars (Tarnowski 2010). As a result, the historic complex reef structures have either been destroyed or dramatically reduced (Rothschild et al. 1994, Woods et al. 2005).
As a result of the extensive decline in C. virginica population levels in the Chesapeake Bay, efforts have been undertaken to restore oyster reefs in select areas. One organization, the Oyster Recovery Partnership, has been seeding historic oyster bars in the Chesapeake Bay with hatchery-reared juvenile oysters (spat) for the past 11 y (Paynter 1999, Paynter et al. 2010). Newly seeded spat suffer mortality rates that range from 25-100% within a few weeks after planting (Paynter 2009). Exploring the causes of spat mortality may provide valuable information for improving restoration success and understanding recent changes in natural recruitment rates.
Predation by benthic invertebrates is one source of spat mortality. Known spat predators in the Chesapeake Bay include polyclad flatworms (Stylochus ellipticus Girard, 1850), blue crabs (Callinectes sapidus, Rathbun, 1896), and the common blackfingered mud crab (Panopeus herbstii (Edwards, 1834)) (Bisker & Castagna 1987, Eggleston 1990, Newell et al. 2000, O'Conner et al. 2008). In addition to P. herbstii, four other xanthid crabs have been reported to inhabit the Chesapeake Bay (Ryan 1956). Of these species, the flat mud crab (Eurypanopeus depressus (Smith, 1869)) and the white-fingered mud crab (Rhithropanopeus harrisii (Gould, 1841)), have been found in high abundances on oyster reefs in the middle to upper Chesapeake Bay (Harwell 2010, Rodney & Paynter 2006). Although predation by P. herbstii has been well documented (Seed 1980, Whetstone & Eversole 1981, Bisker & Castagna 1987, Grabowski 2004, O'Conner et al. 2008), few studies have examined oyster predation by E. depressus and R. harrisii. McDermott (1960) measured E. depressus predation on oyster spat and found a mean predation rate of 3.8 spat per crab per day. However, crabs in that study (McDermott 1960) were not separated into individual cages, so intraspecific competition may have artificially reduced the estimated predation rates. Newell et al. (2007) compared the percentage of C. virginica and Crassostrea ariakensis (Fujita, 1913) spat consumed by a range of predators, including E. depressus and R. harrisii, over a 30-day study period. They showed that E. depressus preyed on a larger percentage of C. virginica spat than R. harrisii, and that both species consumed spat smaller than 7 ram, even though they had access to larger spat. Because individuals had a choice of consuming C. ariakensis, a food source not currently available in the Chesapeake Bay, the results observed might not reflect natural predation potential. Milke and Kennedy (2001) showed that E. depressus not only preyed upon a larger size range of mytiliform bivalves than R. harrisii, but also had a significantly greater mechanical advantage in their crusher claw. Although previous studies (McDermott 1960, Milke & Kennedy 2001, Newell et al. 2007) have examined predation pressures exerted by E. depressus and R. harrisii, we have no estimates of the size or quantity of hatchery-reared spat consumed by these crabs on Chesapeake Bay oyster reefs. To investigate the spat predation rates by E. depressus and R. harrisii, we quantified spat predation by each of these species over a 96-h study period. Because E. depressus is generally larger than R. harrisii, we expected E. depressus to prey on oyster spat at a higher rate and on a larger size range than R. harrisii.
Spat and Mud Crab Preparation
Spat of C. virginica were produced at the oyster hatchery at Horn Point Laboratory in Cambridge, Maryland. Spat settlement densities and sizes varied among oyster shells ([mu] = 28.1 [+ or -] 20.7 spat per shell; range, 1-29 mm). Between experimental runs, spat-on-shell were maintained in floating mesh containers in the South River. Before the spat were used, epifaunal organisms were scrubbed off the shells.
Individual crabs were collected from the Choptank (E. depressus) and South rivers (R. harrisii). Crabs were given at least 4 days to acclimate to laboratory conditions in holding tanks and were held no longer than 11 days. In each holding tank, 2-3 g of macerated scallop meat was fed to the crabs every other day. Holding tanks were at ambient room temperature, approximately 25[degrees]C, and filled with artificial seawater kept at, approximately, a salinity of 10.
Experimental runs were conducted within three 55-gal. tanks, each of which held 6 2.5-gal. plastic drum bowl tanks. The 55-gal. tanks were covered with a fitted brown tarp to simulate low-light water conditions and to reduce the possibility of human activity altering the predatory behavior of the crabs. Similar to the mud crab holding tanks, water was at ambient room temperature and filled with artificial seawater kept at a salinity of approximately 10. Water flow was distributed among the 6 2.5-gal. tanks using PVC piping, and water flowed out of each tank through holes on the side. Water changes were performed between experimental runs. In addition, each 2.5-gal. tank contained approximately 3 cm cleaned commercial river pebbles.
[FIGURE 1 OMITTED]
Within each 55-gal. tank, five or the six 2.5-gal. tanks were experimental, in which a single crab was starved for 24 h before spat-on-shell were placed in the tank. The final 2.5-gal. tank was used as a control, where spat-on-shell were placed in the tank without a crab. The number of spat placed in a tank was recorded prior to each experimental run. Across all the experimental runs, the number of spat presented to E. depressus ranged from 26-136, and 19-93 for R. harrisii; the spat were spread over 1-3 shells in any given experimental run. To expose the highest shell surface area, the convex side of each shell was leaned against the front of the 2.5-gal. tank (Fig. 1).
Crabs were arbitrarily assigned to each 2.5-gal. tank after having their carapace widths (CWs) measured to the nearest 0.01 mm using digital calipers. Forty-five crabs were tested for each species. Each experimental run lasted 96 h; shells were removed from the experimental tanks every 24 h, and the number and size (shell height) of spat scars (visual representations of recently preyed on spat) were recorded. Shell height was measured as the length from the umbo to the marginal lip; measurements were made to the nearest millimeter.
For general trends, mean total and daily predation rates were calculated for each species, as well as the mean size of spat consumed. Total predation rate was calculated as the number of spat preyed on during the 4-day study period. Daily predation rates were calculated as the number of spat preyed on in each 24-h period. Daily predation rates were based on the initial spat count taken for each day. To account for the high variability in the number and size of spat provided, predation rates were also represented as the percentage of available spat consumed. The percentage of available spat consumed was categorized into three spat size classes: small (1-5 mm), medium (6-10 mm), and large (>10 mm). Mean percentage of available spat consumed within each spat size class were then also calculated for each species.
JMP 5.0.1 Statistical Discovery Software was used for statistical comparisons ([alpha] = 0.05 for all comparisons). Because data could not be normalized with transformations, nonparametric tests were used. Spearman's rho rank correlation test was used to analyze trends in the size and number of spat consumed. Wilcoxon's rank sum test was used to determine significant differences between groups. For analyzing predation rates, only the mean percentage of available spat consumed within each spat size class was compared statistically. Crabs that had molted or died during the experiment were removed from analyses.
CW was significantly different between species (Wilcoxon's rank sum test, P < 0.0001), where E. depressus had a mean CW of 15.8 [+ or -] 0.5 (SEM) mm and R. harrisii had a mean of 9.1 [+ or -] 0.3 mm. More oyster spat were preyed on by E. depressus than R. harrisii during the 96-h study period. The mean number of spat consumed in 4 days by E. depressus was 22.7 [+ or -] 2.9 spat per crab, or 37.2 [+ or -] 3.4% of available spat. Conversely, the mean number of spat consumed in 4 days by R. harrisii was 4.5 [+ or -] 0.9 spat per crab, or 9.2 [+ or -] 1.7% of available spat. Both species preyed on the greatest amount of oyster spat within the first 24 h, where E. depressus and R. harrisii consumed 16.2 [+ or -] 2.1% and 6.1 [+] 1.3% of available spat, respectively (Table 1). After the first 24 h, daily predation rates continued to decline, decreasing from an initial rate of 10.4 [+ or -] 1.7 spat per crab to a final rate of 2.9 [+ or -] 0.5 spat per crab for E. depressus, and 2.9 [+ or -] 0.6 spat per crab to 0.4 [+ or -] 0.1 spat per crab for R. harrisii.
The number of spat consumed throughout the study period was positively correlated with the number of spat provided for E. depressus (Spearman's rho = 0.6469, P < 0.0001), but was not correlated for R. harrisii (Spearman's rho = 0.2536, P > 0.05). The percentage of available spat consumed was not correlated with the number of spat provided in either species (E. depressus: Spearman's rho = 0.1516, P> 0.05; R. harrisii: Spearman's rho = 0.0489, P > 0.05).
Both species exhibited a similar pattern in the spat sizes they consumed (Fig. 2). Spat size was negatively correlated with the mean number of spat consumed (E. depressus: Spearman's rho = -0.8488, P < 0.0001; R. harrisii: Spearman's rho = -0.8767, P < 0.0001). Approximately 75% of spat preyed on by both species were less than 8 mm. Mean spat size preyed upon for E. depressus was 5.92 [+ or -] 0.25 mm, and 5.52 [+ or -] 0.29 mm for R. harrisii. The largest spat that E. depressus and R. harrisii preyed on were 23 mm and 12 mm, respectively.
Spat Predation by Size Class
Within each size class, E. depressus preyed on a significantly larger proportion of available spat than R. harrisii (individual size class results described later; for all size classes, Wilcoxon's rank sum test, P < 0.0001; E. depressus, n = 38; R. harrisii, n = 34; Fig. 3). Furthermore, in both species, the mean percentage of spat consumed among the size classes was significantly different (for both species: P < 0.0001). In both species, the small size class (1-5 mm) showed the highest predation rate over 4 days and the large size class (>10 mm) showed the lowest. E. depressus consumed 61.9 [+ or -] 4.5% of available small spat over 4 days and R. harrisii consumed 19.7 [+ or -] 3.4%. In contrast, E. depressus preyed on 11.9 [+ or -] 2.5% of available large spat and R. harrisii preyed on 0.9 [+ or -] 0.8%. In addition, the highest percentages of available small and medium spat were consumed during the first 48 h (Table 2). Within each time period, the crabs consumed spat in the small size class at approximately twice the rate as those in the medium size class. Alternatively, for the large size class, E. depressus consumed similar percentages in each time period, whereas R. harrisii consumed no large spat in the second and last day.
[FIGURE 2 OMITTED]
There were 22 E. depressus and R. harrisii individuals whose CWs were not significantly different, ranging from 10-13 mm (Wilcoxon's rank sum test, P < 0.1228; E. depressus, n = 11; R. harrisii, n = 11). Of these crabs, E. depressus consumed a significantly greater proportion of spat than R. harrisii in each size class (for the small size class, P < 0.0017; for the medium size class, P < 0.0110; for the large size class, P < 0.0239; E. depressus, n = 11; R. harrisii, n = 11). Specifically, E. depressus consumed 63.3 [+ or -] 9.1% of available small spat, 28.8 [+ or -] 6.7% of available medium spat, and 6.0 [+ or -] 3.3 % of available large spat over 4 days, whereas R. harrisii consumed 12.9 [+ or -] 4.8%, 9.4 [+ or -] 4.5%, and 0%, respectively.
Based on the results of this study, E. depressus could be a substantial predator of spat in the Maryland portion of the Chesapeake Bay. Of the available spat, E. depressus preyed on 37%, whereas R. harrisii preyed on 9% of available spat within 96 h. Sizes of spat preyed on ranged from 1-23 mm, but the vast majority of the spat consumed were between 1 mm and 8 mm. Because the hatchery-based restoration program in Maryland typically plants spat within this size range, these two predators could have a significant influence on survivorship of juvenile oysters.
[FIGURE 3 OMITTED]
To assess the relative contribution E. depressus and R. harrisii have on spat mortality, results were compared with predation rates of two other important crab predators of spat: C. sapidus and P. herbstii. Daily predation rates by C. sapidus and P. herbstii were more than double the 4-day predation rate of either E. depressus or R. harrisii (Bisker & Castagna 1987). However, Bisker and Castagna (1987) used "cultchless" spat, which has been shown to be easier to handle and results in higher spat mortality (Krantz & Chamberlain 1978). Although E. depressus and R. harrisii did not prey on as many spat as C. sapidus and P. herbstii, E. depressus and R. harrisii could have a substantial impact on spat survival based on their abundances on oyster reefs in Maryland. From preliminary counts, E. depressus has been found in densities of 100 crabs/[m.sup.2] in the Patuxent River, whereas R. harrisii has been found in densities of 100 crabs/[m.sup.2] in the Severn River (Harwell, unpubl.). Based on the estimated predation rates from the current study, the E. depressus population within a 1-[m.sup.2] area could have the capacity to consume more than 2,000 spat in 4 days and R. harrisii could have the capacity to consume approximately 500 spat during the same time period. Because restoration efforts in Maryland plant about 250-500 spat/[m.sup.2], E. depressus and R. harrisii populations could reduce those spat densities by half or more, especially in areas where crab densities are high. In addition, population levels of E. depressus and R. harrisii have been shown to be four orders of magnitude higher on restored oyster reefs compared with nonrestored reefs, suggesting that crab population levels respond to the addition of shell and an increase in oyster reef complexity (Rodney & Paynter 2006).
Predation rates found in this study were also compared with those previously reported for E. depressus and R. harrisii. The percentage of available C. virginica spat consumed by R. harrisii in 96 h was consistent with findings in the work by Newell et al. (2007), who had given individual crabs a choice of consuming either C. ariakensis or C. virginica spat over 30 days. Conversely, E. depressus in the current study had preyed on a greater percentage of available C. virginica spat than found in Newell et al. (2007). Although both species were shown to consume significantly more C. ariakensis than C. virginica in Newell et al. (2007), the added presence of C. ariakensis may have had more of an influence on the C. virginica predation potential for E. depressus than R. harrisii. In addition, our study observed a higher average daily E. depressus predation rate of 5.7 crabs per day compared with the 3.8 spat crabs per day reported by McDermott (1960). The difference in predation rates could be attributed to the influence of intraspecific competition, because McDermott (1960) did not separate crabs into individual containers.
The sizes of the crabs collected in this study likely reflect the natural size distribution found in the upper Chesapeake Bay. Typically, E. depressus grows to a larger CW than R. harrisii (Ryan 1956). Even though the CWs were significantly different between species, we do not believe the difference in crab size explains their differing predation rates. Among individuals that had similar CWs, E. depressus still consumed a significantly greater proportion of spat than R. harrisii in each size class. The differing predation rates may instead indicate that the two species have different resource preferences. Milke and Kennedy (2001) found a greater crusher claw mechanical advantage in E. depressus than R. harrisii, which may allow E. depressus to remove spat from the shell more effectively. This difference in claw strength may result in a shorter processing time for spat predation by E. depressus than R. harrisii, making C. virginica a more efficient food resource for E. depressus. Further investigations need to be conducted before the prey dynamics of E. depressus and R. harrisii are clearly understood.
Both crab species showed clear spat size preferences, preferring smaller spat (1-5 mm). The observed size frequency distribution cannot be explained purely by chelae mechanical limits because both mud crab species demonstrated an ability to open large spat (>10 mm). In addition, despite the ability of E. depressus to open larger spat than R. harrisii, E. depressus still preyed on the same mean spat size range as R. harrisii. Furthermore, our study found that both species were capable of preying on larger spat than found in Newell et al. (2007), suggesting that E. depressus and R. harrisii actively select smaller spat. Crab selection of smaller spat has been recorded in multiple predation studies, and may be a direct result of energetic costs (Elner & Lavoie 1983, Bisker & Castagna 1987, Eggleston 1990, Brown & Haight 1992, Juanes 1992). Shell strength and handling time need to be investigated further to uncover the underlying cause behind smaller spat selection in R. harrisii and E. depressus.
The patterns in the spat sizes preyed on could be used to estimate a size refuge from E. depressus and R. harrisii predation. Approximately 75% of spat preyed on were less than 8 mm in size. After spat grow to 8 mm in size, E. depressus and R. harrisii may become less efficient in their predation on spat, thus potentially decreasing predation pressure. Currently, the spat planted for restoration are approximately 1 mm in size (Paynter, pers. obs.). Although spat grow at different rates under different environmental conditions, spat have been shown to grow approximately 12 mm per month from July to October (Paynter & DiMichele 1990). Based on that growth rate, spat would be vulnerable to mud crab predation for at least 2 wk after planting and settlement. However, predation rates in the benthos could be very different from what has been measured in the laboratory. Additional predation experiments should be repeated in the field, which may provide a more realistic representation of spat predation in the Maryland portion of the Chesapeake Bay.
We thank Karen Kesler, Grace Chon, and Anthony Strube for their contributions to the project; as well as Jiuzhou Song for his help with the statistical analysis. We also thank the oyster hatchery at Horn Point Laboratory for supplying the spat for this project. Support for this research was provided by a grant to the University of Maryland from the Howard Hughes Medical Institute and the Oyster Recovery Partnership.
Bisker, R. & M. Castagna. 1987. Predation on single spat oysters Crassostrea virginica (Gmelin) by blue crabs Callinectes sapidus Rathbun and mud crabs Panopeus herbstii Milne-Edwards. J. Shellfish Res. 6:37-40.
Brown, K. M. & E. S. Haight. 1992. The foraging ecology of the Gulf of Mexico stone crab Menippe adina (Williams et Felder). J. Exp. Mar. Biol. Ecol. 160:67-80.
Burreson, E. M. & L. M. Ragone Calvo. 1996. Epizootiology of Perkinsus marinus disease of oysters in Chesapeake Bay, with emphasis on data since 1985. J. Shellfish Res. 15:17-34.
Dame, R. F. 1979. The abundance, diversity, and biomass of macrobenthos on north inlet, South Carolina, intertidal oyster reefs. Proc. Natl. Shellfish. Assoc. 69:6-10.
Eggleston, D. B. 1990. Foraging behavior of the blue crab, Callinectes sapidus, on juvenile oysters, Crassostrea virginica: effects of prey density and size. Bull. Mar. Sci. 46:62-82.
Elner, R. W. & R. E. Lavoie. 1983. Predation on American oysters (Crassostrea virginica [Gmelin]) by American lobsters (Homarus americanus Milne-Edwards), rock crabs (Cancer irroratus Say), and mud crabs (Neopanope sayi [Smith]). J. Shellfish Res. 3:129-134.
Ford, S. E. & M. R. Tripp. 1996. Disease and defense mechanisms. In: V. S. Kennedy, R. I. E. Newell & A. F. Eble, editors. The Eastern oyster, Crassostrea virginica. College Park, MD: Maryland Sea Grant Publications. pp. 581-660.
Grabowski, J. H. 2004. Habitat complexity disrupts predator-prey interactions but not the trophic cascade on oyster reefs. Ecology 85:995-1004.
Grizzle, R. E., J. K. Greene & L. D. Coen. 2008. Seston removal by natural and constructed intertidal Eastern oyster (Crassostrea virginica) reefs: a comparison with previous laboratory studies, and the value of in situ methods. Estuaries Coasts 31:1208-1220.
Harwell, H. D. 2010. Habitat complexity and habitat function of native (Crassostrea virginica) and non-native (Crassostrea ariakensis) oysters in the Chesapeake Bay region. PhD diss., Virginia Institute of Marine Science. 202 pp.
Juanes, F. 1992. Why do decapod crustaceans prefer small-sized molluscan prey? Mar. Ecol. Prog. Ser. 87:239-249.
Kemp, W.M., W.R. Boynton, J.E. Adolf, D.F. Boesch, W. C. Boicourt, G. Brush, J.C. Cornwell, T. R. Fisher, P. M. Glibert, J. D. Hagy, L. W. Harding, E. D. Houde, D. G. Kimmel, W. D. Miller, R. I. E. Newell, M. R. Roman, E. M. Smith & J. C. Stevenson. 2005. Eutrophication of Chesapeake Bay: historical trends and ecological interactions. Mar. Ecol. Prog. Ser. 303:1-29.
Kennedy, V. S. 1996. The ecological role of the Eastern oyster, Crassostrea virginica, with remarks on disease. J. Shellfish Res. 15:172-183.
Kirby, M. X. & H. M. Miller. 2005. Response of a benthic suspension feeder (Crassostrea virginica Gmelin) to three centuries of anthropogenic eutrophication in Chesapeake Bay. Estuar. Coast. Shelf Sci. 62:679-689.
Krantz, G. E. & J. V. Chamberlain. 1978. Blue crab predation on cultchless oyster spat. Proc. Natl. Shellfish. Assoc. 8:38-41.
McDermott, J. J. 1960. The predation of oysters and barnacles by crabs of the family Xanthidae. Proc. Penn. Acad. Sci. 34:199-211.
Milke, L. M. & V. S. Kennedy. 2001. Mud crabs (Xanthidae) in Chesapeake Bay: claw characteristics and predation on epifaunal bivalves. Invertebr. Biol. 120:67-77.
Nelson, K. A., L. A. Leonard, M. H. Posey, T. D. Alphin & M. A. Mallin. 2004. Using transplanted oyster (Crassostrea virginica) beds to improve water quality in small tidal creeks: a pilot study. J. Exp. Mar. Biol. Ecol. 298:347-368.
Newell, R. I. E. 1988. Ecological changes in Chesapeake Bay: are they the result of overharvesting the American oyster, Crassostrea virginica? In: M. P. Lynch & E. C. Krome, editors. Understanding the estuary: advances in Chesapeake Bay research. Solomons, MD: Chesapeake Research Consortium. pp. 536-546.
Newell, R. I. E., G. S. Alspach, V. S. Kennedy & D. Jacobs. 2000. Mortality of a newly metamorphosed Eastern oysters (Crassostrea virginica) in mesohaline Chesapeake Bay. Mar. Biol. 136:665-676.
Newell, R. I. E., V. S. Kennedy & K. S. Shaw. 2007. Comparative vulnerability of predators, and induced defense responses, of Eastern oysters Crassostrea virginica and non-native Crassostrea ariakensis oysters in Chesapeake Bay. Mar. Biol. 152:449-460.
O'Conner, N. E., J. H. Grabowski, L. M. Ladwig & J. F. Bruno. 2008. Simulated predator extinctions: predator identity affects survival and recruitment of oysters. Ecology 89:428-438.
Paynter, K. T. 1999. Managing around oyster diseases in Maryland and Maryland oyster roundtable strategies. In: M. W. Luckenbach, R. Mann & J. A. Wesson, editors. Oyster reef habitat restoration: a synopsis and synthesis of approaches. Gloucester Point, VA: Virginia Institute of Marine Science Press. pp. 317-328.
Paynter, K. T. 2009. Oyster recovery monitoring report. Annual report to the Oyster Recovery Partnership, Annapolis, MD. 57 pp.
Paynter, K. T. & L. DiMichele. 1990. Growth of tray-cultured oysters (Crassostrea virginica Gmelin) in Chesapeake Bay. Aquaculture 87:289-297.
Paynter, K. T., V. Politano, H. A. Lane, S. Allen & D. Meritt. 2010. Growth rates and Perkinsus marinus prevalence in restored oyster populations in Maryland. J. Shellfish Res. 29:309-317.
Porter, E. T., J. C. Cornwell & L. P. Sanford. 2004. Effect of oysters Crassostrea virginica and bottom shear velocity on benthic-pelagic coupling and estuarine water quality. Mar. Ecol. Prog. Ser. 271:61-75.
Rodney, W. S. & K. T. Paynter. 2006. Comparisons of macrofaunal assemblages on restored and non-restored oyster reefs in mesohaline regions of Chesapeake Bay in Maryland. J. Exp. Mar. Biol. Ecol. 335:39-51.
Rothschild, B. J., J. S. Ault, P. Goulletquer & M. Heral. 1994. Decline of the Chesapeake Bay oyster population: a century of habitat destruction and overfishing. Mar. Ecol. Prog. Ser. 111:29-39.
Ryan, E. P. 1956. Observations on the life histories and the distribution of the Xanthidae (mud crabs) of Chesapeake Bay. Am. Midl. Nat. 56:138-162.
Seed, R. 1980. Predator-prey relationships between the mud crab Panopeus herbstii, the blue crab, Callinectes sapidus and the Atlantic ribbed mussel Geukensia (=Modiolus demissa). Estuar. Coast. Mar. Sci. 11:445-458.
Tarnowski, M. 2010. Maryland oyster population status report. 2009 Fall survey. Maryland Department of Natural Resources, Shellfish Program, Cooperative Oxford Laboratory. Oxford, MD: Department of Natural Resources. MDNR publication no. 17-8172010-471. 48 pp.
Tolley, S. G. & A. K. Volety. 2005. The role of oysters in habitat use of oyster reefs by resident fishes and decapods crustaceans. J. Shellfish Res. 24:1007-1012.
Wells, H. W. 1961. The fauna of oyster beds, with species reference to the salinity factor. Ecol. Monogr. 31:239-266.
Whetstone, J. M. & A. G. Eversole. 1981. Effects of size and temperature on mud crab, Panopeus herbstii, predation on hard clams, Mercenaria mercenaria. Estuaries 4:153-156.
Woods, H., W. J. Hargis, C. H. Hershner & P. Mason. 2005. Disappearance of the natural emergent 3-dimensional oyster reef system of the James River, Virginia, 1871-1948. J. Shellfish Res. 24:139-142.
REBECCA E. KULP, VINCE POLITANO, HILLARY A. LANE, SARA A. LOMBARDI AND KENNEDY T. PAYNTER *
Department of Biology, University of Maryland, College Park, Maryland 20 742
* Corresponding author. E-mail: firstname.lastname@example.org
TABLE 1. Percentage of Crassostrea virginica spat preyed on by Eurypanopeus depressus and Rhithropanopeus harrisii during each 24-h time period of the study. Time Periods (h) Species 0-24 24-48 Eurypanopeus depresses 16.2 ([+ or -] 2.1) 13.6 ([+ or -] 2.0) Rhithropanopeus harrisii 6.1 ([+ or -] 1.3) 3.03 ([+ or -] 0.8) Time Periods (h) Species 48-72 72-96 Eurypanopeus depresses 9.4 ([+ or -] 1.5) 7.9 ([+ or -] 7.7) Rhithropanopeus harrisii 1.3 ([+ or -] 0.5) 0.9 ([+ or -] 1.7) TABLE 2. Percentages of Crassostrea virginica spat preyed upon by Eurypanopeus depressus and Rhithropanopeus harrisii in each spat size class during each 24-h time period. Eurypanopeus depressus * Time Periods (h) Size class 0-24 24-48 Small 26.5 ([+ or -] 3.5) 27.3 ([+ or -] 4.0) Medium 13.9 ([+ or -] 1.9) 11.4 ([+ or -] 1.9) Large 3.7 (1.2) 2.2 ([+ or -] 4.4) Rhithropanopeus harrisii ([dagger]) Time Periods (h) Size Class 0-24 24-48 Small 12.2 ([+ or -] 2.5) 11.0 ([+ or -] 4.4) Medium 6.0 ([+ or -] 1.6) 2.6 ([+ or -] 0.7) Large 1.6 ([+ or -] 1.5) 0 ([+ or -] 0) Eurypanopeus depressus * Time Periods (h) Size class 48-72 72-96 Small 24.7 ([+ or -] 4.5) 13.6 ([+ or -] 2.6) Medium 8.0 ([+ or -] 1.4) 7.1 ([+ or -] 1.8) Large 3.0 ([+ or -] 0.9) 4.4 ([+ or -] 1.3) Rhithropanopeus harrisii ([dagger]) Time Periods (h) Size Class 48-72 72-96 Small 3.1 ([+ or -] 1.5) 2.9 ([+ or -] 1.8) Medium 0.9 ([+ or -] 0.4) 0.7 ([+ or -] 0.4) Large 0.5 ([+ or -] 0.5) 0 ([+ or -] 0) * Spat consumption by E. depressus. ([dagger]) Spat consumption by R. harrisii. The 3 size classes were small (1-5 mm), medium (6-10 mm), and large (>10 mm). SEM is displayed in parentheses.
|Printer friendly Cite/link Email Feedback|
|Author:||Kulp, Rebecca E.; Politano, Vince; Lane, Hillary A.; Lombardi, Sara A.; Paynter, Kennedy T.|
|Publication:||Journal of Shellfish Research|
|Date:||Aug 1, 2011|
|Previous Article:||The status of silverlip pearl oyster Pinctada maxima (Jameson) (mollusca, pteridae) in the Solomon Islands after a 15-year export ban.|
|Next Article:||Effect of marine acidification on calcification and respiration of Chlamys farreri.|