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1 April 2009 Losing the Bounty? Investigating Species Richness in Isolated Freshwater Ecosystems of Oceania
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Abstract

The South Pacific freshwater ecosystems have never been investigated systematically. Although their ecological value has long been recognized and recommended for protection, little action has been taken so far. Here, we present results of 39 lentic water bodies on 18 islands belonging to seven countries. Temperature, conductivity, and pH were measured and samples of aquatic organisms were collected. Freshwater algae, nematodes, rotifers, ostracods, copepods, cladocerans, and aquatic oribatid mites were identified to genus or species level. Sixty-six percent of all taxa recorded have a cosmopolitan distribution, 14% are circumtropical/tropicopolitan species, and for 20% a restricted distribution predominantly in Australasia has previously been reported. Eleven new copepod and three new ostracod taxa were discovered. Out of 39 water bodies we found at least 17 stocked with nonindigenous fish species. Salinization and uncontrolled introduction of alien fish species may lead to reduced species richness in these remote freshwater ecosystems. The highest species richness was recorded in old, shallow, fish-free softwater lakes at high altitude.

THE SOUTH PACIFIC islands harbor some of the most isolated freshwater lakes of the world. Most of them fill volcanic craters that formed thousands of kilometers away from the next continent. These small islands of freshwater habitat surrounded by a vast saline water mass are ideal targets for ecological and biogeographic research. Although their ecological value has long been recognized (Dahl 1980), up to now only one lake is protected as a national park (Lake Lanoto'o, Samoa); however, even this lake remains so ill-explored that its depth was unknown before our visit.

A limited number of freshwater plankton and benthos organisms colonized these lakes through long-distance dispersal probably via resistant propagules carried by wind, rain, animal vectors, or humans (for recent reviews see Bilton et al. 2001, Bohonak and Jenkins 2003. Havel and Shurin 2004, Panov et al. 2004. Green and Figuerola 2005, Vanschoenwinkel et al. 2008). The relative importance of the different vectors is still unknown, and as Bohonak and Jenkins (2003:785) stated, “Despite its noble pedigree, our knowledge base regarding passive dispersal in freshwater invertebrates has progressed little since Darwin's time.”

In higher plants and animals the low number of colonizers radiated into extensive insular species complexes. Today the Pacific islands present one of the highest levels of endemism in the world. With decreasing distance to the Asian and Australian continent, the total number of animal and plant species found on each island increases, and the number of endemic species decreases (Loope 1998).

Whether the same evolutionary forces are shaping freshwater protist, algal, and micrometazoan communities is a matter of debate. Fenchel and Finlay (2004) argued that dispersal is rarely (if ever) restricted by geographical barriers and that propagules (diapausing resting eggs or cysts) up to 1 mm might disperse globally. To the contrary, Foissner (2004) and Kristiansen (2005) argued that there is indisputable evidence of endemism and restricted geographical distribution in at least some protist species. Similar opposing views exist for several groups of freshwater microalgae (mainly diatoms, blue-green algae/cyanobacteria, and desmids [Kristiansen 1996]) and micrometazoa (Frey 1982, Dumont 1983, Dumont and Segers 1996, Reid 1997).

Theory predicts that we should find higher species richness in old, deep, productive lakes on large islands closer to a continental land mass (Green 1992). According to the equilibrium model of McArthur and Wilson (1967) immigration rates were most likely positively related to dispersal vectors such as wind or birds as well as target island/lake size and negatively related to “source to target” distance (see also Whittaker 1998). Current-day community composition in isolated South Pacific freshwater bears the imprint of local processes (e.g., habitat suitability, competition, predation, disturbance) that limit the diversity in individual communities, whereas regional processes (e.g., immigration, speciation) should enrich local communities (He et al. 2005, Hessen et al. 2006).

Detailed surveys of algae and micrometazoa are available for the Hawaiian Archipelago (e.g., Jersabek 2003, Sherwood 2004), but comparatively little limnological research has been conducted on South Pacific islands, due to the remoteness and low accessibility of many freshwater ecosystems. Descriptive studies on lake morphology and physicochemical variables together with short paragraphs on flora and fauna are available only for Tagimaucia crater lake on Taveuni Island, Fiji (Southern et al. 1986), and the Vai Lahi crater lake on Niuafo'ou Island, Tonga (Maciolek and Yamada 1981). Species lists of nematodes, rotifers, and microcrustaceans are available for Easter Island (Segers and Dumont 1993, Dumont and Martens 1996) and the Galápagos Islands (DeSmet 1989a,b, Segers 1990, Eyualem and Coomans 1995); older data refer to Melanesia and Micronesia (Lindberg 1954). Meisch et al. (2007) presented a list of ostracods described from Oceania. Chappuis (1955), Yeatman (1983), and Dussart (1984) reported harpacticoids from Fiji, Western Samoa, Tonga, and New Caledonia. Taxonomic descriptions of New Caledonian copepods were provided by Dussart (1984, 1986) and Defaye (2001) and for cladocerans by Timms (1985). Korovchinsky (2001) reviewed the cladoceran family Sididae and described the new species Diaphanosoma samoaensis from Lake Lanoto'o on Samoa. Older records of different crustacean species are available from Sars (1904), Stingelin (1905), Jenkin (1929), and Lowndes (1928, 1931).

The species richness in these lakes may be reduced by a number of different threats. Alien fish species have been introduced into the majority of suitable freshwater habitats and may alter plankton and benthos communities (Schindler and Parker 2002). In addition, societal demands have contributed to environmental degradation (i.e., forest clearance and logging [also by pre-European settlers, as described by Rolett and Diamond 2004], commercial development and urban sprawl [Schuster et al. 1996]). Finally, the Pacific island nations will be among the first to experience adverse impacts of climate change. Rising sea levels will eventually lead to coastal erosion and saline intrusions.

The aim of this study was to measure abiotic variables and collect samples in 39 South Pacific freshwater ecosystems listed in Scott's (1993) Directory of Wetlands in Oceania. Species lists for algae, nematodes, rotifers, copepods, cladocerans, ostracods, and mites (Oribatida) are presented. We also discuss our results in respect to potential threats to freshwater ecosystems and provide recommendations for future research.

MATERIALS AND METHODS

Sampling Sites

The majority of water bodies were volcanic crater lakes (Nos. 12, 13, 15–29, 31–34, 36, 37 [Plate 1, Table 1]). Lake Vaihiria (1) on Tahiti was originally formed by a rock slide. Together with Lake Bleu (2), the two water bodies are artificially dammed for hydropower. On the Cook Islands the freshwater runoff from the basaltic volcanic cone is collected at the inner cliff of an old fringingreef surface that has been exposed through tectonic uplift (Makatea [Ellison 1994, Parkes 1997] [3, 4, 6, 10]). The underground drainage in the Makatea is occasionally open to the surface at partly collapsed karst caves (often referred to as “Vai” for “freshwater” [5, 7, 8, 9, 11]). Similar openings in the karst water system are found in Vanuatu (30, 35). Lake Isiwi on Tanna was originally dammed by the active volcano Mount Yasur but drained in 2000. Only a few puddles remained near the outflowing river (39). In a few cases the formation of the lake basin was not obvious (14, 33, 38).

Some craters in Fiji were probably formed more than 2 million years ago (Nunn 1998 and pers. comm.), but most of them are younger. All lakes that depend on the water table of the entire island must have been dry during the last glacial maximum when the sea level in the tropical Pacific was 120 m below current level. Most of them started filling again in the Early (10,000–6,000 B.P.) or the Middle Holocene (6,000–3,000 B.P.) when the sea level was 1.5–2.0 m above its current level (Nunn 1999 and pers. comm.). The Manaro lakes on Ambae, Vanuatu, are only 420 yr old. Fourteen years ago, Lake Manaro Vui (29) underwent strong heating due to volcanic activity, and water levels fluctuated ∼10 m within 3 days (Robin and Monzier 1995). In 2005, a new crater started to rise within the lake.

Sampling and Species Identification

Water bodies classified as freshwater ecosystems were chosen from the compilation of wetlands in Oceania (Scott 1993). Additional inland aquatic ecosystems were located on various geographic maps and aerial photographs. Finally, R.S. and G.D. sampled a total of 39 different water bodies on 18 different islands (Table 1). Conductivity, pH, and temperature were measured at the water surface with a portable device (Hanna Instruments). The presence of fish was assessed by observation from shore or by snorkeling. A lake containing solely eels was not classified as a “fish-lake” because eels are predators and do not feed on detritus or zooplankton. In this respect, all “fish-lakes” likely were stocked, although time constraints, difficult accessibility, or turbid water prevented us from determining species in three cases and from assuring presence or absence of fish in seven cases.

Plankton samples were collected with a 30 µm plankton net (21 cm diameter). Shallow water bodies (<1 m) were sampled either by scooping up water with a beaker or by throwing out and retrieving the net from shore. In larger lakes we swam with the net and dived down to a depth of approximately 5 m. When macrophytes were present the net was dragged through them; however strictly benthic microhabitats (e.g., different sediments) were not targeted specifically. Twenty-five ml of each sample were preserved in 4% formaldehyde. In the laboratory species were isolated under a stereomicroscope, prepared on slides, and identified to genus or species level: algae (excluding desmids and most diatoms) by E.R.; desmids by R.L.; nematodes by N.R. and W.T.; rotifers by R.S. and C.D.J.; cyclopoid copepods by F.S.; harpacticoid copepods by F.F.; cladocerans by A.A.K.; ostracods by K.M.; oribatids by H.S.

Information is provided where the different taxa so far have been reported to occur. We chose the terms circumtropical, tropicopolitan, cosmopolitan, and restricted distribution. In the literature, the different terms are used inconsistently to describe distributions, and the geographic or climatic definitions are seldom provided (e.g., pan-, cosmo-, circumtropical, tropicopolitan). Our definitions follow.

TABLE 1

Lentic Freshwater Ecosystems Sampled on South Pacific Islands

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Circumtropical: Species that have primarily been reported from tropical environments between the Tropics of Cancer (23°27′ N) and Capricorn (23°27′ S).

Tropicopolitan: Organisms that are frequently found throughout the tropical and subtropical zones (up to approx. 34° N and S) but that do occur at higher latitudes, if local temperature regimes permit.

Cosmopolitan: Species that are found worldwide. The occurrence in polar regions or high-altitude environments is not confirmed in every case.

Restricted distribution: Species that so far have been found only in a restricted area (e.g., Australasia: the islands of the southern Pacific Ocean, including Australia, New Zealand, and New Guinea).

Statistical Analysis

The exploratory power of different environmental variables to predict overall species richness was tested using Generalized Linear Models (GLM [McCullagh and Nelder 1989]): archipelago (seven levels: Tahiti, two sites; Cook Islands, nine; Fiji, three; Samoa, five; Wallis, six; Tonga, four; Vanuatu, nine), fish (two levels: present, absent), submersed vegetation (two levels), active volcanism near water body (two levels), and eight continuous variables (log conductivity, pH, temperature, log surface area, log maximum depth, log [altitude + 1], geographical longitude, and latitude). Conductivity, altitude, maximum depth, and surface area were log transformed due to skewed data. Acid Lake Manaro Vui contained no living organisms and was omitted from the analysis.

Community composition was analysed with Nonlinear MultiDimensional Scaling (NMDS [Kruskal 1964]) using presence-absence data of all determined taxa and the environmental variables. The Bray-Curtis index was calculated because it performs well in detecting underlying ecological gradients. The analysis was done with the R package Vegan (Oksanen et al. 2007) following Minchin (1987).

In ordination, fitted vectors (biplot arrows) have become the method of choice for testing environmental variables. However, traditional linear fits onto ordination diagram models may yield poor fits, due to curvature and distortion in ordination space. Given these restrictions, we additionally applied Thin-Plate Splines (TPS) estimated with General Additive Models (GAM [Wood 2003]). TPS interpolate a smooth surface passing through the values of environmental variables. To assess significance levels of fitted vectors and factors, 1,000 permutations were run.

Because communities within an archipelago were similar, they were chosen as permutable units for a third approach in statistical analysis. NPMANOVA (NonParametric Multivariate ANalysis Of VAriance) is a method in which simultaneous responses of several, potentially nonindependent variables (usually species in an assemblage) are compared in a one-factor or multifactorial ANOVA setting (Anderson 2001, McArdle and Anderson 2001). P values were obtained by 4,999 permutations.

RESULTS

Sampling Sites

A distance of approx. 4,500 km separates the eastern- and westernmost sampling sites, in Tahiti and Vanuatu, respectively (Plate 1, first panel). The sampled water bodies covered a broad range in altitude (0–1,397 m above sea level [a.s.l.]), surface area (>0.001–1,900 ha), depth (10 cm-360 m), temperature (19.5°C-36.6°C), pH (1.56–9.75), and conductivity (3->4,000 µS cm-1 [Figure 1]). Ion content showed a bimodal distribution with the majority of sampling sites being either softwater or slightly saline environments. Crater lakes near sea level ranged from pure freshwater to almost oligohaline conditions (Table 1). Increased ion content has also been observed in water bodies with no adjacent volcanic activity and most likely resulted from an underground connection to the sea. Lake Manaro Vui was acidic (pH 1.56) due to volcanic activity and contained no living organisms.

PLATE1.

Sampling sites in Oceania (first panel) and photographs of South Pacific freshwater ecosystems taken during the survey in 2004/2005 (subsequent panels).

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PLATE2.

Cumulative number of species of the major groups of organisms in the 39 different water bodies. Stocked ecosystems are marked by a fish symbol above the bar. Elevated conductivity (> 1000 µS cm-1) is indicated by an “s” below the x-axis.

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FIGURE1.

Number of water bodies in relation to altitude, area, depth, temperature, pH, and conductivity.

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Fish Species

Of the 39 sampled water bodies, at least 17 contained large numbers of one or more nonindigenous fish species (Table 1). We encountered tilapias (Oreochromis spp., Tilapia spp., Sarotherodon spp.) mosquitofish (Poecilia reticulata), guppies (Gambusia affinis), swordtails (Xiphophorus hellerii), and goldfish (Carassius auratus). Native freshwater eels were observed in Lake Rotonui (Anguilla obscura) and Lake Letas (A. marmorata or A. megastoma), but different species of eels are reported by locals to occur in all larger crater lakes. Endemic fish (e.g., Gobiidae or Eleotridae) were not observed. They are amphidromous and probably restricted to lotic ecosytems.

Species Richness and Community Composition

A total of 138 algal, 36 nematode, 98 rotifer, 32 copepod, nine cladoceran, nine ostracod, and four oribatid taxa were identified (Appendix). The highest cumulative species numbers were found in dormant and shallow craters filled with vegetation such as Lakes Aselemo and Tagimaucia (Fiji), Fiti (Samoa), and Imao (Vanuatu) (Plate 2).

STATISTICAL ANALYSES: GLM: After testing the exploratory power of all variables on species richness, a simplified model was built containing archipelago (P < .001), log conductivity (P < .001), submersed vegetation (P < .001), and fish (P = .026) in linear combination (Table 2). No significant interactions were observed. Model results are presented in the form of a deviance table, which is analogous to an ANOVA table, except that the variance component reported is the deviance rather than the sums of squares (see McCullagh and Neldar [1989] for a full discussion of deviance and Generalized Linear Models). Altitude negatively correlated with conductivity (Pearson's R = -0.79, P < .001). The deviance explained by both variables was nearly the same, so we decided to use conductivity in the model to facilitate ecological interpretation.

NMDS (Table 3): A significant spatial effect was detected and communities were more similar within an archipelago (P < .001). A weak but significant effect was also found for active volcanism (P = .026). Log conductivity (P < .001) and log altitude (P < .001) were the most important factors explaining community composition. In addition, geographical latitude (P = .045) explained a significant amount of species dispersion.

TABLE 2

Analysis of Deviance Table (Generalized Linear Model)

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TABLE 3

Linear Fit of Environmental Variables on Community Composition (Two Dimensions of Nonlinear Multidimensional Scaling)

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GAM (Table 4): Thin-plate splines added surface temperature (P = .010) and longitude (P = .027) as weakly significant variables.

NPMANOVA (Table 5): Significant effects of pH (P = .028) and submersed vegetation (P = .020) emerged.

Distribution

Sixty-six percent of all taxa recorded have a cosmopolitan distribution, 14% are circumtropical/tropicopolitan species, and for 20% a restricted distribution predominantly in Australasia has previously been reported. Crustaceans comprised a lower number of cosmopolitan taxa compared with algae, nematodes, rotifers, and oribatid mites (Figure 2).

DISCUSSION

Distribution and Taxonomic Status

ALGAE: Although a large proportion of the mostly planktonic algae (excluding desmids) are supposed to have a cosmopolitan (60%) distribution, 38% can be grouped into circumtropical (18%) and tropicopolitan (20%) taxa, respectively (Figure 2). The proportion of circumtropical/tropicopolitan taxa is high compared with 19% in a recent Southeast Asian study (Rott et al. 2008). The majority of desmids were cosmopolitan species (Appendix). Out of 54 taxa, 14 are assigned to the Indo-Malaysian North Australian phycogeographic region (sensu Coesel [1996] and Vyverman [1996]). Staurastrum aureolatum was recorded from Australia, New Zealand, and South Africa (Croasdale et al. 1994).

TABLE 4

Fit of Thin-Plate Splines of Continuous Environmental Variables to Community Composition (Fitted by a Generalized Additive Model onto Two Dimensions of Nonlinear Multidimensional Scaling)

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TABLE 5

Effects of Environmental Variables on Community Composition (NPMANOVA on Bray-Curtis Distances)

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NEMATODES: Except for four species, the nematodes are probably all cosmopolitan, but information on distribution is scarce. Dichromadora cf. tobaensis has only been reported from Sumatra (Andrássy 1984), Mesodorylaimus cf. guarani from Paraguay and Costa Rica (Ahmad and Shaheen 2004), Mesodorylaimus cf. meyli from Eurasia (Vinciguerra 2006), and Neoactinolaimus cf. duplicidentatus from Eurasia and Africa (Vinciguerra 2006).

ROTIFERS: More than 90% of all rotifers were widely distributed species. The remainder were predominantly species that were described in the recent past and for which biogeographic information is scarce (e.g., after its discovery in a high-altitude lake in southern India Polyarthra indica [Segers and Babu 1999] has now been found in Africa [Schabetsberger et al. 2004] and throughout the Pacific islands, suggesting a circumtropical distribution).

CYCLOPOID COPEPODS: The copepods Tropocyclops prasinus meridionalis, Ectocyclops rubescens, Mesocyclops aspericornis, and Tropocyclops confinis s.l. all have a circumtropical distribution. The subspecies T. prasinus meridionalis probably deserves to be elevated to species rank. Tropocyclops confinis s.l. is a widely distributed species complex in need of revision. Australoeucyclops aff. timmsi is probably a new taxon; unfortunately Australoeucyclops timmsi was described from New South Wales, Australia (Kiefer 1969), based on females only, and has not been found again. The genus is endemic to Australasia (Karanovič 2004), and so are Mesocyclops woutersi and Thermocyclops crassus macrolasius. The three Mesocyclops aff. woutersi taxa all differ from M. woutersi on the basis of microcharacters whose variability is still unknown (Holyńska 2000). The two Microcyclops aff. varicans species differ substantially in the armature of swimming legs but cannot be attributed to any of the described species; the tropical species of this genus too are in urgent need of revision: Microcyclops varicans is considered to be cosmopolitan, but several species may be included under this name. More taxonomic effort throughout the Australasian region is required to define the borders of distribution of the different copepod species.

FIGURE2.

Distributions of the major taxonomic groups of organisms. For definitions of the terms “cosmopolitan,” “tropicopolitan,” “circumtropical,” and “restricted” distribution, see the Materials and Methods section. The number of taxa determined to species level is shown in each segment.

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HARPACTICOID COPEPODS: Nineteen different harpacticoid species belonging to eight families have been found. Members of the families Phyllognathopodidae, Canthocamptidae, and Parastenocarididae are exclusively continental. Diosaccidae, Louriniidae, Cletodidae, and Laophontidae are predominantly marine but have many representatives occurring in brackish (estuarine) environments. The family Ameiridae contains species occurring in marine, brackish, or freshwater environments. In the following paragraphs only the continental representatives are considered.

The genus Phyllognathopus is distributed worldwide, but its systematics is confused (Dussart and Defaye 1990) and morphological species discrimination is still lacking (Glatzel and Königshof 2005). The specimens from Cook Islands, Tahiti, and Vanuatu resemble in many aspects the specimens from Western Samoa, identified as P. viguieri by Yeatman (1983), and are listed as members of the Australian realm.

Apart from Mesochra sp., a globally distributed genus inhabiting estuaries, canthocamptids are represented by two cosmopolitan genera: Elaphoidella and Epactophanes. Elaphoidella bidens shows a worldwide distribution, and E. sewelli minuta is only known from central Africa and Madagascar (Palaeotropical). Elaphoidella grandidieri has a circumtropical distribution and has been found in continental Africa, Asia, South America, and the Caribbean (Dussart and Defaye 1990). Yeatman (1983) reported it, together with E. taroi, from Fiji and Western Samoa.

The genus Epactophanes has been found on every continent. It has long been considered as monotypic, with E. richardi. The confused systematics is comparable with that of Phyllognathopus (see Dussart and Defaye 1990). A second species, E. philippinus, was recently described from the Philippines and was detected in the samples from Vanuatu, where it cooccurs with an unnamed species. A third, new species was detected on Taveuni, Fiji.

The three representatives of the family Parastenocarididae appear to be directly related to Parastenocaris leeuweni, known from high-altitude bryophytes in Sumatra, and with two unnamed Parastenocaris species described from Sri Lanka (Enckell 1970) and New Caledonia (Dussart 1984). The three species studied here are considered as faunal elements from the Oriental realm.

CLADOCERANS: Among 33 cladoceran species recorded from Pacific islands by previous authors, only Diaphanosoma samoaensis, recently described from Lac Lanoto'o, Samoa (Korovchinsky 2001), is endemic (Forró et al. 2008). We found it also in a neighboring lake on the island of Upolu (23). Ceriodaphnia cornuta and Ilyocryptus spinifer have a predominantly tropicopolitan distribution; however, “C. cornuta” apparently consists of a group of species (Berner 1985), and Ilyocryptus spinifer reaches Nearctic regions in Canada (Kotov and Dumont 2000). Chydorus eurynotus, Diaphanosoma sarsi, and Karualona karua are considered circumtropical (Smirnov 1971, Korovchinsky 2004). Karualona karua also consists of a group of several species with unknown borders of distribution (Dumont and Silva-Briano 2000). Alona setigera has been regarded as Australian, but similar forms have been found in Brazil (Santos-Wisniewski et al. 2001). Bosmina meridionalis is restricted to Australia and New Zealand (Kořínek 1983).

OSTRACODS: With two new genera and three new species the ostracods are the group with the highest level of new taxa (>30%). Limnocythere notodonta has been found in East Africa (McKenzie 1971), and Sarscypridopsis glabrata is known from South Africa (Martens 2001). The new Sarscypridopsis species also have South African affinities (K.M., unpubl. data). More taxonomic research is required to resolve if these are undescribed taxa with a wider distribution or real endemics. The Paracypridinae of Tofua crater lake probably have marine ancestors that overcame the salinity boundary and colonized inland stygohabitats before entering the lake. Cypridopsis vidua and Penthesilenula brasiliensis are cosmopolitan (Martens and Rossetti 2002); Stenocypris major is a circumtropical species (Martens 2001). In concordance with Meisch et al. (2007) we only found female ostracods, implying that all species reproduce parthenogenetically.

ORIBATID MITES: Although most oribatid mites are known as inhabitants of terrestrial habitats, a few taxa are bound to aquatic habitats (Schatz and Behan-Pelletier 2008). All four species of oribatid mites encountered in the material reported here are known to colonize wet and freshwater habitats. Trypochthoniellus longisetus is a cosmopolitan species (excluding Antarctica). Hydrozetes lemnae was found in the Palaearctic, Neotropical, and Oriental regions, as well as in Australia and the Pacific islands. Trimalaconothrus maior has been reported from the Holarctic, western Oriental, and Neotropical regions and New Zealand and the subantarctic islands but not yet from the South Pacific islands. Nasozetes stunkardi is a rare species, which had previously been found only on Guam and the Philippines (Sengbusch 1957). The known distribution of the genus is restricted to the Greater Sunda and the western Pacific islands.

Species Richness

The highest species richness was recorded in high-altitude, fish-free, shallow lakes in the late stage of succession where the basin had silted up and was full of submersed vegetation (12, 13, 25, 32). They were also characterized by comparatively low pH and conductivity. Because we did not specifically sample benthic microhabitats, we introduced a bias toward collecting more tychoplanktonic species in these ecosystems. However, Lake Tagimaucia on Taveuni exhibited by far the highest number of species, although other shallow sites were sampled. In this respect this lake combines several features that are likely to be positively related to species richness: it is situated in the large and geologically old Fiji Archipelago; it is itself relatively old, large, and silted compared with most other investigated crater lakes (minimum of 14,000 yr B.P. [Southern 1986]); and it is close to the Australian continent. In addition the lake is surrounded by diverse swamp vegetation. Within the lake, sedges, mosses, and algae provide a rich mosaic of microhabitats (Southern et al. 1986:509). In contradiction to our results those authors stated that “the fauna of the lake and swamp are low in both diversity and abundance” and that “crustaceans and other invertebrate taxa were scarcely recorded”; however the major focus of that study was on higher plants and animals.

We did not find a significant decrease in species richness with increasing distance of the island from the Australian continent. However, species accumulation curves showed that we sampled no more than 55% of all species present. Each water body was only visited once and different benthic microhabitats were not sampled separately. Hence, additional studies are necessary to obtain a more complete species inventory of South Pacific freshwater ecosystems.

Dispersal

Our survey confirms earlier results from Pacific islands that had revealed impoverished species assemblages with a large proportion of cosmopolitan or circumtropical species and a low level of endemism (Galapagos Islands) or no endemism at all (DeSmet 1989a,b, Segers and Dumont 1993, Dumont and Martens 1996). However, the higher similarity of species communities within archipelagos suggests a more frequent dispersal of freshwater organisms between lakes on the same or between neighboring islands compared with large distance dispersal across the open ocean.

The relatively low number of crustaceans together with a higher proportion of new taxa suggests that viable propagules arrive at a lower rate compared with smaller invertebrates or algae. Endemic species were found, implying that the gene flow between archipelagos is probably low, because of less-effective dispersal abilities, and it may not be frequent enough to overcome local selective pressures. Live resting eggs of calanoid copepods obviously do not reach the South Pacific islands at all, because this group was completely absent from all 39 water bodies.

The relative importance of the different vectors wind, rain, animals, and humans for long-distance dispersal of freshwater invertebrates is still unknown. We can only speculate that the high proportion of small, cosmopolitan taxa in our samples is an indication of arrival by wind and rain. Bohonak and Jenkins (2003) and Bilton et al. (2001) questioned that anemochory and/or ombrochory are important for long-distance dispersal, but Muñoz et al. (2004) found evidence that connection by “wind highways” increases floristic similarities in the Southern Hemisphere. Green and Figuerola (2005) and Frisch et al. (2007) emphasized the importance of migrating birds as vectors. Viable resting eggs of crustaceans have been found attached to feet, bills, and plumage of waterfowl (external phoresis) but also survived transport through the digestive system (internal phoresis). However, the limited number of freshwater habitats on South Pacific islands is not part of major flyways of birds. Some shorebirds are occasionally found near the freshwater sites. They follow the East Asian-Australasian flyway, stretching from Siberia and Alaska, southward through East and Southeast Asia, to Australia and New Zealand. The origin of other vagrant birds (e.g., ducks) is difficult to track down (D. Wading, pers. comm.).

There is a growing list of human-mediated long-distance dispersal of zooplankton species and subsequent establishment of populations (for case studies see Panov et al. [2004]). Humans started to colonize the Pacific islands in a series of waves starting to flow out of East Asia 3,000–4,000 yr ago. The eastern Pacific was reached during the first millennium A.D. (Campbell 2003). Humans imported tools, crops, and animals that could have been contaminated with diapausing stages of freshwater invertebrates. For example, Dumont and Martens (1996) suspected humans as the introducing agent of two crustacean species on Easter Island, which had only been found in the top sediment layers of a crater lake. The abuse of lakes as dumping sites of military equipment during World War II (e.g., Wallis Island) may also have altered species communities. Relatively recently different alien fish species have been introduced into Pacific lakes and ponds and could have carried invertebrate resting eggs in their digestive tracts. Only a systematic survey of sediment cores would shed light on changes of species communities over time.

Threats to Freshwater Communities

Altitude was an important factor in explaining community composition and richness. It was negatively correlated with salt content and probability of fish stocking. Human impact generally decreases with increasing altitude, but we were unable to quantify factors such as habitat degradation within the watershed and nutrient input. However, at this point we anticipate two major threats to freshwater communities, as follows.

(1) Fish Introduction: Of the 39 water bodies investigated, at least 17 had been stocked with nonindigenous fish species. Only three large and deep crater lakes (28, 31, 34) remain unstocked. At least 56 species of freshwater fish have been introduced to the Pacific islands exclusive of the Hawaiian Islands, but not all stocking measures have been successful (Eldredge 2000). Some of these actions date back to the beginning of the last century (e.g., Lake Lanoto‘o on Upolu, Samoa, was stocked with goldfish [Carassius auratus] during German occupation). During a campaign in the 1950s to 1970s, tilapias (mostly Oreochromis mossambicus but also O. niloticus, O. aureus, O. urolepis, O. macrochir, Tilapia rendalli, T. zillii, Sarotherodon melanotheron, and S. occidentalis), mosquitofish (Gambusia affinis), and guppies (Poecilia reticulata) were released (Maciolek 1984, Eldredge 2000). Oreochromis mossambicus was the most widely introduced species, having been taken to 19 Pacific island territories, followed by Gambusia affinis (14 territories) and Poecilia reticulata (10 territories).

The main reasons were the provision of an additional source of protein for the local communities and the biological control of mosquitoes. Guppies and swordtails (Xiphophorus hellerii, R.S. and G.D., pers. obs. in Lac Vaihiria) probably originated from the aquarium trade and were accidentally or voluntarily released into natural ecosystems. Once populations are established, there is a high risk of contamination of additional water bodies due to transferral or escape from the point of release.

Today these introduced fish are considered to be pests on Pacific islands. Nevertheless, we witnessed new and illegal stocking of Tilapia sp. into lakes in Vanuatu. Their impact on native communities has been detrimental to various groups of animals including native insects (Englund 1999), fish (Lobel 1980), and birds (Stinson et al. 1991, Scott 1993). However, their impact on the native plankton communities of South Pacific lakes has never been studied.

Effects of fish on species richness and community composition were masked by other more prominent variables such as conductivity. However, all introduced fish species are known to develop large populations and prey on a variety of food items at different trophic levels including detritus, algae, and zooplankton (FishBase 2008). Their effect on ecosystem processes is complex (Eby et al. 2006), but direct (predation) and indirect effects (e.g., increased turbidity and loss of microhabitats) may have caused changes in freshwater communities. No systematic monitoring of South Pacific freshwater ecosystems accompanied the large-scale stocking campaign with tilapias and we can only speculate about the impact on the environment. Scott (1993) reported that the originally algal-colored green crater lake on Niuafo‘ou, Tonga, lost its color after the introduction of tilapias. Precisely because we know so little about these ecosystems and their invertebrate communities, protecting the remaining lakes from further deterioration is of utmost importance.

(2) Global Warming: We argue that a major threat to South Pacific freshwater ecosystems may arise from global warming and salinization. The Intergovernmental Panel on Climate Change (IPCC) (2007) projected that owing to global warming temperatures will rise by 1.8°C–4.0°C accompanied by a sea level rise of 0.18–0.59 m over the next century. Some of the models also predict more frequent El Niño-Southern Oscillation events (ENSOs), resulting in a 26%–200% increase in rainfall over the central and east-central Pacific and with possible decreases in the Melanesian and Polynesian regions. Although there is no consensus about the behavior of tropical cyclones in a warmer world, there is reasonable confidence that their intensity is likely to increase by 10%–20% when atmospheric levels of carbon dioxide reach double preindustrial levels as predicted for the end of the twenty-first century (Burns 2002, Hay et al. 2003, Intergovernmental Panel on Climate Change [IPCC] 2007).

Freshwater is a limited resource on most Pacific islands and hence there is great concern about the impact of global warming (Burns 2002, Hay et al. 2003). The basal aquifer on Pacific islands essentially forms a freshwater lens floating on denser salt water (Ghyben-Herzberg lens). Possible scenarios are either that the rising sea level will result in the intrusion of salt water into the freshwater lenses (Watson et al. 1998, White et al. 2007) or, alternatively, that a rise of 40–50 cm might actually increase their volume because the top of the freshwater lens would rise while its base remains relatively unaffected (East-West Center 2001). However, if the rise in sea level is accompanied by coastal erosion together with a reduction in rainfall, the volume of freshwater could be seriously reduced (Burns 2000).

Some of the larger lakes will most likely become important future freshwater reservoirs for humans. Water of Lake Wai Memea (Ambae, Vanuatu) is pumped to the top of the crater rim and provides freshwater for the town of Lolowai (R.S. and G.D., pers. obs.). Further, use of the water of Lake Lanoto‘o on Samoa is being considered to satisfy the growing demand of freshwater in the capital, Apia (T. Tipama‘a, pers. comm.). However, nothing is known about the limnological conditions in these ecosystems.

There is evidence from our survey for reduced species richness and distinct communities in water bodies experiencing saline intrusions (e.g., 3, 5–11, 17, 30, 34–37) such as the Vais and lakes within the Makatea or the deep crater lakes near sea level. For the latter we assume that freshwater floats on an ion-rich saline and probably hypoxic hypolimnion as described in a preliminary study of the remote Tongan lake Vai Lahi on Niuafo‘ou island (Maciolek and Yamada 1981).

Rising sea levels, reduced precipitation, potential water removal, and higher frequency of more intense tropical storms could all lead to more intense mixis of the stratified water bodies with a transfer of ion-rich water into the epilimnion. Besides a steady, slow increase in salinity, sudden pulses of salt intrusions into epilimnetic layers seem possible with a potential loss of resilience of the entire ecosystem (Scheffer et al. 2001, Hart et al. 2003). Freshwater plankton communities are sensitive to such saline intrusions (James et al. 2003, Nielsen et al. 2003). As salinity increases, the abundance and species richness of rotifers and microcrustaceans generally decrease (Brock and Shiel 1983, Halse et al. 1998). The threshold for the majority of microzooplankton organisms has been placed at salinities of less than 1–2 ppt (James et al. 2003). Schallenberg et al. (2003) were able to demonstrate severe perturbations of the zooplankton community structure and abundance by even minor saline intrusions just above the range we observed at the surface of Lake Lalolalo and Tofua crater lake.

In their review, Nielsen et al. (2003) stressed the paucity of suitable information for making informed predictions on what future aquatic communities will look like as salinities increase. We therefore suggest launching a monitoring program to assess the stratification and species communities in lakes with various degrees of saltwater intrusions. Long-term data sets should allow scientists to pinpoint species of bioindicative value and provide first predictions on how invertebrate communities might react to water removal and/or saline intrusions. With this information available, these crater lakes could serve as model systems for the detection of salinization, thereby providing Pacific island nations with a warning system for environmental change. Continued ecological and taxonomic research in combination with better management strategies is vital to safeguard the remaining species richness.

ACKNOWLEDGMENTS

We thank Hoifua Aholahi, Calando Aiga, Ernest Bani, Tony Chamberlain, Emmanuel Coutures, Rainer Drozdowski, Paula Holland, Vainunpo Jungblut, Dona Kalfatek, Francis Latu, Faumuina Sailimalo V.P. Liu, Russel Nari, Patrick Nunn, Marc Overmars, Asipeli Palaki, Uilou Samani, Tepa Suaesi, Toni Tipama‘a, Paino Vanai, Paul Vuhu, Peter Whitelaw, Adrew Wright, and Leon Zann for scientific information, logistic support, or help with obtaining permits. We are indebted to Leia Alien, Russel and Tenssly Aru, Paulina and Jim Bibi, David Boseto, Rob and Alex Crapper, the Daugunu family, Fr. Luke and Ronna Dini, Faamanuiaga Etenati, Ropate and Litea Masioliva, Herbert Mohr, Mii O'Brien, John Peter, Ioelu Siaea, Posa Skelton, Falakiko Uatini, Failauga Usutoe, Jim and Juliett Ventress, and Henry Vuki for their help and friendship. The warm hospitality and support of many more people throughout the South Pacific made this study possible. Two anonymous reviewers provided numerous suggestions. We thank Professor Hans Adam and the “Stiftungs und Förder-ungsgesellschaft der Universität Salzburg” for covering printing costs and Professor Alois Lametschwandtner for providing funds to N.R. The base map of Oceania (Plate 1) was copied with permission from the CD-ROM Der grosse Kosmos 3D-Globus, © 2002 United Soft Media Verlag GmbH, Munich.

Literature Cited

  1. W. Ahmad , and A. Shaheen . 2004. Five new and two known species of the family Dorylaimidae (Nematoda: Dorylaimida) from Costa Rica. Nematology 6:567–586. Google Scholar

  2. M. Anderson 2001. A new method for nonparametric multivariate analysis of variance. Aust. Ecol. 26:32–46. Google Scholar

  3. I. Andrássy 1984. Klasse Nematoda. Pages 1–509 in H. Franz, ed. Bestimmungsbücher zur Bodenfauna Europas. Gustav Fischer Verlag, Stuttgart. Google Scholar

  4. D. B. Berner 1985. Morphological differentiation among species in the Ceriodaphnia cornuta complex (Crustacea, Cladocera). Verh. Int. Ver. Limnol. 22:3099–3103. Google Scholar

  5. D. T. Bilton , J. R. Freeland , and B. Okamura . 2001. Dispersal in freshwater invertebrates. Annu. Rev. Ecol. Syst. 32:159–181. Google Scholar

  6. A. J. Bohonak , and D. G. Jenkins . 2003. Ecological and evolutionary significance of dispersal by freshwater invertebrates. Ecol. Lett. 6:7837ndash;796. Google Scholar

  7. M. A. Brock , and R. J. Shiel . 1983. The composition of aquatic communities in saline wetlands in Western Australia. Hydrobiologia 105:77–84. Google Scholar

  8. W. C. G. Burns 2000. The impact of climate change on Pacific Island developing countries in the 21st century. Pages 233–339 in A. Gillespie and W. C. G. Burns, eds. Climate change in the South Pacific: Impacts and responses in Australia, New Zealand, and small island states. Kluwer Academic Publishers, Dordrecht. Google Scholar

  9. W. C. G. Burns 2002. Pacific Island developing country water resources and climate change. Pages 113–131 in P. H. Gleick, W. C. G. Burns, E. L. Chalecki, M. Cohen, K. K. Gushing, A. S. Mann, R. Reyes, G. H. Wolff, and A. K. Wong, The World's Water 2002–2003: The bienniel report on freshwater resources. Island Press, Washington, D.C. Google Scholar

  10. I. C. Campbell 2003. Worlds apart: A history of the Pacific islands. Canterbury University Press, Christchurch, New Zealand. Google Scholar

  11. P. A. Chappuis 1955. Notes sur les Copépodes. Notes Biospéol. 10:7–101. Google Scholar

  12. F. M. Coesel 1996. Biogeography of desmids. Pages 41–53 in J. Kristiansen, ed. Biogeography of freshwater algae. Dev. Hydrobiol. 118/Hydrobiologia 336. Google Scholar

  13. H. Croasdale , E. A. Flint , and M. M. Racine . 1994. Flora of New Zealand. Freshwater algae, Chlorophyta, desmids with ecological comments on their habitats. Vol. 3: Staurodesmus, Staurastrum and the filamentous desmids. Manaaki Whenua Press, Lincoln, Canterbury, New Zealand. Google Scholar

  14. A. L. Dahl 1980. Regional ecosystems survey of the South Pacific area. SPC Technical Paper 179. South Pacific Commission, Noumea, New Caledonia. Google Scholar

  15. D. Defaye 2001. A new Mesocyclops (Copepoda, Cyclopidae) from New Caldedonian freshwaters. Crustaceana (Leiden) 74:647–658. Google Scholar

  16. W. H. DeSmet 1989a. Rotifera uit de Galapagoseilanden. Natuurwet. Tijdschr. 69:110–131. Google Scholar

  17. W. H. DeSmet 1989b. Addendum bij: Rotifera uit de Galapagoseilanden. Natuurwet. Tijdschr. 71:80–81. Google Scholar

  18. H. J Dumont . 1983. Biogeography of rotifers. Hydrobiologia 104:19–30. Google Scholar

  19. H. J. Dumont , and K. Martens . 1996. The freshwater microcrustacea of Easter Island. Hydrobiologia 325:83–99. Google Scholar

  20. H. J. Dumont , and H. Segers . 1996. Estimating lacustrine zooplankton species richness and complementarity. Hydrobiologia 341:125–132. Google Scholar

  21. H. J. Dumont , and M. Silva-Briano . 2000. Karualona n.gen. (Anomopoda: Chydoridae), with a description of two new species, and a key to all known species. Hydrobiologia 435:61–82. Google Scholar

  22. B. H Dussart . 1984. Sur quelques crustacés de Nouvelle-Calédonie. Rev. Hydrobiol. Trop. 17:301–308. Google Scholar

  23. B. H. Dussart 1986. Parathalassius fagesi gen. et. sp. nov. (Centropagidae), copepod nouveau de Nouvelle-Calédonie. Cah. Biol. Mar. 27:63–68. Google Scholar

  24. B. H. Dussart , and D. Defaye . 1990. Répertoire mondial des crustacés copépodes des eaux intérieures. III. Harpacticoïdes. Crustaceana Suppl. (Leiden) 16:1–384. Google Scholar

  25. East-West Center. 2001. Pacific Island regional assessment of the consequences of climate variability and change. EastWest Center, Honolulu, Hawai‘i,  http://www2.eastwestcenter.org/climate/assessment/climate_draft2a.htmlGoogle Scholar

  26. J. A. Eby , W. J. Roach , L. B. Crowder , and J. A. Stanford . 2006. Effects of stockingup freshwater food webs. Trends Ecol. Evol. 21:576–584. Google Scholar

  27. L. G. Eldredge 2000. Non-indigenous freshwater fishes, amphibians, and crustaceans of the Pacific and Hawaiian islands. Pages 173–190 in G. Sherley, ed. Invasive species in the Pacific: A technical review and draft regional strategy. South Pacific Regional Environmental Programme, Apia, Samoa. Google Scholar

  28. J. C. Ellison 1994. Palaeo-lake and swamp stratigraphic records of holocene vegetation and sea-level changes, Mangaia, Cook Islands. Pac. Sci. 48:1–15. Google Scholar

  29. P. H. Enckell 1970. Parastenocarididae (Copepoda Harpacticoida) from Ceylon. Ark. Zool. 22:545–556. Google Scholar

  30. R. A. Englund 1999. The impact of introduced poeciliid fish and Odonata on the native Megalagrion damselflies of Oahu Island, Hawaii. J. Insect Conserv. 3:225–243. Google Scholar

  31. A. Eyualem , and A. Coomans . 1995. Freshwater nematodes of the Galapagos. Hydrobiologia 299:1–51. Google Scholar

  32. T. Fenchel , and B. J. Finlay . 2004. The ubiquity of small species: Patterns and local and global diversity. BioScience 54: 777–784. Google Scholar

  33. W. Foissner 2004. Ubiquity and cosmopolitanism of protists questioned. SILnews 43:6–7. Google Scholar

  34. L. Forró , N. M. Korovchinsky , A. A. Kotov , and A. Petrusek . 2008. Global diversity of cladocerans (Cladocera; Crustacea) in freshwater. Hydrobiologia 595:177–184. Google Scholar

  35. D. G. Frey 1982. Questions concerning cosmopolitanism in Cladocera. Arch. Hydrobiol. 93:484–502. Google Scholar

  36. D. Frisch , A. J. Green , and J. Figuerola . 2007. High dispersal capacity of a broad spectrum of aquatic invertebrates via waterbirds. Aquat. Sci. 69:568–574. Google Scholar

  37. T. Glatzel , and D. Königshof . 2005. Cross-breeding experiments among different populations of the “cosmopolitan” species Phyllognathopus viguieri (Copepoda: Harpacticoida). Hydrobiologia 534:141–149. Google Scholar

  38. J. Green 1992. Island biogeography, diversity and dominance of zooplankton in crater lakes on the Azores. Biol. J. Linn. Soc. 46:189–205. Google Scholar

  39. A. J. Green , and J. Figuerola . 2005. Recent advances in the study of long-distance dispersal of aquatic invertebrates via birds. Div. Dist. 11:149–156. Google Scholar

  40. S. A. Halse , R. J. Shiel , and W. D. Williams . 1998. Aquatic invertebrates of Lake Gregory, North-western Australia, in relation to salinity and ionic composition. Hydrobiologia 381:15–29. Google Scholar

  41. B. T. Hart , P. S. Lake , J. A. Webb , and M. R. Grace . 2003. Ecological risk to aquatic systems from salinity increases. Aust. J. Bot. 51:689–702. Google Scholar

  42. J. E. Havel , and J. B. Shurin . 2004. Mechanisms, effects, and scales of dispersal in freshwater zooplankton. Limnol. Oceanogr. 49:1229–1238. Google Scholar

  43. J. E. Hay , N. Mimura, J. Campbell, S. Fifita, K. Koshy, R. F. McLean, T. Nakalevu , P. Nunn , and N. de Wet . 2003. Climate variability and change in sea-level rise in the Pacific Islands region: A resource book for policy and decision makers, educators and other stakeholders. South Pacific Regional Environmental Programme, Apia, Samoa. Google Scholar

  44. F. He , K. J. Gaston , E. F. Connor , and D. S. Srivastava . 2005. The local-regional relationship: Immigration, extinction, and scale. Ecology 86:360–365. Google Scholar

  45. D. O. Hessen , B. A. Faafeng, V. H. Smith , V. Bakkestuen , and B. Walseng . 2006. Extrinsic and intrinsic controls of zooplankton diversity. Ecology 87:433–443. Google Scholar

  46. M. Holyńska 2000. Revision of the Australasian species of the genus Mesocyclops Sars, 1914 (Copepoda: Cyclopidae). Ann. Zool. 50:363–447. Google Scholar

  47. Intergovernmental Panel on Climate Change (IPCC). 2007. Fourth assessment report.  http://www.ipcc.ch/ipccreports/ar4-syr.htmGoogle Scholar

  48. K. R. James , B. Cant , and T. Ryan . 2003. Responses of freshwater biota to rising salinity levels and implications for saline water management: A review. Aust. J. Bot. 51:703–713. Google Scholar

  49. P. M. Jenkin 1929. Notes on some Cladocera from the New Hebrides. Ann. Mag. Nat. Hist., Ser. 10 4:246–249. Google Scholar

  50. C. D. Jersabek 2003. Freshwater Rotifera (Monogononta) from Hawai‘i: A preliminary checklist. Records of the Hawai‘i Biological Survey. Bishop Mus. Occas. Pap. 74:46–72. Google Scholar

  51. T. Karanovič 2004. Subterranean copepods (Crustacea: Copepoda) from arid Western Australia. Crustaceana Suppl. (Leiden) 3:1–366. Google Scholar

  52. F. Kiefer 1969. Eine neue ParacyclopsArt (Crustacea: Copepoda) aus Australien. Zool. Anz. 182:91–94. Google Scholar

  53. V. Kořínek 1983. Genus Diaphanosoma. Pages 10–12 in N. N. Smirnov and B. V. Timms, eds. Revision of Australian Cladocera. Rec. Aust. Mus. Suppl. 1. Google Scholar

  54. N. M. Korovchinsky 2001. Review of Sididae (Crustacea: Cladocera: Ctenopoda) of the Pacific Ocean islands, with description of a new species of Diaphanosoma from West Samoa. Hydrobiologia 455:171–181. Google Scholar

  55. N. M. Korovchinsky 2004. Cladocerans of the order Ctenopoda of the world fauna (morphology, systematics, ecology, biogeography). KMK Press, Moscow. [In Russian.] Google Scholar

  56. A. A. Kotov , and H. J. Dumont . 2000. Analysis of the Ilyocryptus spinifer s. lat. species group (Anomopoda, Branchiopoda), with description of a new species. Hydrobiologia 428:85–113. Google Scholar

  57. J. Kristiansen , ed. 1996. Biogeography of freshwater algae. Dev. Hydrobiol. 118, Hydrobiologia 336. Google Scholar

  58. J. Kristiansen 2005. Endemicity in silicascaled chrysophytes. Nova Hedwigia, Beiheft 128:65–83. Google Scholar

  59. J. B. Kruskal 1964. Nonmetric multidimensional scaling: A numerical method. Psychometrika 29:115–129. Google Scholar

  60. K. Lindberg 1954. Cyclopides (Crustacés Copépodes) d'iles du Pacifique Sud (Mélanésie et Micronésie) et de Bornéo. K. Fysiogr. Sällsk. Lund Förh. 24:161–174. Google Scholar

  61. P. S. Lobel 1980. Invasion of the Mozambique tilapia (Sarotherodon mossambicus; Pisces; Cichlidae) of a Pacific atoll marine ecosystem. Micronesica 16:349–355. Google Scholar

  62. L. L. Loope 1998. Hawaii and Pacific Islands. Pages 747–774 in M. J. Mac, P. A. Opler, C. E. Puckett Haecker, and P. D. Doran, eds. Status and trends of the nation's biological resources. U.S. Geological Survey, Reston, Virginia. Google Scholar

  63. A. G. Lowndes 1928. Freshwater Copepoda from the New Hebrides. Ann. Mag. Nat. Hist., Ser. 10 1:704–712, pls. 20–21. Google Scholar

  64. A. G. Lowndes 1931. On Entomostraca from the New Hebrides collected by Dr. J.R. Baker. Proc. Zool. Soc. Lond. for 1930:973–977, pls. 1–2. Google Scholar

  65. J. A. Maciolek 1984. Exotic fishes in Hawaii and other islands of Oceania. Pages 131–161 in W. R. Courtenay Jr. and J. R. Stauffer Jr., eds. Distribution, ecology, and management of exotic fishes. Johns Hopkins University Press, Baltimore, Maryland. Google Scholar

  66. J. Maciolek , and R. Yamada . 1981. Vai Lahi and other lakes of Tonga. Verh. Int. Ver. Limnol. 21:693–698. Google Scholar

  67. K. Martens 2001. Ostracoda. Pages 9–77 in J. A. Day, I. J. de Moor, B. A. Stewart, and A. E. Louw, eds. Guides to the freshwater invertebrates of southern Africa. Vol. 3. Crustacea II. Ostracoda, Copepoda and Branchiura. Water Research Commission Report TT 148/01. Google Scholar

  68. K. Martens , and G. Rossetti . 2002. On the Darwinulidae (Crustacea, Ostracoda) from Oceania, with the description of Vestalenula matildae n. sp. Invertebr. Syst. 16:195–208. Google Scholar

  69. B. McArdle , and M. Anderson . 2001. Fitting multivariate models to community data: A comment on distance based redundancy analysis. Ecology 82:290–297. Google Scholar

  70. R. H. McArthur , and E. O. Wilson . 1967. The theory of island biogeography. Princeton University Press, Princeton, New Jersey. Google Scholar

  71. P. McCullagh , and J. Nelder . 1989. Generalized Linear Models. 2nd ed. Chapman and Hall, London. Google Scholar

  72. K. G. McKenzie 1971. Entomostraca of Aldabra, with special reference to the Genus Heterocybris (Crustacea, Ostracoda). Philos. Trans. R. Soc. Lond., Ser. B 260:257–297. Google Scholar

  73. C. Meisch , N. Mary-Sasal , J.-P. Colin , and K. Wouters . 2007. Freshwater Ostracoda (Crustacea) collected from the islands of Futuna and Wallis, Pacific Ocean, with a check-list of the non-marine Ostracoda of the Pacific Islands. Bull. Soc. Nat. Luxemb. 108:89–103. Google Scholar

  74. P. Minchin 1987. An evaluation of the relative robustness of techniques for ecological ordination. Vegetatio 69:89–107. Google Scholar

  75. J. Muñoz , A. M. Felicísimo, F. Cabezas , A. R. Burgas , and I. Martínez . 2004. Wind as long-distance dispersal vehicle in the Southern Hemisphere. Science (Washington, D.C.) 304:1144–1147. Google Scholar

  76. D. L. Nielsen , M. A. Brock , G. N. Rees , and D. S. Baldwin . 2003. Effects of increasing salinity on freshwater ecosystems in Australia. Aust. J. Bot. 51:655–665. Google Scholar

  77. P. D. Nunn 1998. Pacific island landscapes. Institute of Pacific Studies, The University of the South Pacific, Suva, Fiji. Google Scholar

  78. P. D. Nunn 1999. Environmental change in the Pacific basin. John Wiley, Chichester. Google Scholar

  79. J. Oksanen, R. Kindt, P. Legendre, B. O'Hara, and M. H. H. Stevens. 2007. Vegan: Community ecology package. R version 1.8–8.  http://cran.r-project.org/http://r-forge.r-project.org/projects/veganGoogle Scholar

  80. V. E. Panov , P. I. Krylov , and N. Riccardi . 2004. Role of diapause in dispersal and invasion success by aquatic invertebrates. J. Limnol. 63:56–69. Google Scholar

  81. A. Parkes 1997. Environmental change and the impact of Polynesian colonization: Sedimentary records from central Polynesia. Pages 166–199 in P. V. Kirch and T. L. Hunt, eds. Historical ecology in the Pacific Islands. Yale University Press, New Haven, Conneticut. Google Scholar

  82. J. W. Reid 1997. How “cosmopolitan” are the continental cyclopoid copepods? Comparison of the North American and Eurasian faunas, with description of Acanthocyclops parasensitivus sp. n. (Copepoda: Cyclopoida) from the U.S.A. Zool. Anz. 236:109–118. Google Scholar

  83. C. Robin , and M. Monzier . 1995. Risque volcanique à Vanuatu. ORSTOM, Port-Vila, Vanuatu. Notes Tech. Sci. Terre Géophys. Noumea, ORSTOM 6:1–16. Google Scholar

  84. B. Rolett , and J. Diamond . 2004. Environmental predictors of pre-European deforestation on Pacific islands. Nature (Lond.) 431:443–446. Google Scholar

  85. E. Rott , E. I. L. Suva , E. Enriquez , and S. Ingthamjitr . 2008. Phytoplankton community structure with special reference to species diversity in five tropical Asian water bodies. Pages 81–120. In F. Schiemer, D. Simon, U. Amarasinghe, and J. Moreau, eds. Aquatic ecosystems and development: Comparative Asian perspectives. Margraf & Backhuys Publishers, Weikersheim. Google Scholar

  86. M. J. Santos-Wisniewski, O. Rocha, and T. Matsumura-Tundisi. 2001. First record of Alona setigera Brehm (Cladocera, Chydoridae) in the Neotropical region. Braz. J. Biol. 61 (4): 701–702. Google Scholar

  87. G. O. Sars 1904. Pazifische PlanktonCrustaceen. Zool. Jahrb. Abt. Syst. Oekol. Geogr. Tiere 19:629–646. Google Scholar

  88. R. Schabetsberger , G. Drozdowski, I. Drozdowski , C. D. Jersabek , and E. Rott . 2004. Limnological aspects of two tropical crater lakes (Lago Biao and Lago Loreto) on the island of Bioko (Equatorial Guinea). Hydrobiologia 524:79–90. Google Scholar

  89. M. Schallenberg , C. J. Hall , and C. W. Burns . 2003. Consequences of climateinduced salinity increases on zooplankton abundance and diversity in coastal lakes. Mar. Ecol. Prog. Ser. 251:181–189. Google Scholar

  90. H. Schatz , and V. M. Behan-Pelletier . 2008. Global diversity of oribatids (Oribatida; Acari-Arachnida). Pages 323–328 in E. V. Balian, C. Lévêque, H. Segers, and K. Martens , eds. Freshwater animal diversity assessment. Hydrobiologia 595. Google Scholar

  91. M. S. Scheffer , J. Carpenter, C. Foley , B. Folkes , and B. Walker . 2001. Catastrophic shifts in ecosytems. Nature (Lond.) 413:591–596. Google Scholar

  92. D. W. Schindler , and B. R. Parker . 2002. Biological pollutants: Alien fishes in mountain lakes. Water Air Soil Pollut. Focus 2:379–397. Google Scholar

  93. C. Schuster , A. Whistler , and T. S. Tuailemafua . 1996. The conservation of biological diversity in upland ecosystems of Samoa. Division of Environment and Conservation of the Department of Lands, Surveys and Environment. Government of Samoa, Apia. Google Scholar

  94. D. A. Scott , ed. 1993. A directory of wetlands in Oceania. The International Waterfowl and Wetlands Bureau (IWRB), Slimbridge, U.K., and Asian Wetlands Bureau (AWB), Kuala Lumpur, Malaysia. Google Scholar

  95. H. Segers 1990. Contribution to the knowledge of the rotifer fauna of the Galapagos Islands. Biol. Jaarb. Dodonaea 58:113–119. Google Scholar

  96. H. Segers , and S. Babu . 1999. Rotifera from a high-altitude lake in southern India, with a note on the taxonomy of Polyarthra Ehrenberg, 1834. Hydrobiologia 405:89–93. Google Scholar

  97. H. Segers, and H. J. Dumont. 1993. Zoogeography of Pacific Ocean islands: A comparison of the rotifer faunas of Easter Island and the Galapagos Islands. Hydrobiologia 255/256:475–480. Google Scholar

  98. H. G. Sengbusch 1957. A new species of oribatoid mites from Guam with a key to the species of Nasozetes Sellnick 1930 (Acarina, Oribatei). J. Parasitol. 43:93–96. Google Scholar

  99. A. R. Sherwood 2004. Biological checklist of the nonmarine algae of the Hawaiian Islands. Records of the Hawai‘i Biological Survey. Bishop Mus. Occas. Pap. 80:1–26. Google Scholar

  100. N. N. Smirnov 1971. Chydoridae of the world's fauna. Fauna SSSR. Rakoobraznie 1 (2): 1–531. Leningrad. [In Russian.] Google Scholar

  101. W. Southern 1986. The late Quaternary environmental history of Fiji. Ph.D. diss., Australian National University, Canberra. Google Scholar

  102. W. Southern , J. Ash , J. Brodie , and P. Ryan . 1986. The flora, fauna and water chemistry of Tagimaucia crater, a tropical highland lake and swamp in Fiji. Freshwater Biol. 16:509–520. Google Scholar

  103. T. Stingelin 1905. Untersuchungen uber die Cladoceren Fauna von Hinterindien, Sumatra und Java, nebst einem Beitrag zur Cladoceren-Kenntnis der Hawaii-Inseln. Zool. Jahrb. Abt. Syst. Oekol. Geogr. Tiere 21:327–367. Google Scholar

  104. D. W. Stinson , M. W. Ritter , and J. D. Reichel . 1991. The Mariana common moorhen: Decline in an island endemic. Condor 93:38–43. Google Scholar

  105. B. V. Timms 1985. The Cladocera (Crustacea) of New Caledonia. Proc. Linn. Soc. N.S.W. 108:47–57. Google Scholar

  106. B. Vanschoenwinkel, S. Gielen, M. Seaman, and L. Brendonck. 2008. Any way the wind blows: Frequent wind dispersal drives species sorting in ephemeral aquatic communities. Oikos 117:125–134. Google Scholar

  107. M. T. Vinciguerra 2006. Dorylaimida, Part II: Superfamily Dorylaimoidea. Pages 392–467 in Abebe Eyualem, W. Traunspurger, and I. Andrássy, eds. Freshwater nematodes: Ecology and taxonomy. CABI Publishing, Wallingford, U.K. Google Scholar

  108. W. Vyverman 1996. The Indo-Malaysian North-Australian phycogeographic region revised. Pages 107–120 in J. Kristiansen , ed. Biogeography of freshwater algae. Dev. Hydrobiol. 118/Hydrobiologia 336. Google Scholar

  109. R. T. Watson , M. C. Zinyowera , and R. H. Moss . 1998. The regional impacts of climate change. Cambridge University Press, Cambridge, U.K. Google Scholar

  110. I. White , T. Falkland, T. Metutera, E. Metai, M. Overmars , P. Perez , and A. Dray . 2007. Climatic and human influences on groundwater in low atolls. Vadose Zone J. 6:581–590. Google Scholar

  111. R. J. Whittaker 1998. Island biogeography. Oxford University Press, Oxford, U.K. Google Scholar

  112. S. Wood 2003. Thin-plate regression splines. J. R. Stat. Soc. Ser. B 65:95–114. Google Scholar

  113. H. C. Yeatman 1983. Copepods from microhabitats in Fiji, Western Samoa, and Tonga. Micronesica 19:57–90. Google Scholar

Notes

[1] Manuscript accepted 20 May 2008.

Appendices

Appendix

Appendix

Freshwater Algae, Nematoda, Rotifera, Crustacea, and Oribatida Found in South Pacific Freshwater Ecosystems, Their Occurrence in the 39 Investigated Freshwater Ecosystems and Their Known Distribution

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© 2009 by University of Hawai‘i Press
Robert Schabetsberger, Gabriele Drozdowski, Eugen Rott, Rupert Lenzenweger, Christian D. Jersabek, Frank Fiers, Walter Traunspurger, Nicola Reiff, Fabio Stoch, Alexey A. Kotov, Koen Martens, Heinrich Schatz, and Roland Kaiser "Losing the Bounty? Investigating Species Richness in Isolated Freshwater Ecosystems of Oceania," Pacific Science 63(2), (1 April 2009). https://doi.org/10.2984/049.063.0201
Published: 1 April 2009
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