Next Article in Journal
A Case Study of Whistle Detection and Localization for Humpback Dolphins in Taiwan
Next Article in Special Issue
Age, Growth and Otolith Microstructure of the Spotted Lanternfish Myctophum punctatum Rafinesque 1810
Previous Article in Journal
Safety Barrier Management: Risk-Based Approach for the Oil and Gas Sector
Previous Article in Special Issue
Deep-Water Cartilaginous Fishes in the Central Mediterranean Sea: Comparison between Geographic Areas with Two Low Impact Tools for Sampling
 
 
Search for Articles:
Title / Keyword
Author / Affiliation / Email
Journal
Article Type
 
 
Advanced Search
 
Section
Special Issue
Volume
Issue
Number
Page
 
Journals
JMSE
Volume 9
Issue 7
10.3390/jmse9070723
jmse-logo
Submit to this Journal Review for this Journal Propose a Special Issue
► Article Menu

Article Menu

share Share announcement Help format_quote Cite question_answer Discuss in SciProfiles thumb_up
...
Endorse textsms
...
Comment
first_page
settings
Order Article Reprints
Font Type:
Arial Georgia Verdana
Font Size:
Aa Aa Aa
Line Spacing:
Column Width:
Background:
Article

A Very Large Spawning Aggregation of a Deep-Sea Eel: Magnitude and Status

by
Alan Williams
1,*,
Deborah Osterhage
2,
Franziska Althaus
1,
Timothy Ryan
1,
Mark Green
1 and
John Pogonoski
1
1
CSIRO Oceans and Atmosphere, Marine Laboratories, Castray Esplanade, Hobart, TAS 7001, Australia
2
Institute for Marine and Antarctic Studies, University of Tasmania, Hobart, TAS 7001, Australia
*
Author to whom correspondence should be addressed.
J. Mar. Sci. Eng. 2021, 9(7), 723; https://doi.org/10.3390/jmse9070723
Submission received: 24 May 2021 / Revised: 10 June 2021 / Accepted: 21 June 2021 / Published: 30 June 2021
(This article belongs to the Special Issue Deepwater Fishes)
Browse Figures
Review Reports Versions Notes

Abstract

:
Multiple lines of evidence substantiate the existence of a very large aggregation of the basketwork eel, Diastobranchus capensis, on the small (3 km2) Patience Seamount off southeast Australia. The aggregation appears to be present year-round, but largest in the austral autumn when composed of spawning eels. Twenty eels caught in April 2015 (14 female, 6 male) were all in advanced stages of spawning condition. The eel’s abundance in the aggregation was very high as measured at seamount, local and regional scales. Hydroacoustic measurement of the spawning aggregation’s dimensions (~100 × 1000 m) and conservative counts of 100 s of eels along camera transects of ~1000–2000 m length indicate 10,000 s individual eels may have been present. The absence of other known spawning locations indicates the Patience Seamount is a regional-scale spatial anchor for spawning. The aggregation was protected in a marine park in 2007 following a decades-long impact from bottom trawling, indicating that the population can be expected to stabilise and recover. Monitoring the aggregation’s status, and validating seasonal spawning, provide important opportunities to examine conservation-led recovery in the deep sea as part of Australia’s new national strategy of Monitoring, Evaluation, Reporting and Improvement (MERI) for conservation values within marine parks.

1. Introduction

Over 1000 species of true eels frequent world oceans [1] from coastal waters to hadal depths [2], but little is known of the spawning ecology of eels. The most studied are the catadromous anguillid eels, known to migrate and spawn in the oceans. Approximate spawning locations, based largely on leptocephalus catches, have been estimated for all temperate and most tropical anguillid species, with the first described over 100 years ago [3]. Intensive search efforts over the last two decades using increasingly sophisticated technology have resulted in better information for spawning locations, including capture of some mature adult eels, but have not revealed any direct observations of spawning aggregations [3,4,5]. Marine eels are believed to have a number of spawning strategies indicated by leptocephalus catch, namely long migrations to offshore spawning areas, short migrations to the shelf break or deep water near the continental shelf, or no migration [6]. There are few reported instances of marine eel spawning, and most are inshore including observations of spawning moray and garden eels [7,8,9], and a suggested spawning aggregation based on increased catch of mature conger eels within a harbour [10]. Aggregations of marine eels are also rarely reported: ophichthid eels have been seen aggregating offshore at the sea surface (n ≥ 62), but not spawning [11,12], and there have been two observations of synaphobranchid eel aggregations on seamounts, both associated with hydrothermal vents, namely Dysommina rugosa (unquantified) [13]; and Maedia abyssalis (n = 30–40) [14]. The latter was speculated to be a spawning aggregation because the eels’ skin condition resembled that of Anguilla eels that had been experimentally induced to spawn. Eels are also known to be attracted in numbers to baited cameras, with the most significant being the synaphobranchis eel Ilyophis arx on an abyssal seamount (max N = 115) [15]. To date, however, there have been no observations of confirmed spawning aggregations.
In this article, we provide evidence for an oceanic spawning aggregation of the basketwork eel Diastobranchus capensis (Synaphobranchidae), a large-bodied, deep-sea eel found in mid-continental slope (~700 to ~2000 m depths). The species has a very broad distribution, bounded in the south by the Antarctic Convergence [16,17], and extending into the North West Atlantic [18], and Arctic [19]. However, its core distribution is Southern Hemisphere where it is near circum-austral, and most abundant off temperate Australia and around New Zealand, including on seamounts [20,21].
Little is known of the ecology and biology of D. capensis despite it being a dominant mid-slope species. The species occurs frequently at low densities in scientific and commercial bottom trawl catches [20,22,23] and lone individuals are often observed by towed cameras (authors’ observations). Most ecological studies have focussed on its trophic status: the eel is predominantly a piscivore [24], although wider, predominantly mesopelagic, prey ranges are also reported [25,26], and a facultative scavenger [27]; it can also be attracted to baited videos where it has been seen in groups of up to 11 [28]. Specific knowledge of its reproductive ecology is virtually non-existent. Only one gravid specimen had been previously reported [29,30] but no details of the gonad and leptocephalus have been specifically described.
Using opportunistically collected samples from three surveys, our overall objective was to characterize a biological aggregation on Patience Seamount south of Tasmania, Australia which was anecdotally reported as being composed of the deep-sea eel, Diastobranchus capensis. Specifically, we aimed to: (1) map and characterize the aggregation and identify its composition using photographic imagery, net catches and hydro-acoustics; (2) if substantiated as an aggregation of D. capensis, establish its uniqueness by comparing the species’ abundance on adjacent seamounts and with fishery catch data from its core range in Australia and New Zealand; and (3) investigate the aggregation as a spawning aggregation based on reproductive data of D. capensis collected within the aggregation, and infer its seasonality based on data taken at two times during the year (March/April and December). Finally, we discuss the aggregation in terms of its ecological value—from the standpoints of its ecological role, and its recovery from fishing impacts following protection within the ‘Huon’ Australian Marine Park [31]. We make recommendations for future monitoring of the aggregation in the context of management planning for the marine park.

2. Materials and Methods

2.1. Field Sampling

Samples and data from the eel aggregation were collected opportunistically during three surveys that aimed primarily to map the seabed and associated benthic biodiversity on the continental slope off southern Tasmania (Figure 1) in an area containing a cluster of small volcanic seamounts see [32]: survey #1 in March/April 2007 (RV Southern Surveyor, SS200702); #2 in April 2015 (RV Investigator IN2015_E02; and #3 in November/December 2018 (RV Investigator IN2018_V06). A deep-water towed camera platform [33] was used on all surveys to acquire imagery that permitted the relative abundance and density of D. Capensis and co-occurring fishes to be estimated on 10 other adjacent seamounts (Table 1). Real-time video feed through a fibre-optic cable enabled the camera to be maintained at a consistent height (2 to 4 m) off the seabed where it provided continuous stereo-video and regular (5 s interval) high-resolution still images from cameras with an oblique field of view (~5 m wide by 5.5 m depth of field). The camera’s geo-location was estimated to an accuracy within 20 m by cross-referencing the GPS location of the ship with an ultra-short baseline (USBL) tracking beacon mounted on the camera platform; further details are given in [32]. Specimens of D. capensis were captured by a small (4 m wide) beam trawl [34] during survey #2 and with a baited-hook and line on survey #3.

2.2. Acoustic Mapping of the Aggregation at Patience Seamount

The ‘Patience Seamount’ is a small (3 sq km base area) extinct volcano, which was mapped for the first time during survey #1 using a 30 KHz Simrad EM300 multibeam echosounder. This seamount lies at the shallow margin of a cluster of similarly conical-shaped and mostly small (1 to 10, max 25 sq km base area) seamounts, all of which intersect the depth range occupied by D. capensis (approximately 700–2000 m) (Figure 1b). During survey #2, two sets of ‘star-pattern’ transects were made with a calibrated EK60 single beam echosounder at 18 and 38 KHz frequencies during the daytime: set #1 on the 10 April 2015 at 21:53 UTC (07:53 local) and set #2 at 04:17 UTC (14:07 local) to identify the extent and dynamics of the eel aggregation. Additional echosoundings were collected on 12 April during photographic transects. Technical problems lead to the loss of raw acoustic data on 10 April, but images of the real-time display of the Simrad EK60 38 kHz echosounder taken from the Simrad ER60 acquisition software (version 2.4.3, accessed on 5 June 2021) were available.

2.3. Estimating Fish Abundance

We scored the abundance of fishes in two ways:
(1)
Density: counts of individual fishes above (overlapping) polygons of known area were made during Survey #1 [35] for D. capensis and other fishes: predominantly orange roughy (Hoplostethus atlanticus), combined Oreosomatidae (Allocyttus verucosus and Neocyttus rhomboidalis); squaliform sharks, and macrourids. Polygon areas were estimated by using the stereo configuration of the video to determine absolute areas of seafloor in the high-resolution still images. Surface areas in the 3-dimensional perspective of the oblique field of view were calculated from calibrated stereo imagery using Photomeasure software (SeaGIS-TM V3.15 & SeaGIS-EM V5.51, www.seagis.com.au/index.html, accessed on 5 June 2021). Polygons of known area were drawn in the images by identifying a series of common points in corresponding frames from the stereo video and the still images. These polygons encompassed an average area of 5.0 m2. Differences in mean density between seamounts used a 2-tailed t-test.
(2)
Relative abundance: counts of individual D. capensis in the field of view in non-overlapping video-frames (5 s intervals) to provide an along-transect estimate of the total number of individuals. This provided a conservative sum of individuals because eels were not counted in the gaps between images. For survey #3, the video was viewed at half-speed and all eels in the field of view were counted. The observed number of eels was standardised to individuals per h of video tow.

2.4. Reproductive Biology and Swimbladder of Diastobranchus capensis

Most eels were dead when retrieved but a few moribund individuals were euthanized in a 100 mg/L Aqui-S solution until non-responsive. They were then weighed to the nearest gram and measured (total length, TL) to the nearest millimeter and dissected to examine (1) the size and structure of the swimbladder to relate to its acoustic reflectivity, and (2) the gonads to determine sex and numerically score the reproductive status. Gonads were removed and weighed to the nearest gram to calculate the GSI = gonad weight/total (non-eviscerated) fish weight. Ovaries were fixed in 10% formalin for fecundity estimates. Fecundity estimation was as follows: each ovary was drained through 300-micron nylon mesh and rinsed with freshwater, drained again and gently patted with absorbent towel to remove excess liquid. Preserved ovaries were weighed to nearest 0.1 g and subsampled (2 g tissue) in the anterior, posterior and middle sections. Subsamples were rinsed again in freshwater through 250-micron nylon mesh to remove as much formalin as possible and weighed to the nearest 0.1 g. Each subsample was placed separately into a circular (plankton) counting tray and individual eggs were teased away from integumental tissue and counted; the diameter of 10 oocytes from each subsample was measured using an ocular micrometer on a dissecting microscope to an accuracy of 0.1 mm. The data were scaled up to total egg count per ovary (=estimated fecundity) after confirming that counts from the three sections of the ovaries were from the same statistical distribution using the non-parametric Kruskal-Wallis test. Eel bodies were examined for evidence of changes to dentition and skin degradation associated with spawning. A linear regression was used to test for correlation between GSI and fish length.

3. Results

3.1. Abundance of Diastobranchus capensis

Numerous D. capensis were observed in the camera tows on Patience Seamount during each of the three surveys in 2007, 2015 and 2018 (surveys #1 to #3, respectively). More than 25 individual eels were observed in individual images during surveys #1 and #2 (e.g., Figure 2a), and as many as 13 D. capensis individuals counted over a single image polygon during survey #1. The relative abundance of D. capensis along the three camera-transects made in surveys #1 and 2 (March/April) (Figure 3) was very high: standardised counts (eels per h of camera tow) were 278, 362, 162 (mean = 267); counts were lower (17, 123; mean = 70) along two transects made during survey #3 (December) (Figure 3). The total (unstandardised) counts of eels per transect were 763, 931, 475, 59, 167 (order as above); the counts at 5-sec intervals are mapped along the transects to provide spatial context (Figure 3). Within the combined depth range surveyed (755 to 1432 m) across all three surveys at Patience Seamount, the complete distributional depth range of D. capensis was ~900 to 1250 m, but the great majority (>95%) were observed in ~1000 to 1200 m depths (Figure 4). Both our measures of abundance are conservative because the still images and video frames in which eels were counted do not overlap, i.e., there are gaps between them.
The numbers of D. capensis observed on Patience Seamount were relatively very high compared to 10 other adjacent seamounts (Figure 1b). When measured during survey #2, the mean D. capensis density was 0.26 individuals m−2 (+/− 0.038 SE) (Figure 5a) and statistically highly significantly different between seamounts (F = 41.369, df 10,1740, p < 0.001). The relative abundance of D. capensis was also relatively high during survey #3 (Figure 5b), and similarly to surveys #1 and #2, only lone D. capensis were seen on the other seamounts. The density of D. capensis on Patience Seamount during survey #2 was more than double the density of all other fishes combined on that seamount and any of the other nine adjacent seamounts surveyed (Figure 5a).

3.2. Reproductive and Swimbladder Characteristics of Diastobranchus capensis

A total of 20 adult D. capensis specimens were captured in three beam trawl samples during survey #2 in April 2015 (18 in a single sample at 1087 m depth within the Patience Seamount aggregation, and two on the adjacent slope at 1070 m and 1060 m depth) comprised 14 females (782–1204 mm TL and 632–2296 g weight) and six males (653–780 mm TL and 338–588 g). Two other adult females were caught from Patience Seamount by hook and line during survey #3 in December 2018 at ~1019 m. All 20 individuals from 2015 had gonads in an advanced stage of spawning condition (Figure 6) and empty stomachs; in contrast, both females caught in 2018 were in a non-spawning condition. The gonads of gravid females and males had a multi-lobed structure and were very large relative to body size—extending along the entire length of the body cavity (Figure 6). The ovary walls were transparent, and oocytes were clearly seen with the naked eye, but the oocytes were not free and did not flow freely from the cloaca. The testes were firm and white; milt flowed freely from the cloaca when gentle pressure was applied to the body cavity. Fresh ovary weight ranged from 149–537 g, and testes from 28–138 g. The GSI ranged between 17.4 and 25.8 in females, and 6.8 to 24.8 in males; there was no significant correlation between GSI and eel length (R2 = 0.10). Individual fecundity in the mature females, estimated from egg counts in subsamples taken from the anterior, mid- and posterior regions of ovaries from each of five individuals that represented the overall eel size range, ranged from 73,339 to 235,061, with the number of eggs increasing linearly with increasing fish length (R2 = 0.92). The average egg diameter (n = 10) was consistent within and between gonads at 0.9 to 1.0 mm. The mean (n = 15) was 469 eggs per gram (range = 409 to 538; SE = 10.47). There was no significant difference between location of the tissue collection within the ovaries, despite some considerable variation in the counts (Kruskal-Wallis p = 0.65).
All eels observed (spawners, and non-spawners in and away from the aggregation) were generally slow moving and did not show distinct flight response away from the camera unless they came very close to it. We observed no particular indications of spawning behaviour (such as tight grouping or egg shedding) by spawning eels, and there were no external signs of spawning condition such as skin degradation or changes to dentition; scraping and other damage to skin was consistent with net capture (Figure 6).
Dissection of D. capensis revealed it possesses an exceptionally long gas-filled swimbladder (approximately 2/3 of its body length) (Figure 7). The swimbladder has a relatively wide anterior bulb that tapers over the length of the posterior tube.

3.3. Characteristics and Composition of Acoustic Marks at Patience Seamount

During survey #2, echo-soundings at both 38 and 18 kHz identified strong, extensive, and persistent ‘acoustic marks’ encircling the flanks and base of the Patience Seamount, consistent with the presence of a feature-associated fish aggregation 1000 to 1250 m depths. Echo-soundings made down the south-east side of the seamount during video tow 024, Survey #2 on April 12 (Figure 8a) showed only low signal backscatter of biological origin instead of expected high backscatter consistent with the high numbers of D. capensis observed during this tow; this was attributed to the mismatch between the camera observation < 10 m above seafloor and a high acoustic dead-zone ~100 m above seafloor (Figure 8a). A much larger and stronger aggregation was observed later on 12 April on the north-west flank of the seamount (when raw acoustic data were recorded successfully) (Figure 8b). This aggregation was within the expected depth range of D. capensis, and approximately 100 m high long 1000 m, extending away from the seafloor and above the dead-zone region. Images from the star-pattern transects showed the aggregation consistently associated with the Patience Seamount in the depth range of approximately 1000 to 1250 m (Figure 9).
Camera observations confirmed that D. capensis was highly dominant (Figure 2) over the total depth range surveyed (755–1432 m), with the great majority of individuals seen in 1050 to 1200 m depths on the flank and base of Patience Seamount corresponding to the depth of the acoustic marks (Figure 4). Other fishes were photographed on Patience Seamount, and collectively made up 29% of total observations (Figure 5). However, only two taxa occurred at relatively high abundance: orange roughy and oreo dory (mostly juvenile Allocyttus verrucosus), both of which were scattered at low density in a similar depth range to D. capensis (Figure 4). A beam trawl tow targeted at the aggregation in 1087 m depths caught 20 D. capensis but no other fish species.

4. Discussion

4.1. Characteristics of the Aggregation of Diastobranchus capensis

Multiple lines of evidence substantiate our conclusion that there is a large aggregation of the basketwork eel, D. capensis, on Patience Seamount. Its existence was first detected by commercial fishers in the early 1990′s and was present, at varying magnitudes, during our three visits in 2007, 2015 and 2018—a span of some 25 years. Thus, it appears to be persistent through time, present year-round (based on observations in March, April and December), and much larger in the austral autumn (around April). All 20 eels captured during the 2015 austral autumn voyage were in an advanced stage of spawning, with some ‘running ripe’ indicating readiness for imminent spawning, and strongly indicating the large aggregation seen at that time was for spawning purposes. In addition, all 20 had empty stomachs which indicated this was not a feeding aggregation, whereas the two eels caught from the smaller aggregation in December 2018 using baited long line were both feeding and in non-spawning condition.
The abundance of the eel in the aggregation was very high as measured at seamount, local and regional scales. Thus, the mean D. capensis density (0.26 individuals per m2) in the spawning aggregation (April 2015) was 40 to 185 times greater than its density at the other adjacent seamounts where it was present, and 2 to 15 times greater than the combined density of all fish species at any other adjacent seamount (Figure 5). Our examination of research and commercial catch records validated by sea-going observers for D. capensis throughout its range (collectively ~2500 trawl operations from North Atlantic, Chile, New Caledonia, New Zealand and southeastern Australia [21,36,37] showed most recorded catch rates were very low (>90% were <20 kg/nm, or 0.5 gm−2) but that that there were two exceptional catches. These were 286 kg/nm (7.72 gm−2) from the continental slope immediately adjacent to the Patience Seamount, and the largest of 476 kg/nm (12.85 gm−2) taken in September 2000 on the ‘Smith City’ Seamount on the Chatham Rise off New Zealand [data in 21]. The species’ wide range (Antarctic Convergence to Arctic) and frequent occurrence in its core distribution, e.g., 85 and 90% of all trawls examined, respectively off New Zealand and Australia [21], signals there are undoubtably other spawning sites. Clues to their general locations are given by museum records (author’s data) of two gravid females, one each from the Great Australian Bight and southwest Indian Ocean, and possibly by the large catch on Smith City Seamount—although no spawning fish were reported.
We are confident hydro-acoustics have provided a way of scaling the size and dynamics of the aggregation at Patience Seamount. Often caution is required when attributing acoustic marks detected by echosounder to particular species because a mix of species (fishes and invertebrates) with varying acoustic target strengths may be present [38]. Further, ground-truth sampling with cameras can also be problematic because individuals filmed close to the seabed may be in the acoustic ‘dead-zone’ and remain undetected by echo-sounding [39]. This ‘dead-zone’ is generated by the off-axis return acoustic backscatter signal from the seafloor arriving at the echosounder receiver earlier than biological signal from nadir and is further increased by ‘side-lobing’ on the steep flank of seamounts. Dead-zones may extend to as much as 100 m from the seabed when using a hull-mounted echosounder in steep deep-sea environments but can be reduced using acoustic systems deployed on towed platforms that reduce the range between echosounder and seafloor [40]. In our data, large numbers of D. capensis seen in camera transect 024, Survey #2 did not generate an intense acoustic mark as expected (Figure 8a), clearly indicating that the eels were in the acoustic dead-zone. Nonetheless, the strong marks seen around the Patience Seamount at various other times (e.g., Figure 8b) can be confidently predicted to be D. capensis due to (1) its expected very high echo intensity (target strength) relative to other co-occurring species, and (2) the lack of any other plausible target.
Attributing high echo intensity (TS) and the high backscatter regions seen at Patience Seamount to Diastobranchus capensis is corroborated by the morphology and size of its swimbladder. Fish TS is strongly correlated with the gas-water density contrast of the swimbladder and its cross-sectional area [41], with large and long gas-filled bladders producing high acoustic backscatter [42]. These two features are accentuated in D. capensis which is large-bodied and elongate (~1 m in length) and possesses an exceptionally long gas-filled swimbladder (approximately 2/3 of its body length) (Figure 7). Model estimates of TS for a 1 m long D. capensis using parameters provided in [38] give a tilt-averaged TS of −30.1 dB. This is a very high value relative to the TS of co-occurring species: oreos with a TS—one order of magnitude lower [38], and orange roughy with a TS—two orders of magnitude lower [43]. The high backscatter regions observed at Patience Seamount can only have been generated by either a species with an exceptionally high target strength, or by another species with lower target strength but relatively very high density. The latter is implausible because the only other relatively abundant and schooling benthopelagic fishes that co-occur on Patience and adjacent seamounts are orange roughy and, to a much lesser extent, the shallow oreo species (A. verrucosus and N. rhomboidalis). For these species to produce the high backscatter observed, their numeric densities would need to be numerically higher by factors of ~10 and ~100, respectively. There is no evidence of high densities of these species in camera tows, and no expectation of observing large aggregations of orange roughy outside their austral winter spawning period in June/July.
While it is not yet possible to precisely quantify the population size within the D. capensis aggregation at Patience Seamount, our observations show that (1) eel density is very high in areas around the main aggregation, with conservative counts of hundreds of eels along narrow camera transects (field-of-view ~5 × 5 m) of ~1 to 2 km in length, and (2) the main aggregation is of the order of 100 m high and >1 km in length (and unknown width) in echograms (Figure 8b). It is therefore both reasonable and conservative to estimate that tens of thousands of D. capensis comprised the spawning aggregation at the point in time when it was surveyed in April 2015. The total spawning population visiting the Patience Seamount may be much greater if there is an extended period of spawning and turn-over is accounted for. In any event, for D. capensis, a species that is widespread and common at typically very low density, the magnitude of this single substantiated aggregation strongly suggests high spawning-site fidelity and regional-scale catchment for spawning. This is substantiated off southeastern Australia where there is no other record of an eel aggregation from a decades-long documented commercial catch history, anecdotal reports from fishers, or many scientific surveys. Despite the duration of spawning, turn-over dynamics and fluctuations in year-round eel abundance all remaining unknown, our observations suggest that D. capensis migrate from large distances along the narrow mid-continental slope (e.g., several 100 s km around Tasmania alone) to the small Patience Seamount (base area of 3 km2) to spawn.
Although we have not attempted to quantitatively estimate total eel numbers in the aggregation using acoustics due to an unvalidated estimate of D. capensis TS (echo intensity) and dead-zone effects, it appears to be the largest observed natural aggregation of a deep-sea eel. Notwithstanding, any estimate would not be directly comparable to other reports of high eel density from bathyal and greater depths, e.g., [15], because none are of a spawning aggregation, and because most are made with baited cameras that attract fish then extrapolate fish density over broad areas using a variety of different metrics and methods (see review by [15]).

4.2. Ecological Status of the Diastobranchus capensis Aggregation

This population of D. capensis was exposed to impacts from a seamount-focused fishery around Tasmania over a period of some 30 years, starting around 1979. The species was caught as bycatch during the peak of the fishery between about 1985 and 2006 when some 47,000 bottom trawling operations reduced the target stock of orange roughy to ~10% of pre-fishing biomass [44,45], and over 600 trawls were made on the Patience Seamount [32]. Anecdotal (unrecorded) reports of eel bycatch on Patience Seamount, much of it from trawls targeted at acoustic marks mistaken as orange roughy, included individual catches of ‘many tonnes’ (i.e., many 1000′s of individual eels), and were the origin of the fishing industry moniker ‘Eel Hill’ (AW, unpublished data). Bottom trawling also had widespread impacts on seamount habitat, including at Patience Seamount where disintegration and removal of stony coral reefs resulted [32]. Total fishing mortality on D. capensis is unknown but was probably substantial; any estimate based on recorded bycatch would be a great underestimate.
Although the impacts of past fishing upon the eel population associated with Patience Seamount cannot be substantiated due to a lack of baseline data, it is likely to have had a negative effect. High vulnerability of many deep-sea species to exploitation is suggested to stem from a tendency to aggregate on seamounts, and by possessing life-history traits characteristics such as large body size, slow growth, late sexual maturation and low natural mortality that make them vulnerable to exploitation [46,47]. However, there is a continuum in these life-history characteristics among deep-sea fishes [48] and D. capensis appears to be ‘mid-range’ in many respects. Thus, while it is large-bodied (up to 1.8 m, and the largest synaphobranchid eel [17] and has low natural mortality (0.144 [49]), it has a maximum recorded age of 47 years and was not considered long-lived [49], and appears to be sexually mature by about 10 years old (our gravid individuals compared to the age-length curve of [49]). Nonetheless, significant declines of D. capensis have been documented in New Zealand waters where it is also an incidental catch in orange roughy and oreo fisheries, strongly implying that fishing can have a deleterious effect on this species [50]. In the North Altantic, significant fishing-related declines of the related basketwork eel Synaphobranchus kaupi were reported [51,52] and benefits to scavenging synaphobranchid eels from fishery discards were offset by mortality from bycatch [52]. The significance of such fishing-induced impacts may have implications both for D. capensis, and for surrounding ecosystems. Spawning location is the anchor of a fish’s spatial distribution and will affect the degree to which a species can respond to environmental variability by changing habitats [53]. This would indicate that high fidelity to a single small spawning seamount by a regional-scale population will confer a low ability to respond to varying environmental conditions whether caused naturally or human-induced. It is likely that D. capensis is an important component of deep-sea ecosystems given its role a carrion eater [27], and by providing a substantial supply of detrital material to the benthic community [54].
Since this exposure to fishing mortality and habitat alteration, Patience Seamount became part of the ‘Huon’ Australian Marine Park (AMP) in 2007 and is now off-limits to trawling. Our surveys in 2015 and 2018 (made after Patience Seamount was protected) show that the spawning aggregation of D. capensis was still large. We, therefore, hypothesise that the southeast Australian population of D. capensis is stabilising and in a phase of recovery.

4.3. Conservation Value and Recovery Monitoring

Australia is a global front-runner in marine conservation having established a large network of offshore Australian Marine Parks (AMP) since 2007 [31]. Network design recognised the significance of seamount biodiversity and is the primary conservation value of the Huon AMP that encloses most of the cluster of small seamounts containing Patience Seamount. Monitoring conservation values is a priority activity for managing the AMP network, and a national strategy of Monitoring, Evaluation, Reporting and Improvement (MERI) will be implemented soon [55]. The aggregation of D. capensis, undocumented when the Huon AMP was designed and declared, demonstrates the importance of small spatial-scale features and phenomena to this process. The aggregation is an important and tractable indicator for monitoring a biological response to protection because it is fixed in space, has a known temporal signal, and can be quantitatively and cost-effectively measured by acoustics with little further extractive sampling. The objectives for monitoring should include to fully validate its status as a spawning aggregation and reveal presently unknown aspects of its ecology. It is also an important performance indicator of management intervention because fish spawning aggregation sites are being impacted worldwide due to fishing [56]. Monitoring the status of the basketwork eel spawning aggregation at Patience Seamount provides an unprecedented opportunity to understand a conservation-led recovery in the deep sea.

Author Contributions

Conceptualization, A.W.; Data curation, J.P.; Formal analysis, D.O.; F.A. and T.R.; Methodology, A.W., T.R. and M.G.; Project administration, A.W.; Writing—original draft, A.W. and D.O.; Writing—review and editing, A.W., D.O., F.A., T.R., M.G. and J.P. All authors have read and agreed to the published version of the manuscript.

Funding

This research was funded primarily by CSIRO Oceans and Atmosphere. Survey #3 was funded, collectively, by the CSIRO Oceans and Atmosphere, Parks Australia and the Australian Government National Environmental Science Program (NESP), Marine Biodiversity Hub.

Institutional Review Board Statement

The study, including biological collecting, was conducted in accordance with the following permits: Animal Ethics Permit (2018-26); Commonwealth Waters Permit; Australian Marine Parks Permit; and Australian Fisheries Management Authority Permit.

Informed Consent Statement

Not applicable.

Data Availability Statement

Metadata for the data collected for this study is available through Marlin the CSIRO Oceans and Atmosphere metadata tool http://www.marlin.csiro.au/, accessed on 5 June 2021; for access to imagery and annotation data please contact the corresponding author.

Acknowledgments

We acknowledge the committees and staff of Australia’s Marine National Facility (MNF) for access to the research vessels RV Southern Surveyor and Investigator, and the captain and the crew of the vessel for their hard work in making the survey successful. We also thank the sea-going staff from the MNF and many colleagues from CSIRO Oceans and Atmosphere and Parks Australia whose support was vital to the field collection of data.

Conflicts of Interest

The authors declare no conflict of interest.

References

  1. Fricke, R.; Eschmeyer, W.N.; Fong, J.D. Eschmeyer’s Catalog of Fishes: Genera/Species by Family/Subfamily; California Academy of Sciences: San Francisco, CA, USA, 2021; Available online: http://researcharchive.calacademy.org/research/ichthyology/catalog/SpeciesByFamily.asp (accessed on 12 May 2021).
  2. Linley, T.D.; Gerringer, M.E.; Yancey, P.H.; Drazen, J.C.; Weinstock, C.L.; Jamieson, A.J. Fishes of the hadal zone including new species, in situ observations and depth records of Liparidae. Deep Sea Res. Part I Oceanogr. Res. Pap. 2016, 114, 99–110. [Google Scholar] [CrossRef] [Green Version]
  3. Righton, D.; Piper, A.; Aarestrup, K.; Amilhat, E.; Belpaire, C.; Casselman, J.; Castonguay, M.; Díaz, E.; Dörner, H.; Faliex, E.; et al. Important questions to progress science and sustainable management of anguillid eels. Fish Fish. 2021, 1–27. [Google Scholar] [CrossRef]
  4. Chow, S.; Kurogi, H.; Mochioka, N.; Yanagimoto, T. Massive spawning behavior of the triplespine deepwater cardinalfish Sphyraenops bairdianus Poey, 1861 observed on an offshore sea mount in the West Mariana Ridge. Environ. Biol. Fish. 2018, 101, 1701–1705. [Google Scholar] [CrossRef]
  5. Tsukamoto, K.; Chow, S.; Otake, T.; Kurogi, H.; Mochioka, N.; Miller, M.J.; Aoyama, J.; Kimura, S.; Watanabe, S.; Yoshinaga, T.; et al. Oceanic spawning ecology of freshwater eels in the western North Pacific. Nat. Commun. 2011, 2, 179. [Google Scholar] [CrossRef] [Green Version]
  6. Miller, M.J. Contrasting migratory strategies of marine and freshwater eels. Fish. Sci. 2002, 68, 37–40. [Google Scholar] [CrossRef] [Green Version]
  7. Ferraris, C.J., Jr. Redescription and Spawning Behavior of the Muraenid eel Gymnothorax herrei. Copeia. 1985, 2, 518–520. [Google Scholar] [CrossRef]
  8. Fricke, H.W. Ökologische und verhaltensbiologische Beobachtungen an den Rohrenaalen Gorgasia sillneri und Taenioconger hassi (Pisces, Apodes, Heterocongridae); Max-Planck-Institut für Verhaltensphysiologie, Seewiesen und Erling-Andechs: Munich, Germany, 1970; pp. 1076–1099. [Google Scholar]
  9. Moyer, J.T.; Zaiser, M.J. Reproductive Behavior of Moray Eels at Miyake-jima, Japan. Jpn. J. Ichthyol. 1982, 28, 466–468. [Google Scholar]
  10. Castle, P.H.J. Synaphobranch eels from the Southern Ocean. Deep Sea Res. 1968, 15, 393–396. [Google Scholar] [CrossRef]
  11. Cohen, D.M.; Dean, D. Sexual maturity and migratory behaviour of the tropical eel, Ahlia egmotis. Nature 1970, 227, 189–190. [Google Scholar] [CrossRef]
  12. Ross, S.W.; Rohde, F.C. Colections of Ophichthid eels on the surface at night off North Carolina. Bull. Mar. Sci. 2003, 72, 241–246. [Google Scholar]
  13. Staudigel, H.; Hart, S.T.; Pile, A.; Bailey, B.E.; Baker, E.T.; Brooke, S.; Connelly, D.P.; Haucke, L.; German, C.R.; Hudson, I.; et al. Vailulu’u Seamount, Samoa: Life and death on an active submarine volcano. Proc. Natl. Acad. Sci. USA 2006, 103, 6448–6453. [Google Scholar] [CrossRef] [Green Version]
  14. Fujikura, K.; Tsuchida, S.; Ueno, H.; Ishibashi, J.; Gaze, W.; Maki, Y. Investigation of the deep-sea chemosynthetic ecosystem and submarine volcano at the Kasuga 2 and 3 seamounts in the Northern Mariana Trough, Western Pacific. JAMSTEC J. Deep Sea Res. 1998, 14, 127–138. [Google Scholar]
  15. Leitner, A.B.; Durden, J.M.; Smith, C.R.; Klingberg, E.D.; Drazen, J.C. Synaphobranchid eel swarms on abyssal seamounts: Largest aggregation of fishes ever observed at abyssal depths. Deep Sea Res. Part I 2021, 167, 103423. [Google Scholar] [CrossRef]
  16. Castle, P.H.J. Leptocephali of the Nemichthyidae, Serrivomeridae, Synaphobranchidae and Nettastmidae in Australasian waters. Trans. R. Soc. N. Z. Zool. 1965, 5, 131–146. [Google Scholar]
  17. Sulak, K.J.; Shcherbachev, Y.N. Zoogeography and systematics of six deep-living genera of Synaphobranchid eels, with a key to taxa and description of two new species of Ilyophis. Bull. Mar. Sci. 1997, 60, 1158–1194. [Google Scholar]
  18. Moore, J.A.; Vecchione, M.; Collette, B.B.; Gibbons, R.; Hartel, K.E. Selected fauna of Bear Seamount (New England Seamount chain), and the presence of “natural invader” species. Arch. Fish. Mar. Res. 2004, 51, 241–250. [Google Scholar]
  19. Svendsen, F.M.; Langhelle, G.; Byrkjedal, I. First record of a synaphobranchid eel in the Arctic: Diastobranchus capensis caught near Spitsbergen. Cybium 2011, 35, 255–256. [Google Scholar]
  20. Tracey, D.M.; Bull, B.; Clark, M.R.; MaCkay, K.A. Fish species composition on seamounts and adjacent slope in New Zealand waters. N. Z. J. Mar. Freshw. Res. 2004, 38, 163–182. [Google Scholar] [CrossRef]
  21. Clark, M.R.; Althaus, F.; Williams, A.; Niklitschek, E.; Menezes, G.M.; Hareide, N.-R.; Sutton, P.; O’Donnell, C. Are deep-sea demersal fish assemblages globally homogenous? Insights from seamounts. Mar. Ecology. 2010, 31, 39–51. [Google Scholar] [CrossRef]
  22. Zintzen, V.; Anderson, M.J.; Roberts, C.D.; Harvey, E.S.; Stewart, A.L.; Struthers, C.D. Diversity and composition of demersal fishes along a depth gradient assessed by baited remote underwater stereo-video. PLoS ONE 2012, 7, e48522. [Google Scholar] [CrossRef] [Green Version]
  23. Koslow, J.A.; Bulman, C.M.; Lyle, J.M. The mid-slope demersal fish community off southeastern Australia. Deep Sea Res. I 1994, 41, 113–141. [Google Scholar] [CrossRef]
  24. Bulman, C.M.; He, X.; Koslow, J.A. Trophic ecology of the mid-slope demersal fish community off southern Tasmania, Australia. Mar. Freshw. Res. 2002, 53, 59–72. [Google Scholar] [CrossRef]
  25. Anderson, M.E. Food habits of some deep-sea fish off South Africa’s west coast. 2. Eels and spiny eels (Anguilliformes and Notacanthiformes). Afr. J. Mar. Sci. 2005, 27, 557–566. [Google Scholar] [CrossRef]
  26. Clark, M.R.; Anderson, O.F.; Francis, R.I.C.C.; Tracey, D.M. The effects of commercial exploitation on orange roughy (Hoplestethus atlanticus) from the continental slope of the Chatham Rise, New Zealand, from 1979 to 1997. Fish. Res. 2000, 45, 217–238. [Google Scholar] [CrossRef]
  27. Jones, M.R.L.; Breen, B.B. Role of scavenging in a synaphobranchid eel (Diastobranchus capensis, Barnard, 1923), from northeastern Chatham Rise, New Zealand. Deep Sea Res. I 2014, 85, 118–123. [Google Scholar] [CrossRef]
  28. Zintzen, V.; Roberts, C.D.; Clark, M.R.; Williams, A.; Althaus, F.; Last, P.R. Composition, distribution and regional affinities of the deepwater ichthyofauna of the Lord Howe Rise and Norfolk Ridge, south-west Pacific Ocean. Deep Sea Res Part II Top. Stud. Oceanogr. 2011, 58, 933–947. [Google Scholar] [CrossRef]
  29. Whitley, G.P. Some noteworthy fishes from eastern Australia. Proc. R. Zool. Soc. N. S. W. 1950, 27–32. [Google Scholar]
  30. Olsen, A. New fish records and notes on some uncommon Tasmanian species. Pap. Proc. R. Soc. Tasman. 1958, 92, 155–159. Available online: https://eprints.utas.edu.au/14369/ (accessed on 5 June 2021).
  31. Australian Marine Parks Huon Marine Park. 2021. Available online: https://parksaustralia.gov.au/marine/parks (accessed on 5 June 2021).
  32. Williams, A.; Althaus, F.; Maguire, K.; Green, M.; Untiedt, C.; Alderslade, P.; Clark, M.R.; Bax, N.; Schlacher, T.A. The Fate of Deep-Sea Coral Reefs on Seamounts in a Fishery-Seascape: What Are the Impacts, What Remains, and What Is Protected? Front. Mar. Sci. 2020, 7. [Google Scholar] [CrossRef]
  33. Marouchos, A.; Sherlock, M.; Filisetti, A.; Williams, A. Underwater imaging on self-contained tethered systems. In Proceedings of the IEEE Oceans, Anchorage, AK, USA, 18–21 September 2017; Volume 5. [Google Scholar]
  34. Lewis, M. The CSIRO 4m Beam Trawl; CSIRO Marine and Atmospheric Research Paper 033; CSIRO Marine and Atmospheric Research: Hobart, Australia, 2010; 17p. [Google Scholar]
  35. Shortis, M.R.; Seager, J.W.; Williams, A.; Barker, B.A.; Sherlock, M. Using Stereo-Video for Deep Water Benthic Habitat Surveys. Mar. Technol. Soc. J. 2008, 42, 28–37. [Google Scholar] [CrossRef] [Green Version]
  36. Bulman, C.; Wayte, S.E.; Elliott, N. Orange Roughy Surveys, 1988 and 1989 Part A Abundance Indices Part B Biological Data; CSIRO Marine Laboratories: Hobart, Australia, 1994; 40p, Available online: http://www.cmar.csiro.au/e-print/open/CMReport_215.pdf (accessed on 5 June 2021).
  37. AFMA Observer Data. Data Collected through the Australian Fisheries Management Authority Observer Program. 2021. Available online: https://www.afma.gov.au/monitoring-enforcement/observer-program (accessed on 5 June 2021).
  38. McClatchie, S.; Coombs, R. Low target strength fish in mixed species assemblages: The case of orange roughy. Fish. Res. 2005, 72, 185–192. [Google Scholar] [CrossRef]
  39. Ona, E.; Mitson, R.B. Acoustic sampling and signal processing near the seabed: The deadzone revisited. ICES J. Mar Sci. 1996, 53, 677–690. [Google Scholar] [CrossRef]
  40. Kloser, R.J. Improved precision of acoustic surveys of benthopelagic fish by means of a deep-towed transducer. ICES J. Mar. Sci. 1996, 53, 407–413. [Google Scholar] [CrossRef]
  41. Foote, K.G.; Knudsen, H.P.; Vestnes, G.; McLennan, D.N.; Simmonds, E.J. Calibration of Acoustic Instruments for Fish Density Estimation: A Practical Guide; Cooperative Research Report No.144; Marine Laboratory: Aberdeen, UK, 1987; 72p, Available online: http://courses.washington.edu/fish538/resources/CRR%20144%20acoustic%20calibration.pdf (accessed on 5 June 2021).
  42. Hazen, E.L.; Horne, J.K.A. method for evaluating the effects of biological factors on fish target strength. ICES J. Mar. Sci. 2003, 60, 555–562. [Google Scholar] [CrossRef]
  43. Kloser, R.J.; Macaulay, G.; Ryan, T.E.; Lewis, M. Identification and target strength of orange roughy (Hopletethus atlanticus) measured in situ. J. Acoust. Soc. Am. 2013, 134, 97–108. [Google Scholar] [CrossRef] [Green Version]
  44. Clark, M.R. Deep sea seamount fisheries: A review of global status and future prospects. Lat. Am. J. Aquat. Res. 2009, 37, 501–512. [Google Scholar] [CrossRef]
  45. Upston, J.; Punt, A.E.; Wayte, S.; Ryan, T.; Day, J.; Sporcic, M. Orange Roughy (Hoplostethus atlanticus) Eastern Zone Stock Assessment Incorporating Data Up to 2014; CSIRO Oceans and Atmosphere—Australian Fisheries Management Authority: Hobart, Australia, 2014. [Google Scholar]
  46. Morato, T.; Cheung, W.W.L.; Pitcher, T.J. Vulnerability of seamount fish to fishing: Fuzzy analysis of life-history attributes. J. Fish Biol. 2006, 68, 209–221. [Google Scholar] [CrossRef]
  47. Cheung, W.W.L.; Watson, R.; Morato, T.; Pitcher, T.J.; Pauly, D. Intrinsic vulnerability in the global fish catch. Mar. Ecol. Prog. Ser. 2007, 333, 1–12. [Google Scholar] [CrossRef] [Green Version]
  48. Drazen, J.C.; Haedrich, R.L. A continuum of life histories in deep-sea demersal fishes. Deep Sea Res. Part I. 2012, 61, 34–42. [Google Scholar] [CrossRef]
  49. McMillan, P.J.; Hart, A.C.; Horn, P.L.; Tracey, D.M.; Maolagáin, C.Ó.; Finucci, B.; Dunn, M.R. Review of life history parameters and preliminary age estimates of some New Zealand deep-sea fishes. N. Z. J. Mar. Freshw. Res. 2020, 1–27. [Google Scholar] [CrossRef]
  50. Livingston, M.E.; Clark, M.R.; Baird, S.J. Trends in Incidental Catch of Major Fisheries on the Chatham Rise for Fishing Years 1989–90 to 1998–99; NZ Fisheries Assessment Report 2003/52; Ministry of Fisheries: Wellington, New Zealand, 2003.
  51. Bailey, D.M.; Collins, M.A.; Gordon, J.D.M.; Zuur, A.F.; Priede, I.G. Long-term changes in deep-water fish populations in the North East Atlantic: Deeper-reaching effect of fisheries? Proc. R. Soc. Lond. Ser. B. 2009, 276, 1965–1969. [Google Scholar]
  52. Priede, I.G.; Godbold, J.A.; Niedzielski, T.; Collins, M.A.; Bailey, D.M.; Gordon, J.D.M.; Zuur, A.F. A review of the spatial extent of fishery effects and species vulnerability of the deep-sea demersal fish assemblage of the Porcupine Seabight, Northeast Atlantic Ocean (ICES Subarea VII). ICES J. Mar. Sci. 2011, 68, 281–289. [Google Scholar] [CrossRef] [Green Version]
  53. Ciannelli, L.; Bailey, K.; Olsen, E.M. Evolutionary and ecological constraints of fish spawning habitats. ICES J. Mar. Sci. 2015, 72, 285–296. [Google Scholar] [CrossRef] [Green Version]
  54. Koslow, J. Continental slope and deep-sea fisheries: Implications for a fragile ecosystem. ICES J. Mar. Sci. 2000, 57, 548–557. [Google Scholar] [CrossRef] [Green Version]
  55. Hayes, K.R.; Dunstan, P.; Woolley, S.; Barrett, N.; Foster, S.; Monk, J.; Peel, D.; Hosack, G.R.; Howe, S.A.; Samson, C.R.; et al. Designing a Targeted Monitoring Program to Support Evidence-Based Management of Australian Marine Parks: A Pilot in the South-East Marine Park Network; NESP Marine Biodiversity Hub: Hobart, Australia, 2021. [Google Scholar]
  56. Chollett, I.; Priest, M.; Fulton, S.; Heyman, W.D. Should we protect extirpated fish spawning aggregation sites. Biol. Conserv. 2020, 241, 108395. [Google Scholar] [CrossRef]
Jmse 09 00723 g001 550
Figure 1. Study area: (a) Location of the study area (red shaded area) south of Tasmania (inset: Australia) with the boundaries of Australian Marine Parks (AMP) shown in cyan; (b) multibeam sonar bathymetry map of the seamount cluster in the study area with 50 m depth contours overlaid in ~200–2000 m depths; the sampled seamounts are highlighted and named; cyan lines are parts of the boundary of the ‘Huon’ AMP.
Figure 1. Study area: (a) Location of the study area (red shaded area) south of Tasmania (inset: Australia) with the boundaries of Australian Marine Parks (AMP) shown in cyan; (b) multibeam sonar bathymetry map of the seamount cluster in the study area with 50 m depth contours overlaid in ~200–2000 m depths; the sampled seamounts are highlighted and named; cyan lines are parts of the boundary of the ‘Huon’ AMP.
Jmse 09 00723 g001
Jmse 09 00723 g002 550
Figure 2. Near-seabed images from Patience Seamount in ~1100 m depth (camera transect 054 on Survey #1): (a) showing polygon method for calculating fish density (here, four eels overlap the vertical extension of the polygon; (b–d) showing the fish assemblage is highly dominated by Diastobranchus capensis.
Figure 2. Near-seabed images from Patience Seamount in ~1100 m depth (camera transect 054 on Survey #1): (a) showing polygon method for calculating fish density (here, four eels overlap the vertical extension of the polygon; (b–d) showing the fish assemblage is highly dominated by Diastobranchus capensis.
Jmse 09 00723 g002
Jmse 09 00723 g003 550
Figure 3. Map of the distribution of counts of individual D. capensis on Patience seamount in the field-of-view of the video camera at 5 s intervals; mean raw counts from the five transects (anti-clockwise from left) = 763, 59, 931, 475, 167; zero counts are shown as black crosses. Seamount base (blue shading) is defined by rate of change of slope; depth contours = 50 m intervals from 850 m.
Figure 3. Map of the distribution of counts of individual D. capensis on Patience seamount in the field-of-view of the video camera at 5 s intervals; mean raw counts from the five transects (anti-clockwise from left) = 763, 59, 931, 475, 167; zero counts are shown as black crosses. Seamount base (blue shading) is defined by rate of change of slope; depth contours = 50 m intervals from 850 m.
Jmse 09 00723 g003
Jmse 09 00723 g004 550
Figure 4. Depth distribution of dominant fishes on Patience Seamount based on counts of individuals along video transects: right-hand side of plot—D. capensis from Surveys #1 (March 2007), #2 (April 2015), Survey #3 (December 2018) (see Figure 3); left-hand side of plot—orange roughy and oreo dories from Survey #1.
Figure 4. Depth distribution of dominant fishes on Patience Seamount based on counts of individuals along video transects: right-hand side of plot—D. capensis from Surveys #1 (March 2007), #2 (April 2015), Survey #3 (December 2018) (see Figure 3); left-hand side of plot—orange roughy and oreo dories from Survey #1.
Jmse 09 00723 g004
Jmse 09 00723 g005 550
Figure 5. Observations of D. capensis on seamounts south of Tasmania (see Figure 1). (a) Density counts of D. capensis and other fishes derived from still images with polygons of measured area collected during survey #1, densities for each seamount are averaged over the number of images (n) examined. (b) the number of D. capensis observed per h of video taken during survey #3, densities for each seamount are averaged over the number of video transects (n) examined.
Figure 5. Observations of D. capensis on seamounts south of Tasmania (see Figure 1). (a) Density counts of D. capensis and other fishes derived from still images with polygons of measured area collected during survey #1, densities for each seamount are averaged over the number of images (n) examined. (b) the number of D. capensis observed per h of video taken during survey #3, densities for each seamount are averaged over the number of video transects (n) examined.
Jmse 09 00723 g005
Jmse 09 00723 g006 550
Figure 6. Partially dissected Diastobranchus capensis specimens from Patience Seamount showing (a) ovaries in abdominal cavity of female; (b) testes in abdominal cavity; (c) several other individuals with external damage consistent with net capture. Scale bars 50 mm (account for near/far distortion).
Figure 6. Partially dissected Diastobranchus capensis specimens from Patience Seamount showing (a) ovaries in abdominal cavity of female; (b) testes in abdominal cavity; (c) several other individuals with external damage consistent with net capture. Scale bars 50 mm (account for near/far distortion).
Jmse 09 00723 g006
Jmse 09 00723 g007 550
Figure 7. Partial dissection of Diastobranchus capensis to reveal the shape and extent of the gas-filled swimbladder. In this individual of 102 cm total length, the swimbladder is 67 cm long (shown by inner edges of the two white markers); it is widest (4 cm) at the anterior bulb then tapers over the length of the posterior tube.
Figure 7. Partial dissection of Diastobranchus capensis to reveal the shape and extent of the gas-filled swimbladder. In this individual of 102 cm total length, the swimbladder is 67 cm long (shown by inner edges of the two white markers); it is widest (4 cm) at the anterior bulb then tapers over the length of the posterior tube.
Jmse 09 00723 g007
Jmse 09 00723 g008 550
Figure 8. Echosounder (18 kHz) volume backscatter echograms from Patience Seamount showing: (a) echogram recorded on 10 April 2015 commencing at 01:00 (local time) during camera transect 024 (Survey #2) down the south-east flank (magenta line shows the approximate location of the video tow); a region of low backscatter of biological origin can be observed at the end of the transect, the acoustic dead-zone and side-lobe interference can mask signal of biological origin; (b) echogram recorded on 10 April 2015 commencing at 11:15 (local) showing a region of very high backscatter that originates from fish with high target strength diagnostic of large gas-filled swim-bladders; dimensions of the aggregation (~100 m high × ~1000 m long) are indicated by the vertical axis and the horizontal scale bar. Right-hand side colour bar indicates decibel values associated with echogram colours.
Figure 8. Echosounder (18 kHz) volume backscatter echograms from Patience Seamount showing: (a) echogram recorded on 10 April 2015 commencing at 01:00 (local time) during camera transect 024 (Survey #2) down the south-east flank (magenta line shows the approximate location of the video tow); a region of low backscatter of biological origin can be observed at the end of the transect, the acoustic dead-zone and side-lobe interference can mask signal of biological origin; (b) echogram recorded on 10 April 2015 commencing at 11:15 (local) showing a region of very high backscatter that originates from fish with high target strength diagnostic of large gas-filled swim-bladders; dimensions of the aggregation (~100 m high × ~1000 m long) are indicated by the vertical axis and the horizontal scale bar. Right-hand side colour bar indicates decibel values associated with echogram colours.
Jmse 09 00723 g008
Jmse 09 00723 g009 550
Figure 9. High signal acoustic backscatter regions believed to be Diastobranchs capensis (red circles, panels a, c, e, g and h) in the two ‘star-pattern’ surveys. Other low signal backscatter regions, e.g., panels (b) and (d) (blue dashed circles) are unlikely to be D. capensis. High signal regions away from the seamount feature itself also believed to be D. capensis due to the absence of other high signal candidate species are marked separately (black circles). Images from real-time display taken from Simrad ER60 software running the Simrad EK60 38 kHz echosounder. Display range is estimated to be −36 to −72 dB.
Figure 9. High signal acoustic backscatter regions believed to be Diastobranchs capensis (red circles, panels a, c, e, g and h) in the two ‘star-pattern’ surveys. Other low signal backscatter regions, e.g., panels (b) and (d) (blue dashed circles) are unlikely to be D. capensis. High signal regions away from the seamount feature itself also believed to be D. capensis due to the absence of other high signal candidate species are marked separately (black circles). Images from real-time display taken from Simrad ER60 software running the Simrad EK60 38 kHz echosounder. Display range is estimated to be −36 to −72 dB.
Jmse 09 00723 g009
Table
Table 1. Details of seamount sampled and abundance of Diastobranchus capensis in photographic imagery.
Table 1. Details of seamount sampled and abundance of Diastobranchus capensis in photographic imagery.
SURVEY #1SURVEY #2SURVEY #3
SeamountSeamount Peak Depth (m)Depth Range Sampled (m)No.
Images 		Average No. D. capensis per m2No. Video
Transects		Average No. D. capensis per hNo. Video TransectsAverage no. D. capensis per h
Patience817904–12401230.2592220.0269.59
Corvina Group750750–12500--0--62.07
Z511781176–1250220.0000--10
Pedra714725–13434480.0020--74.19
Mongrel723778–12442860.0010--0--
Z1610041057–1404540.0000--141.15
Sisters807864–13504580.0010--106.7
Hill B110641139–1405600.0030--0--
Hill K112381248–18172510.0010--87.82
Hill U10831099–14132470.0020--116.29
Dory Hill10541091–14691130.0000--0--
Publisher’s Note: MDPI stays neutral with regard to jurisdictional claims in published maps and institutional affiliations.

Share and Cite

MDPI and ACS Style

Williams, A.; Osterhage, D.; Althaus, F.; Ryan, T.; Green, M.; Pogonoski, J. A Very Large Spawning Aggregation of a Deep-Sea Eel: Magnitude and Status. J. Mar. Sci. Eng. 2021, 9, 723. https://doi.org/10.3390/jmse9070723

AMA Style

Williams A, Osterhage D, Althaus F, Ryan T, Green M, Pogonoski J. A Very Large Spawning Aggregation of a Deep-Sea Eel: Magnitude and Status. Journal of Marine Science and Engineering. 2021; 9(7):723. https://doi.org/10.3390/jmse9070723

Chicago/Turabian Style

Williams, Alan, Deborah Osterhage, Franziska Althaus, Timothy Ryan, Mark Green, and John Pogonoski. 2021. "A Very Large Spawning Aggregation of a Deep-Sea Eel: Magnitude and Status" Journal of Marine Science and Engineering 9, no. 7: 723. https://doi.org/10.3390/jmse9070723

APA Style

Williams, A., Osterhage, D., Althaus, F., Ryan, T., Green, M., & Pogonoski, J. (2021). A Very Large Spawning Aggregation of a Deep-Sea Eel: Magnitude and Status. Journal of Marine Science and Engineering, 9(7), 723. https://doi.org/10.3390/jmse9070723

Note that from the first issue of 2016, this journal uses article numbers instead of page numbers. See further details here.

Article Metrics

Back to TopTop