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P losses but will also consider losses of N and sediment in order to recommend management practices that can provide maximum environmental benefit. The testing of the mitigation measures examined in this project will provide evidence to help farmers select the most suitable methods for mitigating losses of P from their land. It will also help bodies such as DEFRA to target funding for farmers to undertake mitigation measures. If mitigation measures are to be adopted by farmers they need to be at worst cost-neutral. Analyses will consider the costs associated with introducing and maintaining the mitigations practices and the effect of adopting mitigation options upon economic land management. These analyses will also consider whether any cost shortfall may be met from other funding sources. ACKNOWLEDGEMENTS The authors are grateful to DEFRA for funding this project. REFERENCES ADAS Consulting Ltd (2003). Towards understanding factors controlling transfer of phosphorus within and from agricultural fields. DEFRA project number PE0111. URL http://www.defra.gov.uk/science/project_data/DocumentLibrary/PE0111/PE0111_ 1490_FRP.doc Bartram J and Balance R (1996). Water Quality Monitoring: A Practical Guide to the Design and Implementation of Freshwater Quantitative Studies and Monitoring Programmes. E and FN Spon, London. Department of Environment (1992). Phosphorus and Silicon in Waters, Effluents and Sludges Department of Environment Standing Committee of Analysts, HMSO, London. Haygarth PM, Condron LM, Heathwaite AL, Turner BL and Harris GP (2005). The phosphorus transfer continuum: Linking source to impact with an interdisciplinary and multi-scaled approach. Science of the Total Environment 344, 5–14. Haygarth PM and Jarvis SC (1999). Transfer of phosphorus from agricultural soils. Advances in Agronomy 66, 195–249. Haygarth PM, Chapman PJ, Jarvis SC and Smith RV (1998). Phosphorus budgets for two contrasting grassland farming systems in the UK. Soil Use and Management 14, 160–67. Quinton JN and Catt JA (2004). The effects of minimal tillage and contour cultivation on surface run-off, soil loss and crop yield in the long-term Woburn Soil Erosion Experiment on a sandy soil in England. Soil Use and Management 20, 343–49. USEPA (1985). Methods for Chemical Analysis of Water and Wastes. US Environmental Protection Agency Environmental Monitoring Support Laboratory, Cincinnati, Ohio. 247
NITRATE CONTAMINATION OF GROUNDWATER FROM AGRICULTURE IN CANTERBURY, NEW ZEALAND: MEASUREMENT AND MANAGEMENT OF A HIDDEN PROBLEM KJW Taylor Environment Canterbury, 58 Kilmore Street, PO Box 345, Christchurch, New Zealand 8001, E-mail: Ken.Taylor@ecan.govt.nz SUMMARY Nitrate contamination of groundwater from agriculture is an increasingly important issue for resource management in Canterbury. Most people in the region are dependent on untreated groundwater for drinking, and although communities place a high value on groundwater quality, over much of the plains the resource is unconfined and therefore at risk from nitrate contamination. While samples from only a small proportion of wells in the monitoring network (2-6%) have nitrate-N concentrations in excess of NZ Drinking Water Standards, the data show a trend of increasing concentrations (up to 0.7 mgL -1 yr -1 ) across large parts of the alluvial aquifer system. This is particularly marked in those areas where the primary source of recharge is rainfall, as opposed to seepage from rivers. Agricultural development on the Canterbury Plains has been ongoing for many years, but there has been a shift in production systems over the last decade in particular, from mixed cropping and dry-land sheep grazing to more intensive irrigated pastoral and arable farming, driven in part by developments in irrigation technology. Dairying has emerged as a major land use in formerly dry-land areas. This intensification has the potential to contribute to further increases in nitrate concentrations in groundwater. The management response to the nitrate trend has included: increased research effort to quantify N contributions from multiple sources over time and at a range of spatial scales, more stringent regulation of point-source discharges, and the promotion of best management practices. The most important new initiative is a proposed rule requiring landowners to estimate nitrate-leaching losses, and to undertake nutrient budgeting and other measures if leaching thresholds are exceeded. 248
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International Water Association AGR
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2006 Conference Organising Committe
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Theme 2: Cost-effectiveness of Best
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Poster Presentations The Farm Soils
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viii
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managers need support in understand
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During the past 20 years, it became
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infiltration); and (4) capture, sto
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DOMINATING PARAMETERS OF IMPAIRMENT
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Using the results of the unsupervis
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Kohonen T (2001). Self-Organizing M
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WATER FRAMEWORK DIRECTIVE IMPLEMENT
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Table 1: Modelled total annual loss
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• It should be possible to apply
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Scottish Executive against 18 measu
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REFERENCES Anthony S, Betson M, Lor
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ased on the ‘drainage basin’ in
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management practices’ (BMPs) toge
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It is envisaged that these data wil
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testing (including climate change)
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Council of the European Communities
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DECREASING THE NITROGEN SOIL SURFAC
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Table 1: Overview of the measures c
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Table 2: Costs (C), effects (E) and
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Figure 2: Combination of ‘best av
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MATERIALS AND METHODS At the 5-km 2
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REFERENCES Jordan P, Menary W, Daly
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Although the TMDL programme origina
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grassland and heather moorland, sup
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Given that the release of P from th
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to the underlying causes, and thus
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All water body use attainment infor
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indicate the possible presence of p
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DEVELOPMENT AND IMPLEMENTATION OF M
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BMP is being implemented and the ap
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THE USE OF PONDS TO REDUCE POLLUTIO
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established pond/wetland for nutrie
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Table 1: Hydraulic load, mean water
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Comparable SS removals have been re
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Reddy GB, Hunt PG, Phillips R, Ston
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In general, the combinations of mea
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final word on the POMs selection an
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CONCLUSIONS The ERBD project team i
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Table 1: A summary of the measures
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Table 3: A summary of the represent
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cost (£'000/farm) or reduction in
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ECONOMIC IMPLICATIONS OF MINIMISING
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spread cattle slurry in the autumn
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£25,000. The investment in trailin
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Studies on a drained clay soil at B
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REFERENCES Anon (2000). Fertiliser
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(Haygarth and Jarvis, 1999). The vo
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Application Representative farm sys
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Table 2: Modelled cost-curve for th
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ASSESSING THE SIGNIFICANCE OF DIFFU
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In the absence of data on the sourc
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Magnitude of Impacts The magnitude
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D. Use relative area of farm and wh
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ADAS has developed a matrix for Def
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Dickson JW, Edwards T, Jeffrey WA,
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60% phosphorus and 50% nitrogen of
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RESULTS AND DISCUSSION Landscape St
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was contributed to the low vegetati
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iological uptake in a grassed area.
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Tim US, Jolly R and Liao HH (1995).
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to control SS and P loads from agri
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Total P inputs in fertilisers and m
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Within the Teme catchment, largest
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A RISK ASSESSMENT AND MITIGATION ST
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Environmental Monitoring The primar
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BMP measure 1 (exclusion of stock f
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(a) With reference to the increase
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ACKNOWLEDGEMENTS SAC acknowledges f
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The Environment Sensitive Farming (
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improved further as a result of att
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to do more to reduce pesticide impa
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MANAGING DIFFUSE POLLUTION FROM A F
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turbulent air mixing. The effect th
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Although nitrate leaching can be re
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infiltration of water sheeting off
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Nisbet TR, Orr H and Broadmeadow S
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anthropogenic activities are pollut
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monitoring is determined up front b
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(USEPA). Nevertheless, by applying
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• Sampling equipment •Laborator
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Reinert RE, Knuth BA, Kamrin MA and
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Tier 3 - Tier 3 of LMCs is planned
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policy literature, although this is
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Figure 1: Individual-collective spe
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• tailoring activities to local c
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ACKNOWLEDGEMENTS The support of the
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THE EFFECT OF DIFFUSE POLLUTION FRO
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equires the Minister to designate a
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protection and restoration, sustain
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expensive. One-to-one contact becom
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farmers. In England, recent policy
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practices but, hopefully, the chang
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A CASE STUDY: ADOPTION OF BEST MANA
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The approaches taken by Brittany to
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MANURE TREATMENT By January 2005, t
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REGULATORY OPTIONS FOR THE MANAGEME
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There are also measures that contro
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Page 211 and 212: PHOSPHORUS STORAGE IN FINE CHANNEL
Page 213 and 214: structure and minimum level of main
Page 215 and 216: REFERENCES May L, Place C, O’Hea
Page 217 and 218: LOUND CATCHMENT PROJECT: WORKING WI
Page 219 and 220: MINIMISING THE PRESSURES AND IMPACT
Page 221 and 222: Predicting Bathing Water Quality Vi
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Page 225 and 226: Table 4: Expected lifetime benefits
Page 227 and 228: DETERMINATION OF THE VETERINARY ANT
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Page 231 and 232: Table 2: Regression functions and c
Page 233 and 234: OPPORTUNITIES AND CONSTRAINTS FOR U
Page 235 and 236: to land managers and agency staff t
Page 237 and 238: stakeholders, together with their i
Page 239 and 240: REFERENCES EC (2000). Directive 200
Page 241 and 242: A third scenario was applied to Clu
Page 243 and 244: Based on a detailed distribution of
Page 245 and 246: could be misleading. The results of
Page 247 and 248: TACKLING DIFFUSE NITRATE POLLUTION:
Page 249 and 250: AMMONIA VOLATILISATION FROM CATTLE
Page 251 and 252: and 27% of the soil surface at 80 m
Page 253 and 254: FIELD TESTING OF MITIGATION OPTIONS
Page 255: techniques can significantly reduce
Page 259 and 260: MATERIALS AND METHODS At two UK sit
Page 261 and 262: ACKNOWLEDGEMENTS Funding of this wo
Page 263 and 264: y standard methods and fresh, end o
Page 265 and 266: comparable to those in water draini
Page 267 and 268: Results may be influential in deter
Page 269 and 270: • numbers and distribution of liv
Page 271 and 272: Using this method of classification
Page 273 and 274: Table 5: Results of land use scenar
Page 275 and 276: CONCLUSIONS As a decision support t
Page 277 and 278: types. This paper reports results f
Page 279 and 280: N Losses in Drainage Water Mean nit
Page 281 and 282: SOIL AND CROP MANAGEMENT EFFECTS ON
Page 283 and 284: treatments, typically 10 storm even
Page 285 and 286: Tramline Effects In both years, obs
Page 287 and 288: Notes 278
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