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Population Dynamics and Parasite Load of a Foraminifer on Its Antarctic Scallop Host with Their Carbonate Biomass Contributions

  • Leanne G. Hancock ,

    Contributed equally to this work with: Leanne G. Hancock, Sally E. Walker

    Current address: Department of Earth Sciences, University of California, Riverside, California, United States of America

    Affiliation Department of Geology, University of Georgia, Athens, Georgia, United States of America

  • Sally E. Walker ,

    Contributed equally to this work with: Leanne G. Hancock, Sally E. Walker

    Affiliation Department of Geology, University of Georgia, Athens, Georgia, United States of America

  • Alberto Pérez-Huerta ,

    ‡ These authors also contributed equally to this work.

    Affiliation Department of Geological Sciences, University of Alabama, Tuscaloosa, Alabama, United States of America

  • Samuel S. Bowser

    ‡ These authors also contributed equally to this work.

    Affiliation Wadsworth Center, New York State Department of Health, Albany, New York, United States of America

Population Dynamics and Parasite Load of a Foraminifer on Its Antarctic Scallop Host with Their Carbonate Biomass Contributions

  • Leanne G. Hancock, 
  • Sally E. Walker, 
  • Alberto Pérez-Huerta, 
  • Samuel S. Bowser


We studied the population dynamics and parasite load of the foraminifer Cibicides antarcticus on its host the Antarctic scallop Adamussium colbecki from three localities differing by sea ice cover within western McMurdo Sound, Ross Sea, Antarctica: Explorers Cove, Bay of Sails and Herbertson Glacier. We also estimated CaCO3 biomass and annual production for both species. Cibicides populations varied by locality, valve type, and depth. Explorers Cove with multiannual sea ice had larger populations than the two annual sea ice localities, likely related to differences in nutrients. Populations were higher on Adamussium top valves, a surface that is elevated above the sediment. Depth did not affect Cibicides distributions except at Bay of Sails. Cibicides parasite load (the number of complete boreholes in Adamussium valves) varied by locality between 2% and 50%. For most localities the parasite load was < 20%, contrary to a previous report that ~50% of Cibicides were parasitic. The highest and lowest parasite load occurred at annual sea ice localities, suggesting that sea ice condition is not important. Rather, the number of adults that are parasitic could account for these differences. Cibicides bioerosion traces were categorized into four ontogenetic stages, ranging from newly attached recruits to parasitic adults. These traces provide an excellent proxy for population structure, revealing that Explorers Cove had a younger population than Bay of Sails. Both species are important producers of CaCO3. Cibicides CaCO3 biomass averaged 47-73 kg ha-1 and Adamussium averaged 4987-6806 kg ha-1 by locality. Annual production rates were much higher. Moreover, Cibicides represents 1.0-2.3% of the total host-parasite CaCO3 biomass. Despite living in the coldest waters on Earth, these species can contribute a substantial amount of CaCO3 to the Ross Sea and need to be incorporated into food webs, ecosystem models, and carbonate budgets for Antarctica.


Parasites are emerging as important ecological agents for structuring plant and animal communities, signifying the vitality or degradation of ecosystems [13]. Parasitic biomass often exceeds that of top predators in marine systems, affecting ecosystem function [4]. Despite their importance, the majority of food web topologies exclude parasites [56]. Indeed, the most recent food-web topology for Antarctic ecosystems does not include parasites or the ubiquitous foraminifera [7].

Foraminifera are diverse and abundant in marine ecosystems [8]. They enter into marine food webs at multiple trophic levels, including suspension feeding, grazing, predation, and parasitism [915]. Importantly, foraminifera exhibit multiple trophic modes [13]. Thereby, a single species enters into a food web at multiple levels, with implications for ecosystem function. Of these trophic modes, parasitism is the least well understood.

We examined the relationship between the parasitic foraminifer Cibicides antarcticus and its host, the Antarctic scallop Adamussium colbecki, which live in the coldest waters on Earth near the freezing point of seawater (-1.97 °C). Both species are circum-Antarctic in distribution. Epibenthic Adamussium is considered a major ecosystem engineer because of its large population size, often covering 100% of the seafloor with densities up to 90 m-2 in some locations [1620].

Cibicides antarcticus (formerly C. refulgens in Antarctica) is a facultative parasite. It bores a hole through Adamussium valves with its pseudopods and assimilates 14C-labeled amino acids from the extrapallial cavity [13, 20]. This cavity, which is located between the shell of the mollusk and the mantle, contains fluid that is compositionally different from that of seawater, and is often enriched in calcium ions and amino acids [1314]. Parasitism is thought to occur in 50% of Cibicides populations at Explorers Cove, based on observations from five Adamussium valves [13]. However, a systematic examination of C. antarcticus populations and parasitism using a larger sample size of Adamussium from different Antarctic localities has not been conducted. If Cibicides also suspension feeds and grazes on diatoms [13], it would be important to document the contribution of parasitism to its trophic behavior.

We first examined living Cibicides populations and their bioerosion traces on Adamussium across three Antarctic marine localities from western McMurdo Sound in the Ross Sea: Explorers Cove, Bay of Sails and Herbertson Glacier. Explorers Cove is well known for its foraminifera [2125]. Unlike the other localities, it has multiannual sea ice with partial melt outs since 1991 [26]. It is also situated at the mouth of the Taylor Dry Valley, part of the largest ice-free region in Antarctica [27]. Bay of Sails and Herbertson Glacier experience annual sea ice and are adjacent to glaciated terrane [26, SSB and SEW personal observations]. Microalgae and microbes associated with sea ice are a major food resource for Arctic and Antarctic organisms [2829]. Foraminifera populations are higher at Explorers Cove than Bay of Sails, and this difference could be related to sea ice algae [26]. If so, then parasitism should be rare at Explorers Cove because suspension feeding and grazing would be more important trophic strategies.

Cibicides antarcticus etches permanent traces into Adamussium shells [13]. We categorized these traces into four ontogenetic stages ranging from new recruits to parasitic adults. These stages were then used to examine population structure, spatial distribution, and parasitism in Cibicides. Within this framework, traces can be used in modern and fossil communities as an important life history proxy for Cibicides when it is no longer attached to the shell. Moreover, because C. antarcticus and A. colbecki have a fossil record extending to the Pliocene in Antarctica [3031], these traces provide an evolutionary archive for the development of the host-parasite relationship.

Lastly, we estimated the CaCO3 biomass produced by the host-parasite relationship, as biomass is a long-established measure for ecosystem energetics [4]. In deep-sea communities, foraminifera account for up to 50% of the biomass derived from eukaryotic organisms [32]. In tropical reefs, foraminifera may contribute up to 43 million tons of CaCO3 per year (3.90 x1010 kg yr-1), which has significant implications for CO2 production in the world’s oceans [33]. In particular, reef and planktonic foraminifera may contribute ~1.4 billion tons of CaCO3 a year (1.27 x 1012 kg yr-1) accounting for ~ 25% of oceanic carbonate production [34]. While reef and planktonic foraminifera are well studied, we know little about the role of polar foraminifera in contributing CaCO3 to the world’s oceans. In fact, CaCO3 estimates for polar regions are generally lacking from global CaCO3 budgets [3536]. Recently, macrozoobenthic organisms were described as unimportant for Antarctic CaCO3 budgets [37]. However, that study did not include foraminifera or other epibenthic communities important for estimating CaCO3 production. Therefore, we also examined the CaCO3 biomass and annual production for C. antarcticus and its host A. colbecki.

Materials and Methods

Study locations

We examined Cibicides populations from three localities within McMurdo Sound, Ross Sea, Antarctica (Fig 1): Explorers Cove (EC, 77°34.259'S, 163°30.699'E), Bay of Sails (BOS, 77°21.911'S, 163°32.594'E) and Herbertson Glacier (HG, 77°41.724'S, 163°54.662'E). McMurdo Sound represents the southernmost extension of the Ross Sea [25]. These localities occur in western McMurdo Sound, a region characterized by oligotrophic, nutrient-depleted waters because the water mass that bathes this region has circulated under the Ross Ice Shelf [3839]. Benthic and water column primary productivity is higher in eastern than western McMurdo Sound [4041]. Diatom and organic carbon fluxes are up to two orders of magnitude greater in eastern McMurdo Sound [4243]. As a consequence, the benthic community in western McMurdo Sound resembles the bathyal deep sea [43]. Dominant megafauna in this region include epibenthic Adamussium, ophiuroids, and echinoids [16, 38, 44].

Fig 1. Localities in McMurdo Sound, Ross Sea, Antarctica.

Map modified with permission from Antarctic New Zealand.

Explorers Cove is a marine embayment located at the mouth of the Taylor Dry Valley [24]. It is characterized by gentle topography with rare glacial erratics [23]. Sediments are polymictic fine silty sands with a modal grain size of 125–300 μm [45]. Water currents are negligible except for tidal exchange, with estimates varying between <1 cm/sec to 2.6 cm/sec [4647]. Sea ice has remained largely intact since 1993 with partial melt outs in 1999, 2002 and 2011 [26]. Iceberg disturbance has not occurred in this cove since 1981 [25]. During austral summer, glacially-derived freshwater flows into EC from Commonwealth and Wales deltas [13, 25]. At the time of collection, bottom water temperature was -1.97 °C with a salinity of 35–37 PSU and a pH of 7.6.

Bay of Sails is ~ 30 km north of EC and is located offshore of the Wilson Piedmont Glacier [26]. It is named for the persistent icebergs located offshore. Underwater topography is similar to EC, but with more glacial erratics [SSB personal observation]. Unlike EC, sea ice melts out every year at BOS [26]. Sediments are polymictic very fine sand with a modal grain size of 63–125 μm [26]. Water currents have not been measured and based on diving observations appear to be similar to EC [SSB personal observation]. Iceberg disturbance is likely high in this region, but has not been quantified. During austral summer BOS receives freshwater from the Wilson Piedmont Glacier [SEW personal observation]. At the time of collection, benthic seawater had a temperature of -1.97 °C, a salinity of 35.8 PSU and a pH ~ 7.9 [26].

The HG locality is located in shallow water just offshore of Herbertson Glacier in the Ferrar Glacier embayment. The topography is similar to BOS [SSB personal observation]. Icebergs were not observed in the region of Herbertson Glacier, but they can calve from the Ferrar Glacier [SEW personal observation]. The HG locality has annual sea ice cover and polymictic fine silty sands with a modal grain size of 125–250 μm ( Bottom water had a temperature of -1.97 °C, a salinity of 35.6 PSU and a pH ~7.

Temperature, salinity and pH data were recorded by a YSI sonde deployed by divers at each depth. The sonde equilibrated for 10–15 minutes until stable readings were obtained. The pH probe is certified to -4 °C seawater and was calibrated with three pH standards (4.0, 7.0, and 10.0) prior to each dive. Salinity was calibrated using a 50mS cm-1 standardized solution from YSI International.

Scallop collections

Adamussium were collected from two depths (9 m, 18 m) at each locality in November 2008. Scallops were haphazardly collected by divers (i.e., the nearest scallop bed that was closest to the dive site). Valves of similar size were targeted to control for surface area that could affect Cibicides abundance. Five top (left) and five bottom (right) valves were randomly chosen from each depth for a total of 20 valves per locality. Valve length, width, shell area, and weight were measured. Mean shell height was similar for EC and BOS (EC: n = 20, mean = 8.30 cm, SD = 0.30; BOS: n = 20, mean = 8.68 cm, SD = 0.38); valves from HG were slightly smaller (n = 20, mean = 7.11 cm, SD = 0.42).

Living Cibicides

To determine if attached Cibicides were alive or dead on scallop valves, SSB tethered a live Adamussium with 118 Cibicides living on the top valve in 2005 at 21 m at EC. Video of tethered Adamussium was taken using a JVC Model VN-C30U steerable camera mounted in a custom-built underwater housing from Magee Scientific Company, Berkeley, CA. The top valve was retrieved a year later and fixed with 3% formalin, slightly decalcified, stained with 0.1% Rose Bengal, and examined using a Zeiss SMZ-2T stereomicroscope equipped with a SPOT model 29.2–1.3MP color camera. Attached Cibicides were counted from photographs and their spatial positions were compared to pre-deployment positions.

Cibicides populations by locality, valve type, and depth

Cibicides populations were assessed three ways: 1) Attached Cibicides represent the living population, 2) bioerosion traces represent previous Cibicides populations that are no longer attached to the shell, and 3) attached Cibicides with traces left by previously attached Cibicides represents the total population that has accumulated over the lifespan of the scallop. We expected that Cibicides populations were not significantly different between localities, valve type (top and bottom valves) and depth.

Cibicides and their bioerosion traces were counted on Adamussium valves under a binocular/stereomicroscope at 200-750x. Selected Cibicides and traces were examined with a scanning electron microscope (SEM). To determine if Cibicides populations increased with increasing scallop area, attached Cibicides data were analyzed using a generalized linear model (GLM) with quasipoisson for over-dispersed count data [48]. Welch two-sample t-tests and multiple sample chi-squared tests were run with Cibicides and traces separately and then pooled to ascertain significant differences between localities, valve type, and depth. All statistics were performed in R at alpha = 0.05 unless otherwise specified [49].

Parasite load

The parasite load represents the total number of complete boreholes made by Cibicides on each valve. We expected that the parasite load would not vary significantly between localities, valve type, and depth. We did expected that the parasite load would be higher on top valves than bottom valves because a small part of the bottom valve rests on the seafloor, decreasing surface area for foraminifera to settle. The mean number of Cibicides with and without complete boreholes for all localities were plotted with 95% CIs. Significant differences in the number of boreholes between depths and valve type were tested using Fisher Exact Tests (FETs).

Cibicides population structure and spatial distribution

Population structure.

Cibicides population structure, from the initial attachment trace to the parasitic borehole, was assessed using bioerosion traces. We categorized the traces into ontogenetic stages (herein referred to as trace type) based on the size and morphology of the resting trace in relation to borehole development. We use “ontogenetic” because this term was used previously to examine young versus old bioerosion traces made by another parasitic foraminifera Hyrrokkin sarcophaga, although they did not categorize the traces into growth stages [50]. We then examined the spatial distribution of these trace types on Adamussium valves using six additional top valves from EC and BOS that were randomly selected from the initial scallop collection (n = 3 valves per locality). HG was omitted because the remaining shells were much smaller than those from EC and BOS. The outer resting trace and borehole diameter were measured in mm using the image analysis package iSolution Lite, IMT i-Solution Inc., Vancouver, Canada (Fig 2A). We used the outer resting trace because it represents the basal diameter of C. antarcticus. The borehole diameter will be discussed in a future paper. To determine if EC and BOS had significantly different trace types, Kruskal-Wallis ANOVAs (K-W tests) and post-hoc Wilcoxon tests (W tests) were used. The data were subset for the post-hoc tests yielding alpha = 0.008. We expected that trace-types would be similar between the localities.

Fig 2. Trace Measurements and Sectors used to Examine Cibicides Population Structure on Adamussium.

A. iSolution Lite image showing polygons that were used to measure exterior resting trace and interior borehole diameter. B. Sectors on Adamussium shell that were used to examine the spatial distribution of Cibicides bioerosion traces.

Spatial distribution.

Trace type spatial distribution was examined by dividing the shell surface into sectors (Fig 2B) (after [26, 51]). Sectors were selected based on shell topography because foraminifera are sensitive to microhabitats. Cibicides could settle in certain sectors to increase their ability to obtain nutrients from suspension feeding, grazing or parasitism. Sectors 1 and 2 are the auricles that were identified previously as an area with the greatest number of encrusting foraminifera [26]. Sector 3 is the umbo, the oldest part of the shell. Sectors 4–7 represent the center area of the valve, below which the mantle, muscle, gill, and gonadal tissue reside. Sectors 8–11 represent the outer edge of the scallop and the youngest shell surfaces. Densities for each trace type per sector were standardized to cm2 and were used to evaluate significant patterns in Cibicides spatial distributions. To determine the cut-off value for significantly higher or lower mean density of a particular trace type in a sector, one-sample t-tests were used to generate upper and lower 95% CIs. We expected that if Cibicides occurred randomly on Adamussium top valves, all trace types would have similar densities in each sector.

CaCO3 biomass and annual production

Cibicides CaCO3 biomass was estimated in a series of steps. First, we weighed 579 individual Cibicides from two randomly selected EC top valves used in the previous population study. Cibicides were cleaned, dried at 70 °C for 24 hours, and weighed on a microbalance to the nearest mg to yield CaCO3 biomass. We assumed, like previous studies for foraminifera biomass, that their tests were primarily CaCO3 [3334, 52]. Second, mean Cibicides CaCO3 biomass was binned into seven size classes of 0.10 mg increments and plotted with 95% CIs to determine if significant differences existed between size classes. Lastly, the mean for the entire sample was estimated. The mean provides a conservative estimate for CaCO3 biomass for foraminifera [3334, 52].

We next estimated the CaCO3 biomass of Adamussium. First, we had to determine if their shells were mostly pure carbonate before using them for CaCO3 biomass estimates. Four top valves from EC were cleaned of epibionts, washed with DI water, dried, powdered and subjected to the Loss on Ignition method [53]. The shells yielded a mean organic carbon content of 0.010g Corg (SD = 0.001g; 0.03 wt% Corg) indicating that Adamussium shells are primarily CaCO3. Valve weights were then used as a proxy for CaCO3 biomass.

CaCO3 biomass density was calculated in two steps. First, the total number of attached Cibicides on top valves was divided by the total shell area for each locality, yielding the mean number of Cibicides per cm2. Second, the mean number of Cibicides per cm2 was multiplied by the mean Cibicides biomass to provide a conservative estimate of CaCO3 biomass that was then converted to kg ha-1. The mean carbonate biomass density for Adamussium was calculated by dividing the total shell CaCO3 weight by the total shell area for each locality and converted to kg ha-1. Mean CaCO3 biomass density for both species was plotted with 95% CIs to determine if there were significant differences among localities. We then wanted to determine how much CaCO3 Cibicides contributes to the host-parasite relationship by examining its percent contribution [after 4]. This percent was calculated using the mean biomass estimate divided by the host + parasite biomass (in kg ha-1) for each locality.

We calculated the annual CaCO3 production for Cibicides and Adamussium because annual biomass production reveals ecosystem productivity [4]. To calculate yearly production, we had to determine the turnover rate of Cibicides and Adamussium and then convert their CaCO3 biomass to yearly production. We estimated that the turnover rate was two years for Cibicides and 20 years for Adamussium. Cibicides two-year turnover was based on experimental arrays deployed at EC in austral summer 2008 (SEW personal observation). The experimental arrays had clean Adamussium shell pieces encased within plankton-mesh bags. When the arrays were retrieved two years later (2010), adult Cibicides were attached to the shell pieces. Juveniles were also observed within a Cibicides test in 2008, indicating that they are released during austral summer. As a consequence, propagules may have entered the mesh bags in austral summer 2008, likely growing to their largest size within two years. Additionally, a survivorship analysis based on size classes generated from Cibicides biomass revealed that it has a Type I curve, exhibiting high juvenile survivorship with mortality increasing with age (S1 Fig). Adamussium’s lifespan is thought to be 20 years based on growth-band analysis and mark-recapture estimates [5457]. Therefore, CaCO3 production per year was calculated based on the mean CaCO3 biomass per m2 for each species divided by their turnover rates and then converted to kg ha-1 yr-1.

Next, we wanted to compare CaCO3 biomass density across localities. This was calculated using the number of attached Cibicides and Adamussium at each locality and multiplying each species by its mean CaCO3 biomass. Cibicides and Adamussium mean biomass estimates per locality were plotted with 95% CIs to determine if there were significant differences among localities. We expected that scallop biomass would not differ among localities but Cibicides biomass would be variable because of variation in population size.

Lastly, we quantified the contribution that attached Cibicides makes to the total CaCO3 biomass produced by the species pair at each locality and on an annual basis. CaCO3 biomass contribution (%) was calculated by dividing Cibicides CaCO3 biomass by the total biomass from each species for each locality. Similarly, Cibicides annual CaCO3 biomass contribution (%) was calculated by dividing Cibicides yearly CaCO3 production by Adamussium + Cibicides yearly CaCO3 production. We expected that Cibicides would contribute less to the total host-parasite biomass and yearly carbonate production because of the differences in size between Cibicides and its host.

Ethics Statement

This study was carried out under the auspices of the U.S. Antarctic Program of the National Science Foundation and their research permits.


Living Cibicides

Attached Cibicides are alive, and upon their death they are no longer attached to the shell. Video captured early in deployment showed a sea star feeding on the tethered Adamussium resulting in its death (Fig 3A). Despite the death of its host, Cibicides continued to live on the top valve until it was retrieved from the seafloor a year later. Cibicides cytoplasm was densely stained with Rose Bengal dye indicating that they were alive at the time of collection (Fig 3B, and inset Fig 3). A total of 118 Cibicides in the same position on the shell and an additional eight stained juveniles were present on the retrieved shell. This result indicates that attached Cibicides represent living individuals.

Fig 3. Experiment that Demonstrates Attached Cibicides are Alive.

A. Live Adamussium deployed at EC in 2005 with attached Cibicides. Arms from a sea star can be seen behind the scallop, contributing to the scallop’s death. B. Top valve retrieved after one year and stained with Rose Bengal that stains living tissue pink. Inset: slightly decalcified Cibicides showing Rose Bengal-stained cytoplasm in living individuals. Arrow in A and B point to the three Cibicides that are figured in inset. Scale bar is 20 mm for A and B; inset scale bar is 1 mm.

Cibicides populations by locality, valve type, and depth

Cibicides had relatively high populations at all three localities (Table 1). BOS had the largest attached Cibicides population (39%, n = 1763 individuals) followed by EC (32%, n = 1461) and HG (29%, n = 1306). Cibicides mean densities, however, were higher at HG, averaging 33 cm-2 compared to 30 cm-2 for BOS and 23 cm-2 for EC. Cibicides bioerosion traces were more common at EC (58%, n = 2382) compared to BOS and HG, which had fewer traces (20%, n = 855 and 21%, n = 895, respectively). Mean density for traces was highest at EC (37 cm-2) followed by HG (23 cm-2) and BOS (15 cm-2) (Table 1). EC had a significantly larger total population representing 44% of all individuals (attached Cibicides + traces), while BOS had 30% and HG had 25% of the total population (chi-square = 756.87, df = 2, p < 0.0001). The abundance of attached Cibicides appeared to increase with shell area at all localities, but the trend was not significant because of high population variance among the shells (GLM with quasipoisson, F = 1.32, p = 0.35; Fig 4). Shell area was smaller at HG than the other localities, yet HG had a higher density of Cibicides supporting the GLM result.

Table 1. Cibicides antarcticus Populations by Antarctic Locality, Depth, and Valve Type.

The number of attached Cibicides is reported in the numerator and the number of bioerosion traces is reported in the denominator (attached Cibicides/bioerosion traces). The frequency of occurrence within parentheses depicts the number of either attached Cibicides or bioerosion traces for each locality divided by the total pooled for all localities. The mean shell area for the Antarctic scallop Adamussium colbecki was used to determine the mean density of Cibicides.

Fig 4. Generalized Linear Model of Cibicides Abundance by Shell Area.

Localities: Explorers Cove (EC), Bay of Sails (BOS) and Herbertson Glacier (HG).

Top valves had the largest attached Cibicides populations compared to bottom valves for all three localities (Fig 5A. EC: t = 3.69, df = 9.08, p = 0.004; BOS: t = 2.767, df = 9.09, p = 0.02; HG: t = 6.905, df = 9.07, p < 0.0001). Similarly, traces were more common on top valves (Fig 5B; chi-square χ2 24.956<1). Overall, top valves yielded 91% of living and trace Cibicides populations than bottom valves and this was significant for all localities (Cibicides + traces; Table 1, Fig 5C; EC: t = 7.117, df = 9.59, p < 0.0001; BOS: t = 2.825, df = 9.05, p = 0.02; HG: t = 6.141, df = 9.88, p = 0.0001).

Fig 5. Cibicides Populations on Top and Bottom Valves by Locality.

A. Attached Cibicides. B. Cibicides traces. C. Attached Cibicides with traces pooled. Top = top valves; Bot = bottom valves of Adamussium colbecki.

In general, attached Cibicides and their traces did not vary with depth. Attached Cibicides populations were not significantly different with depth, except at BOS that had a significantly higher population at 18 m than 9 m (Fig 6A; BOS t = -2.226, df = 37.99, p = 0.03). Traces were not significantly different with depth for all localities (Fig 6B). When Cibicides and traces were pooled, there was no difference with depth at EC and HG, except at BOS that had a significantly larger pooled population at 18 m (Fig 6C; BOS: t = -2.699, df = 37.74, p = 0.01).

Fig 6. Cibicides Populations by Depth and Locality.

A. Attached Cibicides. B. Cibicides traces. C. Pooled Cibicides with traces. Localities: Explorers Cove (EC), Bay of Sails (BOS), and Herbertson Glacier (HG). Depths are 9 and 18 m.

Parasite load

Parasite load was relatively low for two of the three localities based on the mean number of Cibicides (Fig 7A). Parasitic Cibicides were significantly less common than non-parasitic Cibicides at EC and HG, but at BOS there was no difference between these groups. In general, the localities were not significantly different from each other for the mean number of parasitic and non-parasitic Cibicides.

Fig 7. Cibicides Parasite Load by Locality, Depth and Valve Type.

For A and B, localities are Explorers Cove (EC), Bay of Sails (BOS), and Herbertson Glacier (HG). A. Mean number of complete boreholes (Bor) compared to Cibicides without boreholes (NoBor), error bars are 95% CIs. B. Frequency of Cibicides boreholes by locality and depth. Frequency was calculated by dividing the number of Cibicides boreholes by the total population of Cibicides. C. Boreholes on top and bottom valves by locality.

The frequency of parasitic Cibicides varied by depth at each locality, ranging from 2 to 50% (Fig 7B). Parasitic Cibicides were significantly more common at 9 m for EC and BOS, but not at HG where significantly more parasites occurred at 18 m (FET: EC, p < 0.0001; BOS p < 0.00001; HG p < 0.00001). Nearly 50% of the Cibicides population at BOS 9 m was parasitic compared to 10% at EC and 2% at HG. The high number of boreholes at BOS 9 m, however, is biased by one shell that had 68 boreholes out of a total of 130 Cibicides. The 18 m depth at BOS and HG had more parasitic Cibicides (16% and 13%, respectively) than EC (10%).

Parasitic Cibicides were more common on top valves than bottom valves at all three localities (Fig 7C). This result was significant for all localities except HG because of the low number of boreholes at that locality (FET: EC, p = 0.002; BOS, p < 0.00001).

Cibicides population structure and spatial distribution

Population structure.

Cibicides bioerosion traces at EC and BOS were categorized into ontogenetic stages that revealed the age structure of the population. The traces ranged from small recruits that first etched the scallop’s shell to larger, parasitic adults that made complete boreholes. Four different ontogenetic stages of Cibicides traces were recognized. Trace 1 (T1) has a relatively smooth resting trace that represents juvenile Cibicides’ early attachment to the shell (Fig 8A). Trace 2 (T1) has a resting trace punctuated by multiple small holes (Fig 8B and 8C). Trace 3 (T3) has a resting trace with one incomplete borehole (Fig 8D). Lastly, Trace 4 (T4) has a resting trace with a complete borehole (Fig 8E). Small accessory holes as depicted in Fig 8C can also be present in T3 and T4.

Fig 8. Four Bioerosion Trace Types Representing Ontogenetic Stages used to Examine Cibicides Population Structure.

Scanning electron micrographs are depicted in A-B, and light photomicrographs are depicted in C-E. A. Attached Cibicides with agglutinated feeding tubes and an initial resting trace (trace type 1) etched by a Cibicides (arrow). B. Attached Cibicides cut in half to reveal the etched upper calcite layer of Adamussium representing trace type 2. C. Trace type 2 with multiple small holes. D. Trace type 3 with an incomplete borehole. E. Trace type 4 with a complete borehole representing parasitic Cibicides.

Young Cibicides were most common at both localities. The early trace types T1 and T2 represent 32% and 54% of the pooled EC + BOS traces, respectively (Table 2). The later ontogenetic stages of T3 and T4 were much less common representing 12% and 2%, respectively, of the pooled trace population. The mean spatial area of the traces increased from T1 (0.58 mm2) to T3 (1.23 mm2). Trace type T4 had a mean spatial area of 1.13 mm2.

Table 2. Cibicides Bioerosion Traces Categorized into Ontogenetic Trace Types.

The trace types were categorized based on trace diameter and the degree of bioerosion. The trace type range from initial recruits that started to etch the shell (T1) to parasitic adults with complete boreholes (T4).

Population structure varied within and between localities (Fig 9). At EC, new recruits (T1) represented 44% of the trace population followed by T2 with 38%, T3 with 15% and T4 with 2%. BOS had fewer new recruits (T1) representing only 23% of the trace population. At BOS, the next ontogenetic stage (T2) represented 66% of the trace population followed by T3 with 10% and T4 with 1%. Most of these trace types were significantly different from each other (S1 Table). The age structure of the population was significantly different between EC and BOS (K-W test: chi-square = 128.42, df = 3, p < 0.0001). This difference results from BOS having significantly more T2 traces than EC (W = 319, p = 0.003, at alpha = 0.0125).

Fig 9. Cibicides Population Structure based on Trace Type for Explorers Cove and Bay of Sails.

Trace type T1-T4 as depicted in Fig 8. EC, Explorers Cove; BOS, Bay of Sails. The sample size for each trace is provided above each bar in this bar plot.

Spatial distribution.

The categorized traces were also used to examine the spatial distribution of Cibicides ontogenetic stages on the top valves of Adamussium. Trace types at EC and BOS were more common in the central region of the scallop than the edges (Fig 10). In general, all trace types had significantly higher mean densities in the center sectors of the shell than the outer sectors (Fig 10; S2 Table). Traces with incomplete boreholes (T3) and complete boreholes (T4) were especially common in the center sectors overlying the muscle, gonads, and other soft tissue (sectors 4, 5). A few of the trace types occurred in some outer sectors and the umbo, but they were not as common as those in the center region of the shell.

Fig 10. Trace Type by Shell Sector for Explorers Cove and Bay of Sails.

The mean number of trace types per shell sector are depicted. The mean was adjusted for sector area. EC, Explorers Cove; BS, Bay of Sails. ** indicates a significantly larger mean population occurs in the sector; * indicates a significantly lower mean population occurs in the sector. Significance is based on 95% CIs generated by one-sample t-tests used for each trace type.

CaCO3 biomass and annual production

Mean CaCO3 biomass for attached Cibicides ranged from < 0.001 mg to 0.690 mg and represented seven size classes (Fig 11A). All biomass classes were significantly different from each other except for the two largest classes (SC 6–7). The mean CaCO3 biomass was 0.226 mg and was used to calculate CaCO3 biomass density and annual CaCO3 production. The frequency distribution for CaCO3 biomass was positively skewed toward younger individuals (Fig 11B).

Fig 11. Size Class and Frequency for Cibicides CaCO3 Biomass.

A. Mean CaCO3 biomass by size class with 95% CIs. Biomass size classes (SC) ranged between 0.00–0.70 mg. B. CaCO3 biomass size class frequency. The sample size for each size class is reported above the bars in the bar plot.

Localities were similar in mean biomass density for both attached Cibicides and Adamussium. Because HG had the highest mean density of Cibicides, it also had the largest CaCO3 biomass density, 73 kg ha-1, followed by BOS with 64 kg ha-1 and EC with 47 kg ha-1, though the differences were not significant (Fig 12A). Adamussium CaCO3 biomass density was > 5000 kg ha-1 for all localities, and the localities were not significantly different from each other (Fig 12B).

Fig 12. CaCO3 Biomass Density for Cibicides and Adamussium by Locality.

The mean CaCO3 biomass density is depicted with 95% CIs. Localities are Explorers Cove (EC), Bay of Sails (BOS) and Herbertson Glacier (HG). A. CaCO3 biomass density for attached Cibicides. B. CaCO3 biomass density for Adamussium.

Adamussium contributed three orders of magnitude more CaCO3 to our Antarctic localities than Cibicides. However, the CaCO3 biomass contributed by Cibicides was not trivial. Cibicides biomass represented 1% of the total CaCO3 produced by both species at EC and BOS and 1.5% at HG (Fig 13A). Cibicides yearly CaCO3 production ranged from 8 to 13% of that generated by the species pair depending on locality (Fig 13B). Annual CaCO3 production by Cibicides varied among the localities from 24 kg ha-1 yr-1 at EC to 37 kg ha-1 yr-1 at HG (Table 3). Adamussium CaCO3 biomass also varied across localities, ranging from 249 kg ha-1 yr-1 at HG to 340 kg ha-1 yr-1 at BOS (Table 3). Together, Adamussium and attached Cibicides contribute from 286 to 372 kg ha-1 yr-1 of CaCO3 to our Antarctic localities (Table 3).

Table 3. Annual CaCO3 Production for Cibicides antarcticus and Adamussium colbecki by Locality.

Cibicides estimates are based on the conservative mean CaCO3 biomass of 0.226 mg.

Fig 13. Cibicides Contribution to Annual CaCO3 Production by Locality.

Cibicides percentage is based on the amount of CaCO3 it produces out of the total Cibicides and Adamussium biomass at each locality. Localities are Explorers Cove (EC), Bay of Sails (BOS) and Herbertson Glacier (HG). A. CaCO3 biomass contributed by attached Cibicides. B. Yearly production of CaCO3 by attached Cibicides.


Living Cibicides

It is essential to distinguish between living and dead populations of Cibicides for population analysis and carbonate estimates. An in situ experiment by SSB showed that attached Cibicides represent living individuals. This finding is in agreement with preliminary observations that > 98% of attached Cibicides on other Adamussium shells were living based on staining with CellTracker Green (SSB personal observation). Therefore, attached Cibicides represent living individuals and their traces represent former populations of Cibicides that are no longer attached to the shell.

Cibicides populations by locality, valve type, and depth

Cibicides populations varied by locality, valve type, and depth. BOS had the largest population of attached Cibicides followed by EC and HG. Densities of attached Cibicides were highest at the two annual sea ice localities BOS and HG. By comparison, the multiannual sea ice locality (EC) had the lowest density of attached Cibicides. Yet, when attached Cibicides were pooled with traces, EC had the largest total population, followed by BOS and HG.

Population differences among the localities could be related to the host’s age: the older the scallop, the longer Cibicides can accumulate on the shell, thereby increasing population size. The size of Adamussium is used as an age equivalent [55, 57]. If we compared our shell sizes to a von Bertalanffy growth equation generated by [56], the approximate age for EC and BOS scallops would be ~15 years and ~12 years for HG. If these age estimates are correct, the total Cibicides population (attached Cibicides + traces) should be similar between EC and BOS with a smaller population at HG. That was not the case: EC had significantly higher total populations than BOS. The results from the GLM also revealed that attached Cibicides populations did not increase with shell area despite HG and BOS having slightly smaller and larger shells, respectively. Other factors must be contributing to Cibicides population dynamics.

Alternatively, a higher total population of Cibicides at EC could be related to sea ice cover. EC was the only locality with persistent sea ice cover, lasting at least a decade prior to our study, whereas sea ice melts out every year at BOS and HG. Sea ice algae are strongly tied to sea ice cover, often reaching concentrations up to hundreds of mg m-3 [30]. Sea ice and its associated microbial communities provide nutrients for Antarctic benthic organisms during austral summer and winter [3031]. As a result, Antarctic benthic communities are strongly affected by sea ice algae distribution, as well as water column and benthic primary productivity [38, 46]. In a study on trophic associations, A. colbecki and the echinoid Sterechinus neumayeri had delta 15N signatures indicative of a diet rich in sea ice algae and benthic detritus at EC. At Terra Nova Bay, where sea ice melts out every year, Adamussium fed on phytoplankton and Sterechinus fed on benthic seaweeds [58]. Additionally, studies in the Bering Sea have shown that a loss of sea ice leads to a decrease in benthic biomass and a shift towards pelagic ecosystems [59]. These results suggest that fluctuations in annual sea ice are related to the strength of trophic interactions. Larger total Cibicides population at EC could be linked to increased nutrients from sea ice algae, enhancing suspension feeding and grazing in this species.

Top valves had the largest Cibicides populations compared to bottom valves. Bottom valves have smaller populations because part of the valve rests on the seafloor, limiting Cibicides settlement. Frequent valve clapping by Adamussium likely increases abrasion on bottom valves reducing foraminifera populations [28, 60]. Moreover, top valves are elevated above the sediment-water interface. Cibicides species tend to live on elevated surfaces where increased water flow enhances suspension feeding [61]. Valve clapping also stirs up fine seafloor sediment that could facilitate suspension feeding in C. antarticus that live on top valves [51].

Cibicides populations were similar at 9 m and 18 m for all localities except BOS, which had significantly higher attached Cibicides populations at 18 m. This difference could result from the patchy nature of foraminiferal distributions on Adamussium valves [26]. It could also result from shallow water disturbance, possibly from anchor ice. Anchor ice occurs to water depths of ~ 33 m in Antarctica, but recent research suggests that anchor ice can occur at much deeper depths [6263]. Anchor ice grows on sediment and benthic organisms [62]. If Adamussium valves were affected by anchor ice at BOS 9 m, we suggest that this could reduce Cibicides populations. Differences in recruitment patterns, predation, or other factors could also account for the reduced populations at BOS 9 m.

Mean densities of C. antarcticus at our Antarctic localities are higher than for other Cibicides species living in Arctic and tropical regions [52, 64]. For example, mean densities of Cibicidoides (Cibicides) lobatulus ranged from 0.33 cm-2 to 2.32 cm-2 on experimental plates deployed off Kosterfjord, southwestern Sweden (converted from m2, Appendix 1 in [52]). In the tropical Caribbean, Cibicides species that encrusted experimental shells after two years on the sea floor had mean densities of ~ 4 cm-2 (15 m depth in [64]). These lower mean densities may be related to increased competition with other encrusting species [65], predation [12], or other factors. For C. antarcticus, its multiple trophic modes could allow it to grow larger and therefore out compete other shell-encrusting foraminifera or invertebrates for resources and space. This species has agglutinated feeding tubes that extend horizontally from its test [13], which could also increase its effectiveness in competing for space.

Parasite load

Parasite populations vary widely across spatial scales in a single host [66]. These differences could be caused by biotic and abiotic environmental conditions [67]. Parasite load in Cibicides also varies widely across our Antarctic localities despite sharing the same host. The overall parasite load varied between 2% and 50% depending on locality and depth at our Antarctic localities. The original work on Cibicides parasitism found that ~ 50% were parasitic at EC [13]. We found that for most localities, parasitism was < 20%.

Abiotic environmental conditions could have changed since the original work on parasitism in Antarctic Cibicides. That study was conducted during a time of more frequent sea ice melt outs that possibly affected foraminiferal populations [26]. If sea ice loss is a factor, then Cibicides may resort to increased parasitism as a trophic mode to supplement its nutrition. At BOS, one of the annual sea ice localities, the parasite load was much higher than EC. Yet at the other sea ice locality HG, the parasite load was similar to EC at 18 m but much lower at 9 m. Rather, it appears that the parasite load is likely related to the population structure of Cibicides and its patchy distribution than sea ice conditions. Adult Cibicides are parasitic and the parasite load is most likely a function of the number of adults in the population.

Differences in methods between the original study on Cibicides parasitism and ours could also account for variation in parasite load. In the original study, they counted the number of etched traces as an indication of parasite load [13], while we counted complete boreholes. Because the number of etched traces are far more common that complete boreholes, they could be overestimating parasitism. They did demonstrate that one etched trace had multiple minute borings that penetrated almost to the shell interior [13]. We could have missed these small pseudopodial borings that do not elicit a host response. By this measure we could be underestimating the parasite load at our localities, suggesting that our estimates are conservative.

Bioerosion is considered a form of parasitism when it contributes to weakening mollusc shells [68]. Boreholes of Cibicides and associated bioerosion traces could negatively affect Adamussium. Considering that Adamussium’s shell is ~ 0.70 mm thick, Cibicides etchings and boreholes could weaken the shell, making it more susceptible to predators. Increased shell permeability also enhances dissolution. Additionally, there is a physiological cost for the scallop because it forms blisters in response to C. antarcticus boreholes, although not all complete boreholes were associated with blisters (SEW personal observation). Shell weakening, increased dissolution and the physiological expense of shell repair could all be added costs of high Cibicides populations on Adamussium.

Parasitism could have arisen accidently in C. antarcticus as a result of the thin shell of Adamussium. Given enough time to bioerode the shell, Cibicides could penetrate to the shell interior. For example, closely related cibicidids living on thicker carbonate substrates, like C. refulgens [69] and the more distantly related C. lobatulus, bioerode but are not parasites [52, 64]. If C. antarcticus lives for two years or longer, its bioerosive activities could completely penetrate the thin shell of Adamussium. The uptake of nutrients and minerals would be beneficial to Cibicides in Antarctic environments where conditions are similar to the deep sea. Further studies are needed to address Cibicides bioerosion rates and whether they use CaCO3 from Adamussium, as well as determine whether Adamussium populations are affected by large populations of Cibicides.

Cibicides population structure and spatial distribution

Population structure.

Bioerosion traces made by C. antarcticus not only provide a record of the parasite load, but also reveal information about its population structure, recruitment patterns, and spatial distributions. Four Cibicides bioerosion traces were documented on Adamussium shells from EC and BOS. These traces represent ontogenetic stages from newly attached individuals that had just started to etch the shell (T1) to parasitic adults with complete boreholes (T4). Overall, early stage traces (T1-T2) were more common than later stage traces (T3-T4) at both localities, indicating that Cibicides populations represent mostly younger individuals. We concur with Alexander and DeLaca’s [13] conclusions that adult C. antarcticus are parasitic, because incomplete and complete boreholes only occurred with larger individuals.

Traces revealed differences in recruitment patterns at the two Antarctic localities. EC had mostly newly attached individuals (T1), while BOS had significantly more of the next stage trace (T2) that had small holes etched into the shell surface. EC also had more adults (T3 and T4) than BOS, but the difference was not significant. The variation in trace population structure suggests differences in Cibicides reproduction and recruitment between EC and BOS. Perhaps sea ice algae and their associated nutrients facilitate higher reproductive rates for Cibicides at EC. Fluxes in sea ice nutrients could also contribute to higher population turnover at EC, which could account for the higher number of traces at this locality. Cibicides also encrusts seafloor glacial erratics at EC and also occurs in sediments although these are likely dead individuals [SSB personal observation]. The population structure of Cibicides on glacial erratics needs to be compared to those on Adamussium valves. If population structure and test size are similar among these different substrates, then parasitism may not be that important for Cibicides.

Spatial distribution.

Parasites have heterogeneous distributions in host populations that can be spatially structured [70]. Spatial distributions of Cibicides on Adamussium valves could reveal preferred settlement sites that maximize food capture. If suspension feeding is important, Cibicides ought to attach where feeding currents are higher presumably near the scallop’s aperture. For example, fossil foraminifera preferentially encrust brachiopod apertures, presumably to take advantage of their feeding currents [71]. However, C. antarcticus is thought to have random distributions on Adamussium valves [51], suggesting that water currents generated by the scallop are not important. We found that Cibicides traces were significantly more common in the center region of Adamussium’s top valves. We also found that center sectors had more parasitic boreholes than the outer sectors. Rarely were complete boreholes found outside of these sectors. More trace populations are likely in the center sectors because they represent some of the oldest regions of the shell, allowing more time for several Cibicides generations to accumulate. Furthermore, these sectors are located over the muscle, gill and gonadal tissue, and perhaps parasitic Cibicides are targeting those tissues.

CaCO3 biomass and annual production

We estimated the mean CaCO3 biomass for C. antarcticus and its host Adamussium for our localities. We first showed that Cibicides had a CaCO3 biomass that ranged from < 0.001 to 0.690 mg, with a mean of 0.226 mg. This mean is an order of magnitude higher than that reported for non-parasitic Cibicidoides lobatulus from polar waters near Kosterfjord, southwestern Sweden (0.0187 mg in [52]). Unfortunately, CaCO3 biomass is not reported for other parasitic foraminifera, so we cannot compare our estimates. At our Antarctic localities, Cibicides CaCO3 biomass varied from 47–73 kg ha-1.

We next demonstrated that Adamussium shells were almost pure carbonate and therefore can be used as a CaCO3 biomass proxy. Mean CaCO3 biomass from Adamussium varied from 4987–6806 kg ha-1 at our localities. The mean CaCO3 biomass per hectare for both Cibicides and Adamussium was not significantly different across our localities.

Cibicides contributes a non-trivial amount of CaCO3 to the host-parasite relationship and represents contributions from younger individuals. Cibicides mean CaCO3 biomass represents 1.0–2.3% of the total CaCO3 biomass produced by Cibicides and Adamussium combined. These estimates are similar to biomass contributions for soft-bodied parasites of metazoans (crabs, polychaetes, bivalves, birds) from subtropical to warm-temperate estuaries [4]. Additionally, Cibicides CaCO3 biomass at EC and BOS represents mostly young individuals. A survivorship curve using biomass revealed that Cibicides has a Type I curve, indicative of low juvenile mortality and increasing mortality with age. Most benthic foraminifera have a Type III curve characterized by high juvenile mortality with few surviving to adulthood [72].

Annual CaCO3 production rates for C. antarcticus are relatively high compared to C. lobatulus from near-Arctic polar regions. Antarctic Cibicides contributes from 24–37 kg ha-1 yr-1 of CaCO3 to our three localities. In near-Arctic polar regions, non-parasitic C. lobatulus contributes 0.00–0.32 g m-2 yr-1 of CaCO3 (3.26 kg ha-1 yr-1 in [52]). This near-Arctic species produces an order of magnitude less than Antarctic Cibicides even though the former has much larger populations.

Cibicides and Adamussium likely contribute considerable CaCO3 to Antarctic communities where they occur. The annual CaCO3 production for Adamussium ranges from 249–340 kg ha-1 yr-1 and with Cibicides, adds 286–372 kg ha-1 yr-1 of CaCO3 to our Antarctic localities. Our estimates are conservative considering that C. antarcticus also lives on other hard substrates and its actual CaCO3 production could be far greater. Both these species are circum-Antarctic in distribution, although we know little about their populations except for a few localities in western McMurdo Sound. Based on our localities, they could potentially add 5.94 x 109 kg ha-1 yr-1 of CaCO3 to the Ross Sea (assuming an areal extent of 1.87 x 107 ha). Future studies need to address their CaCO3 biomass at other localities to bracket their contributions to the carbonate budget of the Ross Sea.

Even though the CaCO3 biomass contribution of Cibicides and Adamussium is considerable, the Ross Sea has very little carbonate in the sedimentary record, a direct result of high primary productivity [73]. Although increased primary productivity contributes to high diversity in this region, carbonate skeletons are rarely preserved in the sediment. High acidic porewaters resulting from benthic respiration induced by primary productivity is inimical to carbonate preservation [37, 73]. Thus, carbonate production by Adamussium, Cibicides, and other carbonate organisms are recycled quickly back into the Ross Sea once they are buried, which could, in part, maintain the supersaturated levels of CaCO3 in this region. This should not preclude work on carbonate producers, as we need to estimate the amount of carbonate produced by the high diversity of Ross Sea organisms to improve carbonate budgets in this region.

Concluding Remarks

The facultative parasite Cibicides antarcticus and its Antarctic scallop host Adamussium colbecki are major components of Antarctic ecosystems, yet we know little about their populations. We found that Cibicides had large populations on Adamussium that varied by locality but not generally with water depth. The largest total Cibicides population, represented by attached individuals and bioerosion traces, occurred at EC. The EC locality has multiannual sea ice, distinguishing it from BOS and HG where sea ice melts out every year. Periodic pulses of sea ice algae could sustain the large populations at EC. Cibicides is a parasite but it also supplements its diet by suspension feeding and grazing on diatoms [13]. Suspension feeding might be more common in younger individuals, because adults are more commonly parasitic. However, even parasitic Cibicides suspension feed and graze on diatoms [13]. Future work using stable nitrogen isotopes could shed light on Cibicides trophic relationships.

Parasites are known to have heterogeneous populations in time and space and Cibicides does not deviate from this pattern. Cibicides parasite load varied by locality, ranging from 2% to 50% of Cibicides populations. Overall, parasitism was rare, occurring in <20% of the population for all localities except for the 9 m site at BOS with the highest parasite load of 50%. Previously, parasitism was thought to occur in ~50% of Cibicides populations at EC [13]. These differences could be related to temporal changes in the environment since that study was conducted. At the time of the original study in the 1980s, sea ice melt out was more common at EC [26]. Since then, sea ice has persisted with occasional partial melt outs. Parasitism in Cibicides could be less common in regions like EC that have persistent sea ice cover and associated sea ice algae. If sea ice begins to completely melt out at EC, it would be important to know if parasitism rates increase to the levels reported in the 1980s.

Cibicides antarcticus etches resting traces on the shell surface of Adamussium [13]. As Cibicides grows, it enlarges the trace and penetrates to the interior tissues of the scallop. As a result, the ontogenetic stages of Cibicides are recorded in these bioerosion traces as well as the development of parasitism. We categorized these ontogenetic stages and used them as a proxy for Cibicides population structure. Based on these traces, populations at EC represent recently attached Cibicides, while those on BOS shells represent slightly older populations. Large Cibicides, presumably adults, always had complete or incomplete boreholes. Therefore, differences in the parasite load among the localities could also be a function of a population structure skewed toward adult Cibicides. We propose that these trace categories can be used to examine the evolutionary history of the host-parasite relationship in recent death or fossil assemblages of Adamussium when Cibicides is no longer attached to the shell.

Cibicides antarcticus and Adamussium colbecki are major components of Antarctic ecosystems. We demonstrated that these species both contribute considerable amounts of CaCO3 to our Antarctic localities, potentially adding 5.94 x 109 kg ha-1 yr-1 of CaCO3 to the Ross Sea. Because of their large CaCO3 contributions, they should be considered in southern polar food webs and ecosystem modeling. If we wish to better understand the global carbon and CaCO3 cycle, we also need to incorporate these species in Antarctic carbonate budgets.

Supporting Information

S1 Fig. Survivorship Curve for Cibicides antarcticus.

The Type I survivorship curve is based on young to adult Cibicides biomass size classes. A Type I curve is characterized by high juvenile survivorship with increasing mortality with age.



S1 Table. Within-Locality Significance Testing for Trace Types T1-T4.

After an initial Kruskal-Wallis test, post hoc Wilcoxon rank sum tests with continuity correction were run to determine within-locality differences in trace type occurrence. Data were subset yielding an alpha = 0.008.



S2 Table. Trace Type 95% Confidence Intervals (CI).

The CIs were used to determine if the mean number of Cibicides were significantly more or less common by shell sector. CIs were calculated using one-sample t-tests and the t-statistic is reported for each test. Trace type refers to Cibicides ontogenetic stages represented by their bioerosion traces. Trace types range from T1 (initial recruits that etch the shell surface) to T4 (parasitic adults that made complete boreholes in Adamussium valves).




We thank the staff at McMurdo Station and the crew of Petroleum Helicopters Inc. for logistical support. The field assistance and dive expertise of Steve Clabuesch, Cecil Shin, Shawn Harper, Henry Kaiser, Doug Coons, and Karen Sterling made this study possible. We are grateful to Jeanine Begg and Krystie Hedley at Antarctic New Zealand for permission to modify a map of Antarctica’s Dry Valleys. We also thank Alan Beu, Geerat Vermeij and an anonymous reviewer for their invaluable editorial suggestions.

Author Contributions

Conceived and designed the experiments: LH SEW. Performed the experiments: LH SEW. Analyzed the data: SEW. Contributed reagents/materials/analysis tools: SEW SSB APH. Wrote the paper: LH SEW APH SSB. Live Cibicides study: SSB. Scanning electron microscopy: APH. Antarctic field logistics: SSB SEW.


  1. 1. Hudson PJ, Dobson AP, Lafferty KD. Is a healthy ecosystem one that is rich in parasites? Trends Ecol Evol. 2006;21: 381–385. pmid:16713014
  2. 2. Poulin R. Evolutionary Ecology of Parasites. 2nd ed. Princeton: Princeton University Press; 2007. pp. 1–360.
  3. 3. Hatcher MJ, Dick JTA, Dunn AM. Diverse effects of parasites in ecosystems: linking interdependent processes. Front Ecol Environ. 2012;10: 186–194.
  4. 4. Kuris AM, Hechinger RF, Shaw JC, Whitney KL, Aguirre-Macedo L, Boch CA, et al. Ecosystem energetic implications of parasite and free-living biomass in three estuaries. Nature. 2008;454: 515–518. doi: 10.1038/nature06970. pmid:18650923
  5. 5. Lafferty KD, Dobson AP and Kuris AM. Parasites dominate food web links. P Natl Acad Sci USA. 2006;103: 11211–11216.
  6. 6. Lafferty KD, Allesina S, Arin M, Briggs DJ, De Leo G, Dobson AP, et al. Parasites in food webs: the ultimate missing links. Ecol Lett. 2008;11: 533–546. doi: 10.1111/j.1461-0248.2008.01174.x. pmid:18462196
  7. 7. Smith WO, Ainley DG, Cattaneo-Vietti R. Trophic interactions within the Ross Sea continental shelf ecosystem. Phil Trans R Soc B. 2007;362: 95–111. pmid:17405209
  8. 8. Sen Gupta BK. Introduction to modern foraminifera. In: Sen Gupta BK, editor. Modern Foraminifera. Dordrecht: Kluwer Academic Publishers; 2009. pp. 3–6.
  9. 9. Suhr SB, Alexander SP, Gooday AJ, Pond DW, Bowser SS. Trophic modes of large Antarctic foraminifera: roles of carnivory, omnivory and detritivory. Mar Ecol Prog Ser. 2008;371: 155–164.
  10. 10. Lipps JH. Biotic interactions in benthic Foraminifera. In: Tevesz MJS, McCall PL, editors. Biotic interactions in recent and fossil benthic communities. New York: Springer; 1983. pp. 331–376.
  11. 11. Mojtahid M, Zubkov MV, Hartmann M, Gooday AJ. Grazing of intertidal benthic foraminifera on bacteria: Assessment using pulse-chase radiotracing. J Exp Mar Biol Ecol. 2011;399: 25–34.
  12. 12. Culver SJ, Lipps JH. Predation on and by Foraminifera. In: Kelley PH, Kowalewski M, Hansen TA, editors. Predator-prey interactions in the fossil record, New York: Kluwer Academic Publishers; 2003. pp. 7–32.
  13. 13. Alexander SP, DeLaca TE. Feeding adaptations of the foraminiferan Cibicides refulgens living epizoically and parasitically on the Antarctic scallop Adamussium colbecki. Biol Bull. 1987;173: 136–159.
  14. 14. Crenshaw MA. The inorganic composition of molluscan extrapallial fluid. Biol Bull. 1972;143: 506–512.
  15. 15. Beuck L, López Correa M, Freiwald A. Biogeographical distribution of Hyrrokkin (Rosalinidae, Foraminifera) and its host-specific morphological and textural trace. In: Wisshak M, Tapanila L, editors. Current developments in bioerosion. Heidelberg: Erlangen Earth Conference Series, Springer; 2008. pp. 329–360.
  16. 16. Stockton WL. The biology and ecology of the epifaunal scallop Adamussium colbecki on the west side of McMurdo Sound, Antarctica. Mar Biol. 1984;78: 171–178.
  17. 17. Chiantore M, Cattaneo-Vietti R, Albertelli G. The population structure and ecology of the Antarctic scallop Adamussium colbecki in Terra Nova Bay. In: Faranda FM, Guglielmo L, Ianora A, editors. Ross sea ecology: Italiantartide expeditions (1987–1995). Berlin: Springer; 2000. pp. 563–573.
  18. 18. Cerrano C, Calcinai B, Bertolino M, Valisano L, Bavestrello G. Epibionts of the scallop Adamussium colbecki (Smith, 1902) in the Ross Sea, Antarctica. Chem Ecol. 2006;22: S235–S244.
  19. 19. Schiaparelli S, Linse L. A reassessment of the distribution of the common Antarctic scallop Adamussium colbecki (Smith, 1902). Deep-Sea Res II. 2006;53: 912–920.
  20. 20. Schweizer M, Bowser SS, Korsun S, Pawlowski J. Emendation of Cibicides antarcticus (Saidova, 1975) based on molecular, morphological, and ecological data. J Foramin Res. 2012;42: 340–344.
  21. 21. DeLaca TE. Trophic position of benthic rhizopods in McMurdo Sound, Antarctica. Antarct J US. 1985;20: 147–149.
  22. 22. Pawlowski J, Fahrni J, Brykczynska U, Habura A, Bowser SS. Molecular data reveal high taxonomic diversity of allogromid foraminifera in Explorers Cove (McMurdo Sound, Antarctica). Polar Biol. 2002;25: 96–105.
  23. 23. Bernhard JM. Foraminferal biotopes in Explorers Cove, McMurdo Sound, Antarctica. J Foramin Res. 1987;17: 286–297.
  24. 24. Bernhard JM. The distribution of benthic foraminifera with respect to oxygen concentration and organic carbon levels in shallow-water Antarctic sediments. Limnol Oceanogr. 1989;34: 1131–1141.
  25. 25. Gooday AJ, Bowser SS, Bernhard JM. Benthic foraminiferal assemblages in Explorers Cove, Antarctica: A shallow-water site with deep-sea characteristics. Prog Oceanog. 1996;37: 117–166.
  26. 26. Radford DR, Walker SE, Bowser SS. Alpha and beta diversity of foraminifera that encrust the Antarctic scallop Adamussium colbecki: Ecological connectivity among shells and between sites. J Foramin Res. 2014;44: 255–280.
  27. 27. Fountain AG, Nylen TH, MacClune KL, Dana GL. Glacier mass balances (1993–2001), Taylor Valley, McMurdo Dry Valleys, Antarctica. J Glaciol. 2006;52: 451–462.
  28. 28. Lizotte MP. The contributions of sea ice algae to Antarctic marine primary productivity. Amer Zool. 2001;41: 57–73.
  29. 29. Arrigo KR. Sea ice ecosystems. Ann Rev Mar Sci. 2014;6: 439–467. doi: 10.1146/annurev-marine-010213-135103. pmid:24015900
  30. 30. Gaździcki A, Webb P-N. Foraminifera from the Pecten Conglomerate (Pliocene) of Cockburn Island, Antarctic Peninsula. Palaeontol Pol. 1996;55: 147–174.
  31. 31. Quaglio F, Whittle RJ, Gaździcki A, Simoes MG. A new fossil Adamussium (Bivalvia: Pectinidae) from Antarctica. Pol Polar Res. 2010;31: 291–302.
  32. 32. Gooday AJ, Leven LA, Linke P, Heeger T. The role of benthic foraminifera in deep-sea food webs and carbon cycling. In: Rowe GT, Pariente V, editors. Deep-sea food chains and the global carbon cycle, NATO ASI Ser. C, 360. Dordrecht: Kluwer Academic Publishers; 1992. pp. 63–91.
  33. 33. Langer MR, Silk MT, and Lipps JH. Global ocean carbonate and carbon dioxide production: the role of reef Foraminifera. J Foramin Res. 1997;27: 271–277.
  34. 34. Langer MR. Assessing the contribution of foraminiferan protists to global ocean carbonate production. J Eukaryot Microbiol. 2008;55: 163–169. doi: 10.1111/j.1550-7408.2008.00321.x. pmid:18460153
  35. 35. Milliman JD. Production and accumulation of calcium carbonate in the ocean: Budget at non-steady state. Global Biogeochem Cy. 1993;7: 927–957.
  36. 36. Milliman JD, Droxler AW. Calcium carbonate sediment in the global ocean: Linkages between the neritic and pelagic environments. Oceanography. 1995;8: 92–94.
  37. 37. Hauck J, Gerdes D, Hillenbrand C-D, Hoppema M, Kuhn G, Nehrke G, et al. Distribution and mineralogy of carbonate sediments in Antarctic shelves. J Marine Syst. 2012;90: 77–87.
  38. 38. Dayton PK, Oliver JS. Antarctic soft-bottom benthos in oligotrophic and eutrophic environments. Science. 1977;197: 55–58. pmid:17828892
  39. 39. Dayton PK, Kim S, Jarrell SC, Oliver JS, Hammerstrom K, Fisher JL, et al. Recruitment, growth and mortality of an Antarctic hexactinellid sponge, Anoxycalyx joubini. PLoS ONE. 2013;8(2): e56939. doi: 10.1371/journal.pone.0056939. pmid:23460822
  40. 40. DeLaca TE, Karl DM, Lipps JH. Direct use of dissolved organic carbon by agglutinated benthic foraminifera. Nature. 1981;289: 287–289.
  41. 41. Dayton PK, Watson D, Palmisano A, Barry JP, Oliver JS, Rivera D. Distribution patterns of benthic microalgal standing stock at McMurdo Sound, Antarctica. Polar Biol. 1986;6: 207–213.
  42. 42. Leventer A, Dunbar RB. Diatom flux in McMurdo Sound, Antarctica. Mar Micropaleontol. 1987;12: 49–64.
  43. 43. Dunbar RB, Leventer AR, Stockton WL. Biogenic sedimentation in McMurdo Sound, Antarctica. Mar Geol. 1989;85: 155–179.
  44. 44. Dayton PK. Polar biology. In: Polar oceanography, Part B: Chemistry, biology, and geology. Smith WO, editor. New York: Academic Press Inc.; 1990. pp. 631–685.
  45. 45. Bowser SS, Bernhard JM. Structure, bioadhesive distribution and elastic properties of the agglutinated test of Astrammina rara (Protozoa: Foraminiferida). J Eukaryot Microbiol. 1993;40: 121–131.
  46. 46. Barry JP, Dayton PK. Current patterns in McMurdo Sound, Antarctica and their relationship to biological production of local biotic communities. Polar Biol. 1988;8: 367–376.
  47. 47. Thrush SF, Hewitt JE, Cummings VJ, Norkko A, Chiantore M. Beta-diversity and species accumulation in Antarctic coastal benthos: Influence of habitat, distance and productivity on ecological connectivity. PLoS ONE. 2010;5(7): e11899. doi: 10.1371/journal.pone.0011899. pmid:20689578
  48. 48. Crawley MJ. Statistics: an introduction using R. Chichester: John Wiley and Sons Ltd; 2005. pp. 1–327.
  49. 49. R Core Team. R: A language and environment for statistical computing. Vienna, Austria: R Foundation for Statistical Computing; 2012.
  50. 50. Freiwald A, Schönfeld J. Substrate pitting and boring pattern of Hyrrokkin sarcophaga Cedhagen 1994 (Foraminifera) in a modern deep-water coral reef mound. Mar Micropaleontol. 1996;28: 199–207.
  51. 51. Mullineaux LS, DeLaca TE. Distribution of Antarctic benthic foraminifers settling on the pectin Adamussium colbecki. Polar Biol. 1984;3: 185–189.
  52. 52. Wisshak M, Rüggeberg M. Colonisation and bioerosion of experimental substrates by benthic foraminifera from euphotic to aphotic depths (Kosterfjord, SW Sweden). Facies. 2006;52: 1–17.
  53. 53. Dean WE. Determination of carbonate and organic matter in calcareous sediments and sedimentary rocks by loss on ignition: Comparison with other methods. J Sediment Petrol. 1974;44: 242–248.
  54. 54. Berkman PA. The population biology of the Antarctic scallop, Adamussium colbecki (Smith, 1902), at New Harbor, Ross Sea. In: Kerry KR, Hempel G, editors. Antarctic ecosystems. Ecological change and conservation. Berlin: Springer; 1990. pp. 281–288.
  55. 55. Chiantore M, Cattaneo-Vietti R, Heilmayer O. Antarctic scallop (Adamussium colbecki) annual growth rate at Terra Nova Bay. Polar Biol. 2003;26: 416–419.
  56. 56. Heilmayer O, Brey T, Chiantore M, Cattaneo-Vietti R, Arntz WE. Age and productivity of the Antarctic scallop, Adamussium colbecki, in Terra Nova Bay (Ross Sea, Antarctica). J Exp Mar Biol Ecol. 2003;288: 239–256.
  57. 57. Lartaud F, Chauvaud L, Richard J, Toulot A, Bollinger C, Testut L, et al. Experimental growth pattern calibration of Antarctic scallop shells (Adamussium colbecki, Smith 1902) to provide a biogenic archive of high-resolution records of environmental and climatic changes. J Exp Mar Biol Ecol. 2010;393: 158–167.
  58. 58. Norkko A, Thrush SF, Cummings VJ, Gibbs MM, Andrew NL, Norkko J, Schwarz A-M. Trophic structure of coastal Antarctic food webs associated with changes in sea ice and food supply. Ecology. 2007;88: 2810–2820. pmid:18051650
  59. 59. Hunt GL, Stabeno P, Walters G, Sinclair E, Brodeur RD, Napp JM, et al. Climate change and control of the southeastern Bering Sea pelagic ecosystem. Deep-Sea Res. 2002;49: 5821–5853.
  60. 60. McClintock JB, Tackett LB, Bowser SS. Video observations on non-swimming valve-claps in the Antarctic scallop Adamussium colbecki. Antarct J US. 2010;22: 173–174.
  61. 61. Schönfeld J. A new benthic foraminiferal proxy for near-bottom current velocities in the Gulf of Cadiz, northeastern Atlantic Ocean. Deep-Sea Res I. 2002;49: 1853–1875.
  62. 62. Dayton PK, Robilliard GA, Devries AL. Anchor ice formation in McMurdo Sound, Antarctica, and its biological effects. Science. 1969;163: 273–274. pmid:17790253
  63. 63. Mager SM, Smith IJ, Kempema EW, Thompson BJ, Leonard GH. Anchor ice in polar oceans. Proc Phys Geogr. 2013;37: 468–483.
  64. 64. Walker SE, Parsons-Hubbard K, Richardson-White S, Brett C, Powell E. Alpha and beta diversity of encrusting foraminifera that recruit to long-term experiments along a carbonate platform-to-slope gradient: Paleoecological and paleoenvironmental implications. Palaeogeogr Palaeoclimatol Palaeoecol. 2011;312: 325–349.
  65. 65. Richardson-White S, Walker SE. Diversity, taphonomy and behavior of encrusting foraminifera on experimental shells deployed along a shelf-to-slope bathymetric gradient, Lee Stocking Island, Bahamas. Palaeogeogr Palaeoclimatol Palaeoecol. 2011;312: 305–324.
  66. 66. Wolinska J, Seda J, Koerner H, Smilauer P, Petrusek A. Spatial variation of Daphnia parasite load within individual water bodies. J Plank Res. 2011;33: 1284–1294.
  67. 67. Ebert D, Hottinger JW, Pajunen VI. Temporal and spatial dynamics of parasite richness in a Daphnia metapopulation. Ecology. 2001;82: 3417–3434.
  68. 68. Huntley J. Towards establishing a modern baseline for paleopathology: Trace-producing parasites on a bivalve host. J Shell Res. 2007; 26: 253–259.
  69. 69. Schweizer M, Pawlowski J, Kouwenhoven T, van der Zwaan B. Molecular phylogeny of common cibicidids and related rotaliida (foraminifera) based on small subunit rDNA sequences. J Foramin Res. 2009;39: 300–315.
  70. 70. Pullan RL, Sturrock HJW, Soares Magalhäes RJS, Clements ACA, Brooker SJ. Spatial parasite ecology and epidemiology: a review of methods and applications. Parasitology. 2012;139: 1870–1887. doi: 10.1017/S0031182012000698. pmid:23036435
  71. 71. Zumwalt GS, DeLaca TE. Utilization of brachiopod feeding currents by epizoic foraminifera. J Paleontol. 1980;54: 477–484.
  72. 72. Murray JW. Ecology and applications of benthic foraminifera. 1st ed. Cambridge: Cambridge University Press; 2006. pp. 1–426.
  73. 73. Anderson JB. Factors controlling CaCO3 dissolution in the Weddell Sea from foraminiferal distribution patterns. Mar Geol. 1975;19: 315–332.