Nitrogen Removal in Streams of Agricultural Catchments—A Literature Review

Bírgand, François; Skaggs, R. W.; Chescheir, G. M.; Gilliam, J. W.

doi:10.1080/10643380600966426

Cited by 215 publications

(205 citation statements)

References 239 publications

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“…Nitrate concentrations were highest at locations around LWD, particularly during the autumn high flow event, indicating increased down-welling of nitrate-rich surface water into the streambed at locations \ 1 m away from LWD at high flow. This increased hyporheic exchange is likely due to enhanced surface water infiltration due to wood-induced bed-form complexity, as has been observed experimentally and in the field (Birgand et al 2007;Elliott and Brooks 1997;Kail 2003;Klaar et al 2011) and has been shown to be particularly effective at high discharge (Munz et al 2011;Packman and Salehin 2003). Krause et al (2014) predicted hyporheic residence times would be longer around LWD, due to fine sediment trapping around the wood structures.…”

Section: Discussionmentioning

confidence: 85%

Enhanced hyporheic exchange flow around woody debris does not increase nitrate reduction in a sandy streambed

et al. 2017

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Anthropogenic nitrogen pollution is a critical problem in freshwaters. Although riverbeds are known to attenuate nitrate, it is not known if large woody debris (LWD) can increase this ecosystem service through enhanced hyporheic exchange and streambed residence time. Over a year, we monitored the surface water and pore water chemistry at 200 points along a * 50 m reach of a lowland sandy stream with three natural LWD structures. We directly injected 15 N-nitrate at 108 locations within the top 1.5 m of the streambed to quantify in situ denitrification, anammox and dissimilatory nitrate reduction to ammonia, which, on average, contributed 85, 10 and 5% of total nitrate reduction, respectively. Total nitrate reducing activity ranged from 0 to 16 lM h -1 and was highest in the top 30 cm of the stream bed. Depth, ambient nitrate and water residence time explained 44% of the observed variation in nitrate reduction; fastest rates were associated with slow flow and shallow depths. In autumn, when the river was in spate, nitrate reduction (in situ and laboratory measures) was enhanced around the LWD compared with non-woody areas, but this was not seen in the spring and summer. Overall, there was no significant effect of LWD on nitrate reduction rates in surrounding streambed sediments, but higher pore water nitrate concentrations and shorter residence times, close to LWD, indicated enhanced delivery of surface water into the streambed under high flow. When hyporheic exchange is too strong, overall nitrate reduction is inhibited due to short flow-paths and associated high oxygen concentrations.

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Section: Discussionmentioning

confidence: 85%

Enhanced hyporheic exchange flow around woody debris does not increase nitrate reduction in a sandy streambed

et al. 2017

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“…Natural sources for phosphorus and nitrogen comprise leaching from terrestrial soils and plant material during decomposition, release of P from weathering rocks, atmospheric deposition of N 2 (precipitation and dry fallout), and biological N fixation through cyanobacteria (Mainstone and Parr 2002;Bernot and Dodds 2005;Birgand et al 2007;Withers and Jarvie 2008). As nutrient inputs from natural sources are generally low, pristine streams usually show SRP concentrations <10 μg SRP L À1 , while average DIN concentrations may amount to 0.1 mg NO 3 -N L À1 , 0.015 mg NH 4 -N L À1 , and 0.001 mg NO 2 -N L À1 (Allan and Castillo 2007).…”

Section: Forms and Sources Of Phosphorus And Nitrogenmentioning

confidence: 99%

“…10.2). Biotic transformations include the autotrophic and heterotrophic uptake of nutrients from the water, their assimilation into biomass, and their release by excretion and microbial decomposition (Reddy et al 1999;Bernot and Dodds 2005;Birgand et al 2007). In deep and slow-flowing rivers and floodplain channels, nutrient uptake by macrophytes and emergent plants plays a major role in nutrient cycling.…”

Section: Nutrient Cycling In Streams and Riversmentioning

confidence: 99%

Phosphorus and Nitrogen Dynamics in Riverine Systems: Human Impacts and Management Options

Weigelhofer

Hein

Bondar‐Kunze

2018

Riverine Ecosystem Management

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“…If we assume hyporheic exchange within the streambed to be the dominant transfer mechanism with the transient storage zones, the mass transfer coefficient can be expressed as a function of the average flow rate into the sediments per unit bed area q B (L T −1 ) and the flow depth as a = q B /h [Marion et al, 2008;Worman et al, 2002;Packman and Bencala, 2000]. The mass transfer velocity q B has been shown to be weakly variable within a narrow range (say, between 5 to 15 [cm d −1 ], [see, e.g., Birgand et al, 2007]. For what concerns the dependence of b on h, we will refer to a simplified scheme employing the basic scales derived from an equivalent rectangular cross sections.…”

Section: Appendix Bmentioning

confidence: 99%

Stochastic modeling of nutrient losses in streams: Interactions of climatic, hydrologic, and biogeochemical controls

Botter

Basu

Zanardo

et al. 2010

Water Resources Research

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[1] We present an analytical, stochastic approach for quantifying intra-annual fluctuations of in-stream nutrient losses induced by naturally variable hydrologic conditions. The relevance of the problem we address lies in the growing concern for the major environmental impacts of increasing nutrient loads from watersheds to freshwater bodies and coastal waters. Here we express the first-order nutrient loss rate constant, k e , as a function of key biogeochemical and hydrologic controls, in particular the stream depth (h). The stage h modulates the impact of natural streamflow temporal fluctuations (induced by intermittent rainfall forcings) on the underlying biogeochemical processes and thus represents the major driver of at-a-site fluctuations of k e . Novel expressions for the probability distribution function (pdf) of h and k e are derived as a function of a few eco-hydrologic, morphologic and biogeochemical parameters. The shape of such pdf's chiefly depends on the following attributes: (1) the average frequency of streamflow-producing rainfall events, l; (2) the inverse of mean catchment residence time, k; and (3) a stream channel shape factor, identified through the discharge rating curve exponent b. For l/(kb) > 1, h and k e have lower intra-annual variability and lower sensitivity to climatic and morphologic controls, leading to improved predictability and ease of measurement of these attributes. Moment analyses suggest that the variability of k e , relative to that of h, is attenuated for l/(kb) > 1. Thus, the interplay between climate-landscape parameters and the stream shape factor b controls the temporal variability induced by stochastic rainfall forcings on stream stages and nutrient removal rates.

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Nitrogen Removal in Streams of Agricultural Catchments—A Literature Review

Cited by 215 publications

References 239 publications

Enhanced hyporheic exchange flow around woody debris does not increase nitrate reduction in a sandy streambed

Enhanced hyporheic exchange flow around woody debris does not increase nitrate reduction in a sandy streambed

Phosphorus and Nitrogen Dynamics in Riverine Systems: Human Impacts and Management Options

Stochastic modeling of nutrient losses in streams: Interactions of climatic, hydrologic, and biogeochemical controls

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