Continuous in situ monitoring of sediment deposition in shallow benthic environments
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Sedimentation is considered the most widespread contemporary, human-induced perturbation on reefs, and yet if the problems associated with its estimation using sediment traps are recognized, there have been few reliable measurements made over time frames relevant to the local organisms. This study describes the design, calibration and testing of an in situ optical backscatter sediment deposition sensor capable of measuring sedimentation over intervals of a few hours. The instrument has been reconfigured from an earlier version to include 15 measurement points instead of one, and to have a more rugose measuring surface with a microtopography similar to a coral. Laboratory tests of the instrument with different sediment types, colours, particle sizes and under different flow regimes gave similar accumulation estimates to SedPods, but lower estimates than sediment traps. At higher flow rates (9–17 cm s−1), the deposition sensor and SedPods gave estimates >10× lower than trap accumulation rates. The instrument was deployed for 39 d in a highly turbid inshore area in the Great Barrier Reef. Sediment deposition varied by several orders of magnitude, occurring in either a relatively uniform (constant) pattern or a pulsed pattern characterized by short-term (4–6 h) periods of ‘enhanced’ deposition, occurring daily or twice daily and modulated by the tidal phase. For the whole deployment, which included several very high wind events and suspended sediment concentrations (SSCs) >100 mg L−1, deposition rates averaged 19 ± 16 mg cm−2 d−1. For the first half of the deployment, where SSCs varied from <1 to 28 mg L−1 which is more typical for the study area, the deposition rate averaged only 8 ± 5 mg cm−2 d−1. The capacity to measure sedimentation rates over a few hours is discussed in terms of examining the risk from sediment deposition associated with catchment run-off, natural wind/wave events and dredging activities.
KeywordsSedimentation Turbidity Coral reefs Sediment trap Deposition sensor
In shallow benthic environments sediments can be temporarily released into the water column by natural wind and wave events, river plumes from catchment run-off, and dredging and dredging-related activities. The suspended sediments can have a range of effects on filter-feeders and, by changing the quantity and quality of light, on photoautotrophs such as corals and seagrasses (Rogers 1990; Anthony and Connolly 2004; Anthony et al. 2004; Erftemeijer and Lewis 2006; Foster et al. 2010; Jones et al. 2016). The sediments can also subsequently fall out of suspension, increasing sedimentation rates and making benthic organisms expend energy self-cleaning. Many studies have highlighted the significance of sedimentation on coral reefs (reviewed by Rogers 1990; Jones et al. 2016), and sedimentation is ‘…considered one of the most widespread contemporary, human-induced perturbations on reefs…’ (ISRS 2004).
Understanding the environmental risk associated with suspended sediments and sediment deposition is predicated on establishing a relationship between physical and chemical changes in the water column and the response of the underlying communities. Some of the physical changes are comparatively simple to measure, such as benthic light availability which can be routinely measured with submersible photosynthetically active radiation (PAR) quantum light sensors. Suspended sediment concentrations (SSCs) and turbidity can be highly correlated, and there are many commercially available optical devices (nephelometers) for recording turbidity (Gray and Gartner 2009, 2010). Sediment deposition, however, has proven difficult to measure at scales which are relevant to the physiology of local organisms (mg cm−2 d−1, see review by Thomas and Ridd 2004). This is unfortunate, as at least for dredging, increased sedimentation and smothering is one of the key causal pathways leading to mortality of marine organisms in the short term (Jones et al. 2016).
In the absence of suitable techniques for sediment deposition monitoring, sediment traps have routinely been used to estimate sedimentation rates. Because of their simple design (open-ended tubes) and construction (e.g. PVC pipes) they have frequently been used for describing sedimentation rates on reefs (English et al. 1997; Storlazzi et al. 2011; Browne et al. 2012). However, there are many problems associated with using sediment traps to quantify the vertical flux of material in shallow energetic environments that are typical of coral reef environments (Wolanski 1994; Larcombe et al. 1995; Ogston et al. 2004; Storlazzi et al. 2011). These problems have been discussed many times in many different marine environmental settings (Hargrave and Burns 1979; Reynolds et al. 1980; Butman et al. 1986; Kozerski 1994; Jürg 1996; Buesseler et al. 2007), including coral reefs (Ridd et al. 2001; Thomas and Ridd 2004; Bothner et al. 2006; Risk and Edinger 2011; Storlazzi et al. 2011; Browne et al. 2012; Jones et al. 2016). Essentially, sediments entering traps have a lower chance of resuspension than sediment settling on the adjacent seabed, and traps therefore provide an estimate of gross rather than net sedimentation rate (see Cortes and Risk 1985). Sediment traps can also favour deposition due to hydrodynamic disturbance of the flow around the trap.
Recently, sediment pods (SedPods) have been suggested as an alternative technique for estimating sedimentation in situ. These are concrete-filled PVC hubs which act as a proxy for a flat, encrusting coral surface. Because they do not suffer the resuspension limitation and deposition bias of traps, they can provide better estimates of net rather than gross sedimentation (Field et al. 2012). Notwithstanding the issue of what sediment traps actually measure (see Storlazzi et al. 2011), another significant problem is that they have to be left in situ for extended periods (days to weeks), and accumulation rates estimated by averaging over the deployment period. This provides at best a very coarse assessment of temporal patterns of sediment deposition. The same issue applies for SedPods.
For more realistic estimates of sediment deposition, and over much shorter timescales, one of the more promising techniques is a deposition sensor based on optical backscatter sensor (OBS) principles (Ridd et al. 2001; Thomas and Ridd 2005). The instrument uses fibre optic bundles set into a horizontal measuring surface and connected to an infra-red LED and a light sensor. The amount of light from the LED that is back-scattered into the sensor varies in proportion to the amount of sediment that has settled (Ridd et al. 2001; Thomas et al. 2003a, b; Thomas and Ridd 2005). Some of the known limitations of the deposition sensor are that measurements are made at a single point, and that the flat deposition plate is very smooth, sometimes resulting in rapid resuspension and even saltation of sediments across the surface, giving low or sometimes spurious readings.
To address some of these issues, the deposition sensor has recently been redesigned to increase the number of sensors and to incorporate a more standardized measuring surface. Since net sediment deposition is dependent on the surface, a surface that more closely approximated the complex and typically rugose microtopography of a coral surface was selected. As with the use of the OBS principle for surrogate (proxy) monitoring of SSCs, differences in number, size, colour, density and shape of suspended particles, and refractive index (the light-scattering properties) need to be considered (Baker and Lavelle 1984; Conner and De Visser 1992; Gibbs and Wolanski 1992; Thackston and Palermo 2000; Gray and Gartner 2010; Storlazzi et al. 2015).
In this study, we describe the redesign of the deposition sensor, and its calibration and laboratory testing in response to different sediment types and different flow regimes. We also report on field deployment of the sensor in a highly turbid, inshore reef community of the central Great Barrier Reef (GBR). The deployment included calm, benign periods and storm periods. The study reports previously undescribed sub-daily patterns of sediment deposition providing new insights into absolute and relative patterns of one of the key anthropogenic ‘pollutants’ on coral reefs.
Materials and methods
The sediment deposition sensor was tested in a series of laboratory experiments where high SSCs were created and allowed to settle onto the deposition sensor and nearby SedPods and sediment traps. Tests were conducted with different sediment types, colours and particle size distributions (PSDs) and conducted under no flow (static) conditions and different flow regimes. Sediments for the laboratory studies were collected from 5 to 9 m depth by Smith-McIntyre grab or by scuba divers from three different coastal reef settings in Australia. Sediment types were (1) light grey predominantly carbonate (biogenic) sediment from the central GBR (Davies Reef, 18°49.507′S, 147°38.826′E), (2) yellow-brown mixed terrigenous mud and carbonate sediment collected at Middle Reef (Cleveland Bay, 19°11.722′S, 146°48.822′E), or (3) red-brown predominantly siliciclastic sediment collected from the nearshore region of north-west Australia (Pilbara region, 21°37.940′S, 115°0.175′E). All sediments were screened to 2 mm and then ground with a rod mill grinder until the mean grain size was ~30 µm (range 0.5–140 µm) as measured using laser diffraction techniques (Mastersizer 2000, Malvern instruments Ltd, UK). A portion of the sediments of each type were then passed through a series of industrial sieves to create finer PSDs where necessary.
Measurement principle and sensor calibration
Calibration involves relating the mV signals from the backscatter sensor to mass per unit area (mg cm−2) using sediment-specific conversion factors to account for differences in the sediment light-scattering properties. Calibrations were performed in a 3-m perspex settling tube, with sediment introduced to the top of the tube and allowed to settle on a plate suspended from a mass balance 5 mm above the sensor plate surface. The weight of the sediment on the balance is converted from a weight in water into mass using the relative densities of water and the sediment. The total mass of sediment is divided by the surface area of the plate to give a mg cm−2 sediment mass surface density which was compared to the instrument readings.
All experiments were conducted in a 1200-L fibreglass tank using 0.4-µm-filtered seawater at salinity of 33 PSU and temperature of 27 °C. At the start of the experiments the sediments were mixed with 2 L of 0.4-µm-filtered seawater in a domestic blender for 2 min to create sediment slurry which was then added to the tanks and mixed thoroughly using submersible pumps. A range of sedimentation rates was generated by creating different SSCs (range 10–800 mg L−1) and turning the pumps off to allow the sediments to gradually settle out of suspension. For experiments examining deposition under different flow rates, the submersible pumps were operated under different power levels to produce variable flow as measured by an acoustic Doppler velocimeter (16-MHz MicroADV, SonTek, CA, USA).
During the studies the deposition sensor was mounted on a perforated fibreglass grid floor, with the sensor head platform located 50 cm below the water surface. Five PVC sediment traps with an aspect ratio of 6:1 and a mouth surface area of 2.4 cm2, and five PVC SedPods with a surface area of 25.2 cm2 were placed beside the deposition sensor. At the end the experiments the sediment traps and SedPods were capped, and any trapped or accumulated sediment determined gravimetrically. Sediment samples were filtered through pre-weighed 0.4-µm, 47-mm-diameter polycarbonate filters, incubated at 60 °C for ≥24 h and weighed to determine sediment mass.
The nephelometer readings (nephelometric turbidity units, NTUs) were converted into SSC (mg L−1) using site-specific conversion factors. Sediment collected from the site was resuspended in a container, and after measuring the NTU value of the fine sediment suspension, the sample was filtered through pre-weighed 0.4-µm, 47-mm-diameter polycarbonate filters which were then incubated at 60 °C until constant weight (≥24 h), and the mass determined using a laboratory balance.
Wind speed data (scalar averaged 10 min data in km h−1) to support the field deployment were accessed from the AIMS weather station (S2 Platform, 19°8.460′S, 146°53.390′E) in Cleveland Bay, 10 km NE of the deposition sensor deployment location (Fig. 1).
Measurement principle and sensor calibration
Sedimentation rates are estimated from measurements taken every 10 min over the period between the sensor head wipes. In response to a 50 mg L−1 suspension of very fine, light grey carbonate sediment (mean particle size 6.4 ± 0.8 (SE) µm, with 95% of the particles <20 µm), and under static (no flow) conditions, the amount of sediment settling on the surface of the sensor increased with each 10 min reading (Fig. 3b). After 2 h, the fibre optics were automatically wiped clean, returning the sensors to zero and then sediment built up again on the fibre optics over the next 2-h measuring period. This sequence of accumulation and removal results in a ‘zigzag’ or ‘saw-tooth’ pattern over time (Fig. 3b), indicative of net sediment deposition. The slope of the period between each sensor wipe gives the sedimentation rate, which in Fig. 3b was an average of ~6 mg cm−2 for the first 2-h period, equivalent to ~72 mg per cm−2 d−1 if the 2-h rate is converted (normalized) to a 24-h basis. Over the course of the 20-h experiment, there was gradual settlement of the sediment from the water column and the amount of sediment accumulating on the sensor decreased to <0.5 mg cm−2 for the last measuring period. The average of all 2-h periods over day was 14.3 mg cm−2 d−1, and ~50% of the sediment settled in the first 2-h measuring period (see Fig. 3b inset), although there was little or no perceptible change in water cloudiness (turbidity) in the tank during this time.
From 7 August, the sub-daily pattern of deposition showed prominent peaks (see grey bands in Fig. 9), where over 1–3-h periods sediment accumulation rate approximately doubled, from 2–3 to 4–6 mg cm−2 of sediment per 1-h measuring period. These peaks occurred a few hours after the low tide and initially occurred once a day and at night time (or early morning, Fig. 9). From 9 to 10 August, after the maximum SSCs of >100 mg L−1 and when wind speed and RMS water height were decreasing, the peaks occurred twice a day for a few hours after each low tide (Fig. 9).
The data presented here show previously undescribed sub-daily patterns of sedimentation near a reef in the turbid coastal central GBR, providing new insights into both relative patterns and absolute values of what is considered one of the key pollutants on coral reefs. Earlier versions of the deposition sensor used in this study have been deployed in situ in Japan, Papua New Guinea and the inshore central GBR (Thomas et al. 2003a; Thomas and Ridd 2005). The instruments have since been reconfigured involving a change from a single sensor block and fibre optics combination to a triangular pattern of three sensor blocks each with five bundles of fibre optics. The other design change was more significant and involved a move away from a smooth (glassy) measuring surface to a more topographically complex, rugose, surface that more closely approximates a coral. Choosing a representative surface is difficult because at the macroscale, coral growth form can be highly varied (Pratchett et al. 2015). At the microscale most corals are made up many individual polyps that sit within a skeletal cup or corallite, and the corallites are also highly varied in size, shape and spacing. If they share a wall with neighbouring polyps they are called cerioid, or meandroid if the joining walls form valleys; if the corallites have their own walls they are referred to as plocoid, or phaceloid depending how tall or tubular they are. These combinations of macro (growth form) morphology and micro (corallite size, shape and spacing) morphology result in numerous possible permutations and a multitude of different surface textures and rugosity to choose from. An important practical consideration was also the need for a standardized, uniform and easily reproducible surface; this was more important than modelling a specific coral. The final choice was a horizontal plane with multiple, identical, non-adjoining and regularly spaced, circular, medium-sized concave depressions representing the corallites. Using coral terminology, the sensor head plate represents a coral with an explanate growth form, medium- to large-sized (6 mm diameter) plocoid-like corallites, with a small inter-corallite (coenosteum) spacing.
The deposition sensor uses the OBS principle which is well known to be sensitive to the number, size, colour, density and shape of suspended particles and refractive index (Conner and De Visser 1992; Gibbs and Wolanski 1992; Thackston and Palermo 2000; Gray and Gartner 2010; Storlazzi et al. 2015). The calibration experiments showed the instrument was reasonably insensitive to sediments of different texture and colour, in part because the PSDs used were quite similar and typical of those in dredging plumes (Jones et al. 2016). The instrument was most sensitive to the light grey sediment from Davies Reef which is probably due to a higher level of reflection of the infra-red, indicating that, as with the use of nephelometers, site-specific calibration is needed depending on the expected type of sediment PSD (see Fig. 4).
The laboratory testing of the deposition sensor against conventional sediment traps and SedPods highlighted some of the well-known issues associated with using sediment traps to estimate deposition in coral reef environments and the difference between gross and net sedimentation. In response to a high concentration of sediment gradually settling under static conditions, the different techniques gave broadly similar results except at very high SSCs. In these experiments, the sediments settled according to Stokes’ law and to sediment grain size, density and particle-specific settling velocity. The majority of the sediments settled out during the 24-h experiment, passing through the measuring plane (50 cm below the surface) where the traps, SedPods and deposition sensors were located. Under increasing flow, the deposition sensor and SedPods gave different estimates than sediment traps, and for the deposition sensor the saw-tooth pattern was weak indicating net sedimentation was low. At the highest flow rates tested the accumulation rate estimated by the sensors or by the SedPods was only 2–5 mg cm−2 d−1, whereas the traps yielded estimates of 40–50 mg cm−2 d−1. Under the flow conditions, the sediments would have been part of turbulent eddies that entered the sediment trap mouth and circulated within the trap body. Beyond a certain depth in the trap, they would have entered a quiescent zone where resuspension forces were insufficient for them to exit, and they became trapped (Storlazzi et al. 2011).
A number of studies have addressed resuspension limitation associated with traps. McClanahan and Obura (1997) note that a factor of three is required to scale up sedimentation rates on flat tiles to those measured with traps. Field et al. (2012) reported that net sediment accumulation on SedPods was an order of magnitude less than gross accumulation in nearby conventional traps. This is similar to the discrepancy observed in this study. As Storlazzi et al. (2011) noted, in turbulent conditions, sediment traps are much more apt to record information on suspended sediment dynamics than to provide any useful data on sedimentation per se. The implication of these studies is that when sediments from field deployments of traps are dried, weighed, normalized to a surface and expressed as mg cm−2 d−1, the result could be an apparent or ‘pseudo-sedimentation’ rate. Depending on conditions during the deployment, the reported sedimentation rates may partly be an artefact of the trapping process. The deposition sensor has the ability to measure, for the first time, deposition rates on reefs over periods of a few hours as opposed to averages over many days or weeks, and without the resuspension limitation and deposition bias associated with sediment traps.
In situ deployment of the deposition sensor
Measurements were made in Cleveland Bay in the inshore turbid reef zone of the central GBR, which has been the subject of many studies associated with understanding sedimentary processes, sediment transport and fate, and the effects of watershed development on reef growth in marginal, turbid environments (Carter et al. 1993; Larcombe et al. 1995, 2001; Jing and Ridd 1996; Orpin et al. 1999, 2004; Anthony et al. 2004; Browne et al. 2010, 2012, 2013; Lambrechts et al. 2010; Bainbridge et al. 2012; Browne 2012; Orpin and Ridd 2012; Perry et al. 2012; Macdonald et al. 2013; Delandmeter et al. 2015).
Over the course of the deployments, sediment deposition was either barely measureable or occurred in one of two distinct patterns: relatively constant or pulsed. The pulsed pattern was made up of short-term (4–6 h) periods of ‘enhanced’ deposition which typically began a few hours after low tide, peaking at the mid-tide phase. In the detailed time course shown in Fig. 9, the pulsed deposition occurred in either a diurnal (once a day) or semi-diurnal (twice a day) pattern. Sedimentation rates were similar between modes: ~42 mg cm−2 d−1 during 3–6 August (constant mode) or ~40 mg cm−2 d−1 during 7–11 August (pulsed mode).
In general terms, SSCs and sedimentation were closely related, in so far as periods of elevated sediment deposition occurred during periods of elevated turbidity. This is intuitive, as resuspended sediment is a prerequisite for sediments to settle out of suspension. The high SSCs were in turn related to elevated wind speeds and wave height, i.e. to wind-wave events. During the study, periods of elevated wind speeds occurred over several days associated with weather fronts and under a diel pattern associated with a locally generated sea breeze. This sea breeze is a prominent feature in Cleveland Bay during the afternoon and early evening (Larcombe et al. 1995), and the turbidity regime in Cleveland Bay is thought to be determined by high-frequency, short-wavelength wind waves and wave-generated resuspension, in addition to longer wave swell along the GBR which refract into Cleveland Bay (Larcombe et al. 1995; Orpin et al. 1999, 2004).
On a finer, sub-daily timescale the relationship between wind speed, SSCs and sedimentation was uncoupled. Perhaps the most interesting result was the pulsed, enhanced sedimentation events during the deployment that tended to occur when wind speeds were falling associated with the loss of the sea breeze at night time, or a gradual decrease in winds over several days associated with the passing of a weather front. Each of the pulses occurred shortly after a transitory increase in SSCs at the seabed. Our interpretation of these observations is a gradual reduction of near-bed wave-induced orbital velocities related to decreasing wind/waves (associated with loss of the sea breeze at night). However, this cannot account for the transition from the more constant deposition pattern to the pulsed pattern and the transition (and eventual loss) of the diurnal then semi-diurnal pulsed patterns (Fig. 9). These patterns developed following the progression from neap tides (lower tidal range) to spring tides (higher tidal range), and each event occurred after low water, peaking at the mid-tide mark. This suggests tidal modulation of the deposition cycle that could be caused by (1) reduced tidal flows and a settling lag, such that sediments in the water column need time to settle out of suspension onto the sensor, or (2) gradually increasing water depth at the mid-tide point, reducing wave orbital velocities and enhancing settling. An alternative suggestion is that the patterns represent advection of turbid water from Cleveland Bay across the sensors. Without measurements of current speed and direction, it is not possible to consider this further.
The deposition sensor was deployed in a naturally very turbid area over a period of time where SSCs ranged from <1 to as high as 157 mg L−1, and averaged 17 mg L−1 (median 7 mg L−1). The exposure period included several spring–neap tidal cycles and a range of wind conditions from calm to extreme. This provided an ideal spectrum of conditions to allow generalizations on the absolute levels of sediment deposition and patterns of deposition in a naturally highly turbid reef environment. For the whole deployment, which included several very high wind events and SSCs >100 mg L−1, deposition rates averaged 19 ± 16 mg cm−2 d−1 (median deposition rate = 11 mg cm−2 d−1). For the first half of the deployment, where SSCs varied from <1 to 28 mg L−1, which are typical for the Cleveland Bay area (Larcombe et al. 1995; Orpin et al. 2004; Macdonald et al. 2013), the deposition rates averaged only 8 ± 5 mg cm−2 d−1. This value is very similar to net deposition rates of 3–7 mg cm−2 d−1 measured over the course of a year at the same site using shallow trays, which also do not limit sediment resuspension (Browne et al. 2012). These values, especially the upper values, are much lower than sediment trap accumulation rates measured around Magnetic Island and Cleveland Bay which have been reported to range 30–120 mg cm−2 d−1 (averaging 80 mg cm−2 d−1; McIntyre and Associates Pty. Ltd. 1986), 25–243 mg cm−2 d−1 (averaging 75 mg cm−2 d−1, including 27–62 mg cm−2 d−1 at Middle Reef; Larcombe et al. 1994) and 3–360 mg cm−2 d−1 (averaging ~50 mg cm−2 d−1; Mapstone et al. 1992). As discussed in Jones et al. (2016), in laboratory-based studies of the effects of sedimentation on corals the application rates used, which are based on sediment trap data, are often in the high tens of mg cm−2 d−1, commonly hundreds of mg cm−2 d−1, and even g cm−2 d−1. These application rates have well-described effects on coral physiology, but if based on a measurement technique (sediment traps) which is overestimating sedimentation rates by up to an order of magnitude, the relevance of these application rates needs to be considered, and application of the knowledge to coral reef processes should be cautious (Storlazzi et al. 2011).
The deposition sensor can be constructed from off-the-shelf electronics (LED lights and sensors, fibre optic bundles, servo, data logger and batteries), with some machining required for the sensor head, sensor block and PVC pipe housing. For the many reasons outlined in Field et al. (2012), SedPods offer a viable low-cost coral proxy for measuring net sedimentation, but they do not have self-cleaning mechanisms to prevent biofouling and this precludes extended in situ deployments. Estimates of net sedimentation at a timescale of 24 h by SedPods requires daily boating and diving operations (for collection and redeployment) which comes with logistical and financial costs and safety issues (Llewellyn and Bainbridge 2015). Obvious future directions include extending the deposition sensor deployments to less marginal environments, and quantifying the intensity, duration and frequency of sedimentation events under natural and under anthropogenic influences (such as during dredging campaigns), to define the range of sedimentation rates corals are likely to experience.
This research was funded by the Western Australian Marine Science Institution (WAMSI) as part of the WAMSI Dredging Science Node, and made possible through investment from Chevron Australia, Woodside Energy Limited, BHP Billiton as environmental offsets and by co-investment from the WAMSI Joint Venture partners. The commercial entities had no role in data analysis, decision to publish, or preparation of the manuscript. This project is also supported through funding from the Australian Government’s National Environmental Science Programme. Natalie Giofre (AIMS) helped with the laboratory and field experiments.
- Cortes JN, Risk MJ (1985) A reef under siltation stress: Cahuita, Costa Rica. Bull Mar Sci 36:339–356Google Scholar
- English S, Baker V, Wilkinson C (1997) Survey manual for tropical marine resources: Australian Institute of Marine Science TownsvilleGoogle Scholar
- Foster T, Corcoran E, Erftemeijer P, Fletcher C, Peirs K, Dolmans C, Smith A, Yamamoto H, Jury M (2010) Dredging and port construction around coral reefs. Report No 108, PIANC Environmental Commission, Brussels, BelgiumGoogle Scholar
- Gray J, Gartner J (2010) Overview of selected surrogate technologies for high-temporal resolution suspended sediment monitoring. Proceedings of the 2nd Joint Federal Interagency Conference (June 27–July 1) Las Vegas, NV, USA, 207 ppGoogle Scholar
- ISRS (2004) The effects of terrestrial runoff of sediments, nutrients and other pollutants on coral reefs. Briefing Paper 3, International Society for Reef Studies, 18 ppGoogle Scholar
- Larcombe P, Ridd PV, Wilson B, Prytz A (1994) Sediment data collection. In: Benson LJ, Goldsworthy PM, Butler IR, Oliver J (eds) Townsville Port Authority Capital Dredging Works 1993. Environmental Monitoring Program. Townsville Port Authority, Townsville, Queensland, Australia, pp 149–163Google Scholar
- Llewellyn LE, Bainbridge SJ (2015) Getting up close and personal: the need to immerse autonomous vehicles in coral reefs. OCEANS 2015-MTS/IEEE Washington, 19–22 October 2015, pp 1–9Google Scholar
- Mapstone BD, Choat J, Cumming R, Oxley W (1992) The fringing reefs of Magnetic Island: benthic biota and sedimentation-a baseline study. Research report No. 13, Great Barrier Reef Marine Park Authority, Townsville, AustraliaGoogle Scholar
- McIntyre and Associates Pty. Ltd. (1986) Magnetic Keys Development, Nelly Bay, Magnetic Island. Impact Assessment Study, May 1986Google Scholar
- Ogston AS, Storlazzi CD, Field ME, Presto MK (2004) Sediment resuspension and transport patterns on a fringing reef flat, Molokai, Hawaii. Coral Reefs 23:559–569Google Scholar
- Reynolds CS, Wiseman SW, Gardner W (1980) An annotated bibliography of aquatic sediment traps and trapping methods. Occasional Publication No. 11, Freshwater Biological Association, UK, 54 ppGoogle Scholar
- Thackston E, Palermo MR (2000) Improved methods for correlating turbidity and suspended solids for monitoring. US Army Engineer Research and Development Center, Vicksberg, MS, p 12Google Scholar
- Wolanski E (1994) Physical oceanographic processes of the Great Barrier Reef. CRC Press, Boca Raton, FLGoogle Scholar
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