Measurement of soluble reactive phosphorus concentration profiles and fluxes in river-bed sediments using DET gel probes

Jarvie, Helen P.; Mortimer, Robert J.G.; Palmer-Felgate, Elizabeth J.; Quinton, Katherine St.; Harman, Sarah; Carbo, P.

doi:10.1016/j.jhydrol.2007.10.041

Cited by 60 publications

(34 citation statements)

References 46 publications

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“…For phosphate at 1 mg L À1 and at much lower concentrations in rivers there was no evidence of binding to APA gels. [51] No enrichment in an agarose gel was observed for Cd, Cu, Mn, chloride, bromide, sulfate and nitrate, but concentrations in solution were high at 10 mg L À1 . [52] In a comprehensive study of cationic trace metal binding to APA, restricted and agarose gels and to the polyethersulfone membrane filter (Supor-450, Pall) commonly used within DGT, [53] the concentration of metals, the ionic strength and the solution composition were systematically varied.…”

Section: Inert Diffusive Gel?mentioning

confidence: 96%

“…[39,51,52] To our knowledge the binding of simple organic ligands has not been directly tested, although measurements of metals by DGT in solutions where they are present have been sensibly interpreted without invoking such effects. [56][57][58] An experimental study has considered directly the enrichment in an APA gel of Suwannee River fulvic acid (SRFA) and humic acid extracted from forest soil (FSHA).…”

Section: Possible Ligand Bindingmentioning

confidence: 99%

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Progress in understanding the use of diffusive gradients in thin films (DGT) – back to basics

2012

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Environmental context. It is now nearly 20 years since the introduction of the technique of diffusive gradients in thin films, which can provide information on solute concentrations and dynamics in sediments, soils and water. The interpretation of these measurements in terms of concentrations relies on simple equations and associated assumptions. This review examines how well they have stood the test of time.Abstract. Diffusive gradients in thin films (DGT) is now widely used to measure a range of determinands in waters, soils and sediments. In most cases the mass accumulated is interpreted in terms of a labile form of the component being measured using a simple equation that applies to steady-state conditions. During the past decade several publications have revealed phenomena that question some of the assumptions necessary for use of the simple equation. This review systematically examines the available evidence relating to appropriate geometry, possible charge effects, binding of solutes and ligands to the diffusive gel and filter, the rate of reaction with the binding layer, the effects of solution complexation and kinetic limitation, necessary time for deployment and the measurement of nanoparticles. DGT emerges as a robust monitoring tool for labile components in solution. Although there is evidence, for some conditions, of binding of metals and, more moderately, humic substances to the diffusive gel and filter membrane, this is unlikely to affect DGT measurement in natural waters for deployment times exceeding a few days. Detailed speciation and kinetic studies require a more thorough interpretation of the mass accumulated by DGT. A coherent theory has emerged for relatively simple solutions, but systems with complex heterogeneous ligands, as is the case for natural waters, are challenging. The size discrimination of DGT is still poorly known. Systematic measurements with well characterised nanoparticles are required to define the distribution of pore sizes in the gels and to establish the contribution of natural colloids to the DGT measurement.

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Section: Inert Diffusive Gel?mentioning

confidence: 96%

Section: Possible Ligand Bindingmentioning

confidence: 99%

Progress in understanding the use of diffusive gradients in thin films (DGT) – back to basics

2012

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“…Data for two large catchments representative of major farming landscapes of the UK are shown in Figure 2. Situations where there is potential for P release from the sediment tend to occur (a) when the sediment is already saturated with P and is reaching equilibrium with the overlying water-column [90]; (b) after a reduction in dissolved P concentrations in the overlying water column (e.g., after point source reductions) and before the sediment has been flushed downstream by subsequent storm events [91,92]; (c) a high sediment organic C content (e.g., from livestock or septic tanks) promoting migration of the redox boundary to, or above, the sediment-water interface and reductive dissolution of the Fe-oxyhydroxides in the surface sediments [91,93]; and (d) mechanical disturbance of the "oxidised cap" of surface sediment, which may release P-rich pore-waters from subsurface anoxic sediment into the overlying river water [94].…”

Section: Waterbody Characteristicsmentioning

confidence: 99%

Agriculture and Eutrophication: Where Do We Go from Here?

et al. 2014

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Abstract:The eutrophication of surface waters has become an endemic global problem. Nutrient loadings from agriculture are a major driver, but it remains very unclear what level of on-farm controls are necessary or can be justified to achieve water quality improvements. In this review article, we use the UK as an example of societies' multiple stressors on water quality to explore the uncertainties and challenges in achieving a sustainable balance between useable water resources, diverse aquatic ecosystems and a viable agriculture. Our analysis shows that nutrient loss from agriculture is a challenging issue if farm productivity and profitability is to be maintained and increased. Legacy stores of nitrogen (N) and phosphorus (P) in catchments may be sufficient to sustain algal blooms and murky waters for decades to come and more innovation is needed to drawdown and recover these nutrients. Agriculture's impact on eutrophication risk may also be overestimated in many catchments, and more accurate accounting of sources, their bioavailabilities and lag times is needed to direct proportioned mitigation efforts more effectively. Best practice farms may still be leaky and incompatible with good water quality in high-risk areas requiring some prioritization of society goals. All sectors of society must clearly use N and P more efficiently to develop long-term sustainable solutions to this complex issue and nutrient reduction strategies should take account of the whole catchment-to-coast continuum. However, the right balance of local interventions OPEN ACCESS Sustainability 2014, 6 5854 (including additional biophysical controls) will need to be highly site specific and better informed by research that unravels the linkages between sustainable farming practices, patterns of nutrient delivery, biological response and recovery trajectories in different types of waterbodies.

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“…Recent research has deployed DET probes in riverine sediments for characterization of fine resolution profiles of NO 3 -, NH 4 ? and soluble reactive phosphorus (Jarvie et al 2008;Palmer-Felgate et al 2010). The depth of DET deployment in these studies ranged from four to fifteen cm below the river bed.…”

Section: Introductionmentioning

confidence: 99%

Influence of emergent vegetation on nitrate cycling in sediments of a groundwater-fed river

et al. 2013

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Emergent vegetation in river beds can play a significant role in nutrient cycling in riverine sediments. We analysed and compared pore water NO 3 -concentration gradients in the sediments of the River Leith, Cumbria, UK, in the presence and absence of emergent vegetation (dominated by Sparganium spp.). High resolution (1 cm interval), in situ, vertical profiles of NO 3 -to 30 cm depth were measured using deployment of diffusive equilibrium in thin films probes on four occasions from July to September 2010. We found significantly (p \ 0.05) lower NO 3 -concentration under vegetated sediments (VS) compared to those under adjacent un-vegetated sediments (UVS). Concentrations of dissolved oxygen, measured in pore water collected from multi-level piezometers at 10, 20, 25, 30 and 35 cm depths at the VS and UVS sties, were generally lower under VS (median concentration = 28 lM) than under UVS (median = 132 lM) and correlated significantly with NO 3 -concentration (Spearman's r = 0.74, p \ 0.05). Similarly, pore water dissolved organic carbon (DOC) concentration was 2.8 times higher under VS compared to UVS, and correlated negatively with NO 3 -concentration (Spearman's r = -0.39, p \ 0.05). Specific ultra-violet absorption at 254 nm (SUVA) and per cent aromaticity values of DOC were significantly higher under VS (p \ 0.05), suggesting that the DOC contained more complex (aromatic) compounds than DOC recorded under UVS. We suggest that, the higher quantity of DOC and its distinct SUVA and percentage aromaticity under VS may have supported faster dissolved oxygen consumption, with the creation of anoxic zones conducive for NO 3 -reduction mainly through denitrification. Metabolic uptake and immobilization of NO 3-by plants and microbes may have further contributed to lower NO 3 -concentrations under VS. As Sparganium spp. is a common plant growing in river beds in the UK, its role in NO 3 -cycling should be considered in attempts to accurately budget N cycling in river beds.

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Measurement of soluble reactive phosphorus concentration profiles and fluxes in river-bed sediments using DET gel probes

Cited by 60 publications

References 46 publications

Progress in understanding the use of diffusive gradients in thin films (DGT) – back to basics

Progress in understanding the use of diffusive gradients in thin films (DGT) – back to basics

Agriculture and Eutrophication: Where Do We Go from Here?

Influence of emergent vegetation on nitrate cycling in sediments of a groundwater-fed river

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