Impact of an alien octocoral, Carijoa riisei, on black corals in Hawaii
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In 2001 Carijoa riisei, an octocoral native to the tropical Western Atlantic, was discovered overgrowing black corals in the Au’au Channel in Hawaii. In this paper data from a 2001 survey are reanalyzed and combined with new data from 2003 and 2004 to assess the ecological impact in greater detail. C. riisei differentially affected reproductively mature black coral colonies with maximum impact between 80 and 105 m. The pattern of C. riisei overgrowth on black corals and C. riisei on the substrata appears to be bounded by high irradiance in shallow water and cold temperature in deep water. Evidence suggests that the C. riisei settlement on black corals is facilitated by other epifauna. Once established, C. riisei spreads vegetatively and smothers the coral. The success of the C. riisei invasion appears to be unaided by anthropogenic disturbance and is at least partially attributable to Hawaii’s depauperate shallow-water (<100 m) octocoral fauna.
KeywordsIntroduced species Octocoral ecology Black coral Carijoa riisei Antipathes dichotoma Antipathes grandis
Carijoa riisei (Duchassaing and Michelotti 1860) is a shallow-water octocoral (Order Alcyonacea, Family Clavulariidae) that is native to the tropical Western Atlantic where it commonly occurs from Florida to Brazil and throughout the Caribbean (Bayer 1961). C. riisei was first found in Hawaii in 1972 in the fouling community in Pearl Harbor (Evans et al. 1974). 1 Since its initial discovery C. riisei has spread throughout the main Hawaiian Islands (Devaney and Eldredge 1977; Thomas 1979; Coles and Eldredge 2002).
Hawaiian black corals Antipathes dichotoma and Antipathes grandis are commercially valuable species used for the manufacture of precious coral jewelry (Grigg 1976). Since 1958, there has been an active fishery that has been successfully managed (Grigg 2001). Black coral is the official gemstone for the state of Hawaii and supports a $30 million statewide precious coral industry (Grigg 2004). Both species occur at depths between 30 and 120 m in Hawaii (Grigg 1976). A. dichotoma grows vertically at a rate of about 6 cm per year and takes approximately 12 years to reach sexual maturity (Grigg 1976).
The history of introduced marine species in Hawaii dates back to 1866 when an attempt to culture eastern oysters Crassostrea virginica was made in Pearl Harbor (Coles et al. 1999). From that time maritime vectors, the aquaculture industry, and the aquarium trade have been implicated in the introduction (both intentional and unintentional) of over 343 nonindigenous marine species in Hawaii (Coles et al. 1999; Eldredge and Carlton 2002). Of these, 287 species are nonindigenous marine invertebrates with most occurring within the major harbors and a few proliferating on adjacent coral reefs (Eldredge and Carlton 2002). C. riisei is the only confirmed nonindigenous coral established in Hawaii (Coles, personal communication).
The accidental introduction of C. riisei in Hawaii represents a significant ecological event since only a few shallow-water (<100 m) octocoral species are native to Hawaii: Sarcothelia edmonsoni (Family Xeniidae), Sinularia densa and S. molokaiensis (Family Alcyoniide); and Acabaria bicolor (Family Melithaeidae) (Grigg and Bayer 1976; Devaney and Eldredge 1977; Hoover 1998; Fenner 2005). S. edmonsoni is zooxanthellate, widely distributed in shallow water (Davis 1977; Devaney and Eldredge 1977). Sinularia densa and S. molokaiensis are also zooxanthellate but less common (Fabricius and Alderslade 2001; Fenner 2005). A. bicolor is azooxanthellate, occurs to depths greater than 400 m (Devaney and Eldredge 1977; Hoover 1998), and may have originated as a deep water species (Grigg and Bayer 1976).
In terms of biodiversity, the number of shallow-water (<100 m) octocoral species in Hawaii is anomalously low compared to the Scleractinian coral species. Hawaii has roughly 10% the number of shallow-water Scleractinian species occurring in the central Indo-Pacific (Veron 1995). In comparison, Hawaii has approximately 0.5% the number of shallow-water octocoral species occurring in the central Indo-Pacific (Spalding et al. 2001). In many coral reef ecosystems, particularly in the Caribbean Sea and the Indo-West Pacific, octocorals form a major and sometimes dominant faunistic component (Bayer 1961; Dinesen 1983; Spalding et al. 2001).
C. riisei is commonly observed on hard substrata in shaded habitat with moderate current flow. In the clear oceanic water surrounding Hawaii, C. riisei is restricted to shaded habitat at depths shallower than 40 m (personal observations). In the Au’au Channel, C. riisei was first reported in shallow water by sport divers in the early 1990s. Observations in the Au’au Channel in 2001 suggest that C. riisei may be causing large-scale mortality of black corals in the depth range of 75–110 m (Grigg 2003, 2004). No large-scale mortality of black coral colonies has been observed previously from any causal factor other than harvesting through 40 years of continuous black coral research and commercial fishing activity (Grigg 2001).
The purpose of this study is to quantify the present ecological impact of C. riisei on black corals and identify patterns of distribution and abundance. This analysis is one component of an ongoing study of the biology and ecology of C. riisei in Hawaii. In 2001, video data of the Au’au Channel as reported in Grigg (2004) were collected to quantify the ecological impact of C. riisei and its depth distribution relative to black corals. In 2003 and 2004, submersible dives and remotely operated vehicle (ROV) deployments covering part of the same area as the 2001 survey were conducted to determine if C. riisei was smothering and killing black coral colonies and whether its impact was increasing over time. Previously unexplored areas of the Au’au Channel were also surveyed to assess the geographic spread of C. riisei at depth. For the present study a subset of the previously reported 2001 video data, previously unreported 2001 video data, and new video data from 2003 and 2004 were analyzed in greater detail.
Materials and methods
Pisces V submersible dives and ROV deployments in the Au’au Channel between the islands of Maui and Lanai (Fig. 1) were conducted during scientific cruises in November 2001, December 2003, and September 2004. During each of these cruises, video transects were conducted in the same black coral bed in the north-central region of the Au’au Channel (the Keyhole Pinnacle area) to enable a time series comparison: three 2001 ROV transects (RCV-122, 123, and 124) consisting of 5.5 h of digital video covering approximately 5.8 km; one 2003 submersible dive (PV-553) with 6.8 h of digital video covering approximately 1.5 km; and one 2004 submersible dive (PV-568) with 7.5 h of digital video covering approximately 5.2 km. In 2004, an additional two submersible dives (PV-569 and 570) and three ROV deployments (RCV-283, 284, and 285) were conducted in other black coral beds in the Au’au Channel with a combined 10.5 h of digital video covering approximately 9.8 km.
In order to determine the C. riisei distribution pattern, water depth, colony height, and level of C. riisei overgrowth were recorded for each black coral colony observed. On the ROV and the submersible digital video, continuous depth data from a Seabird Electronics CTD profiler was used to record depth for each black coral colony. Temperature-depth profiles were also recorded. Due to mechanical difficulties, CTD data was not available for the 2003 submersible video.
In all the surveys the height of each black coral colony was estimated with the aid of parallel laser pointers set 15 cm apart. Colonies were classified as either: small <40 cm; medium 40–75 cm; or large >75 cm. The small size class (<40 cm) corresponds to juvenile colonies that recruited to the population after the arrival of C. riisei to the Au’au Channel in the early 1990s. The medium size class (40–75 cm) corresponds to juvenile colonies that are on average less than 12 years old and are reproductively immature (Grigg 1976). The large size class corresponds to the reproductively mature segment of the population. The large colonies likely recruited to the population prior to the arrival of C. riisei in the Au’au Channel.
For each black coral colony observed, the level of C. riisei overgrowth (none/partial/total) and its state (alive/dead) was recorded. Further distinction was made if the black coral colony appeared to be recently dead. Recently dead black coral colonies retain their fine branches that erode with time eventually leaving only thick branches.
The 2001 and 2004 data were used to calculate the percentage of black coral colonies with C. riisei overgrowth at 5 m depth interval. The total number of black coral colonies within each 5 m depth interval was also tabulated. The lack of high-resolution depth data prevented a similar analysis with the 2003 video data.
Within each size class, the percentage of black coral colonies with and without C. riisei overgrowth was calculated. Chi-square tests were performed on the association of C. riisei overgrowth incidence with 5 m depth interval and with black coral size class. Within the Keyhole Pinnacle area, the 2001–2004 results were compared to identify possible trends with time.
During the 2003 and 2004 submersible dives, digital photos and video of black coral colony cohorts at all stages of C. riisei overgrowth were taken using a zoom lens. Samples of black coral with C. riisei overgrowth were taken using the submersible’s mechanical arm for laboratory examination. Cases of C. riisei growth on open substrata and other benthic fauna were investigated qualitatively using the zoom lens in the digital video camera.
Relative to the medium and large size classes, the small size class was probably underrepresented due to the visual limits in seeing the small colonies. Therefore, this frequency data may not reflect an accurate age/size class distribution for the small size class. The higher counts of black coral colonies observed via the submersible dives versus the ROV transects were due in part to the superior video survey capabilities associated with the submersible.
Live black coral colonies were observed in all stages of C. riisei overgrowth from initial colonization covering less than 5% of surface area to >95% coverage (Fig. 2). C. riisei had overgrown on all recently dead black coral colonies. However, dead black coral colonies with heavily eroded skeletons were regularly observed to be free of C. riisei overgrowth. Black corals free of C. riisei overgrowth (both alive and dead) were often observed in close proximity to C. riisei on the substrata and on neighboring black corals.
In several instances an early stage of C. riisei overgrowth was associated with other epifauna on the black coral colony. Early C. riisei colonization was repeatedly observed on the shells of hammerhead oysters Pterous sp. and on bare skeletal portions of black coral colonies next to encrusting sponges. Laboratory examination of samples revealed that C. riisei readily attached to exposed black coral skeleton adjacent to live black coral tissue using an extensive network of overlapping stolons. Small black coral colonies were generally free of epifauna in contrast to most large otherwise healthy black coral colonies.
C. riisei was also observed colonizing open substrata. Colonization was observed on rugose features (i.e., large rocks, ledges, and corners) and areas immediately below overgrown black coral colonies. In 2003 and 2004, C. riisei was also observed colonizing large areas of more level, and gently sloping substrata at depths of 60–70 m, overgrowing large beds of scleractinian plate corals Leptoseris sp. and Pavona sp., and creating an underwater “prairie” of white polyps (Fig. 2). Close examination revealed that C. riisei was settling on the undersides of live plate corals with the axial polyp extending upward into the water column. Review of the 2001 video data reveals that while C. riisei was present in the plate coral beds, it was somewhat rare and inconspicuous. With the exception of the large size class (>75 cm), a yearly comparison of the percentage of black coral colonies with C. riisei overgrowth within the Keyhole Pinnacle area did not show an increasing trend with time (Fig. 4). In terms of geographic distribution, the 2004 survey confirmed C. riisei overgrowth on black coral colonies at all locations investigated in the Au’au Channel.
The reduced frequency of C. riisei overgrowth shallower than 70 m is consistent with C. riisei’s avoidance of light in shallow water. Shallow-water C. riisei colonies transplanted into exposed sunlight (∼25 m) exhibit tissue necrosis and subsequent death while control colonies transplanted within the shade do not (Kahng, unpublished data). The highest incidence of C. riisei overgrowth on black corals was observed between 80 and 105 m where photosynthetically active radiation (PAR) attenuates to less than 10% of surface values (Kirk 1994). Whether the apparent release with depth is due to direct effects of light irradiance or some other effect requires further investigation, but based on the present evidence, it appears that C. riisei is limited by the direct effects of irradiance.
Analysis by black coral age/size class shows an increasing incidence of C. riisei overgrowth with larger classes suggesting that size and exposure through time increase the cumulative probability of C. riisei settlement and overgrowth. C. riisei appears to settle on black coral colonies opportunistically. Patches of bare skeleton on black corals can be created by abrasion or localized senescence. The pattern of juvenile C. riisei colonies on hammerhead oyster shells attached to black coral colonies and on bare black coral skeletal surfaces created by receding sponge colonies suggests that certain epifauna facilitate C. riisei settlement onto black corals.
Once established on a black coral colony, C. riisei can quickly spread vegetatively and appears to adversely affect the host colony by smothering. The growth rate of C. riisei axial polyp extension of 0.5–2.0 cm per week (Rees 1969; Thomas 1979) is many times greater than that of black coral. Gut content analyses indicate C. riisei feed on zooplankton in the 200–1,200 μm range (Kahng, unpublished data) which overlaps with the size class of black coral prey (Grigg 1964) and suggests the potential for competition for food.
Black coral colonies may also be susceptible to abrasion by C. riisei axial polyps creating additional bare skeletal surfaces for C. riisei colonization. The external surface of C. riisei colonies is covered by tough interlocking calcite spicules. In contrast, the living tissue of a black coral colony forms a fragile, gelatinous layer over a hard internal skeleton. Black coral colony polyps cannot retract and are always susceptible to damage.
The observations of live black coral colonies at all stages of C. riisei overgrowth were consistent with the C. riisei smothering hypothesis. No recently dead black coral colonies were observed to be free of C. riisei or at intermediate stages of overgrowth as would be expected if another factor was causing the large-scale mortality. Given C. riisei’s network of stolonal attachment on black coral colonies, wholesale detachment following colonization appears unlikely. However, C. riisei settlement onto new black coral substrata may be a somewhat limited opportunity. Both live black coral colonies and dead, eroded black coral skeletons were often observed to be completely free of C. riisei in close proximity to overgrown colonies.The resident epifauna on the eroded black coral skeletons may be inhibiting the C.riisei settlement.
The C. riisei invasion may significantly alter the population dynamics of black corals, especially if C. riisei continues to spread. Currently, Hawaiian black corals are harvested at depths shallower than 75 m (Grigg 2001). The zone of C. riisei overgrowth lies largely below current harvesting depths. However, this deeper population has been traditionally regarded as a reserve of large, highly fecund black coral colonies (Grigg 2001). With the C. riisei invasion of the Au’au Channel, black corals there now incur mortality from both invasion and harvesting.
In 2004, the preponderance of juvenile C. riisei colonies and the patchiness in many areas suggest that C. riisei’s biological invasion in the Au’au Channel has not yet peaked. Under favorable conditions in shallow water, C. riisei is regularly observed saturating the substrata and attaining densities of over 1,600 axial polyps per square meter (Kahng, unpublished data). The video record reveals C. riisei’s potential for deep water proliferation on flat, gently sloping, hard substrata deeper than 60 m (Fig. 2). At these depths, the overgrowth of large beds of scleractinian plate corals is similar to the behavior observed in the shaded habitat in shallow water (<40 m) where C. riisei has been observed settling and growing on inert parts of live benthic organisms such as bivalves and the undersides of scleractinian corals Porites lobata and Montipora capitata (Kahng, personal observation). While a comparison of the 2001–2004 results fails to detect a consistent trend of changing impact with time, natural variability, limited spatial coverage of the surveys, and small-scale differences in survey locations may mask any underlying change over this period.
The C. riisei biological invasion of Hawaii’s coral reef community is a unique and significant event that warrants continued ecological research. Given the location of the benthic habitat in the Au’au Channel, the success of the C. riisei invasion appears to be independent of habitat alteration and anthropogenic disturbance—features that differentiates this biological invasion from many others (Orians 1986; Lodge 1993; Carlton 1996). In terms of introduced biomass and displacement of native species, C. riisei may be the most invasive of the nonindigenous marine invertebrate in Hawaii. The low diversity and abundance of shallow-water octocorals may contribute to the susceptibility of Hawaii’s coral reef community to C. riisei. Unfortunately, this susceptibility may apply to other nonindigenous octocoral species should they be introduced to Hawaii.
Formerly known as Telesto riisei
We gratefully acknowledge the support of this research by grants from the University of Hawaii Undersea Research Laboratory (HURL) and the National Oceanic and Atmospheric Administration, Project# R/CR-8, sponsored by the University of Hawaii Sea Grant College Program, SOEST, under Institutional Grant No. NA16RG2254. The captain and crew of the R/V Kaimikai-o-Kanaloa provided surface support for all of the Pisces V submersible dives and RCV ROV deployments. Terry Kirby, Max Cremer, and Chuck Holloway, pilots of the Pisces V provided superb skill in operating the submersible.
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