Irrigation can be broadly defined as the practice of applying additional water (beyond what is available from rainfall) to soil to enable or enhance plant growth and yield and, in some cases, the quality of foliage or harvested plant parts. The water source could be groundwater pumped to the surface or surface water diverted from one position on the landscape to another. The development of irrigation water often entails the development of large-scale, geographically significant dams and water impoundments and/or diversions that can provide additional functions apart from crop growth enhancement, e.g., flood control, recreation, or generation of electricity. In many cases, sustainable irrigation development requires concomitant development of surface and/or subsurface drainage.

Rainfall simulation was used to study the vegetative filter strip (VFS) conditions under which losses of total dissolved phosphorus (TDP) and dissolved reactive phosphorus (DRP) leaching occur. Boxes containing silt loam soil were planted with ryegrass and cut at two different intervals prior to simulated rainfall 14 days apart. Grass clippings were either removed or retained. During the second simulated rainfall, runoff TDP and DRP were greater for treatments cut the day before irrigation with clippings retained as compared to treatments cut the same day as irrigation with clippings retained. Removing clippings yielded the lowest mean TDP and DRP concentrations. Increasing the senesced vegetative surface area for contact with water, and the amount of time for leaching to occur, resulted in the greatest DRP loss. The VFS management implications should consider clipping removal or no or reduced mowing during the growing season followed by end-of-season removal to reduce DRP leaching losses.

Half of the original Everglades system has been lost to drainage and development. What remains is included within the boundaries of the Everglades Protection Area (EPA), comprised of three Water Conservation Areas (WCAs) and Everglades National Park (Park). Inflows to the EPA contain elevated nutrient concentrations. Best management practices (BMPs) were implemented and six large wetlands called stormwater treatment areas (STAs) were constructed to improve water quality. We analyzed water quality in the WCAs and Park and performed an economic analysis of the STAs to remove nutrients from EPA inflows. In general, nutrient concentrations in all WCAs were higher during the pre-STA period than after the STAs became operational. In WCA2 and the Park, total phosphorus (TP) trends showed more negative slopes prior, as compared to after, the STAs became operational. These results suggest that BMPs lead to large initial decreases in nutrient export resulting in improved downstream water quality. A preliminary economic analysis shows that operation and management of the STAs are complicated and cost intensive. Comparing the cost of phosphorus (P) removal from water entering the EPA using BMPs and STAs may not currently be viable. BMPs prevent P from being applied to, or leaving from agricultural fields while STAs remove P from stormwater. We expect nutrient concentrations in water flowing into and out of the STAs to decline as both BMPs and STAs become more effective. We suggest an economic analysis of BMPs, STAs, and other potential approaches to determine the most cost-effective methods to reduce nutrient concentrations and related stressors affecting the Everglades.

Water quality was monitored in the Loxahatchee National Wildlife Refuge based on the Consent Decree (CDN), the Enhanced Refuge (ERN), the four-part Test impacted (FPTIN), and the four-part test unimpacted (FPTUN) networks. Alkalinity, dissolved organic carbon, total organic carbon, dissolved oxygen, total dissolved solids, total suspended solids, turbidity, pH, specific conductivity, calcium, chloride, silicon, sulfate, and total phosphorus (TP) were measured from 2005 through 2009. When the ERN was used, the 10 μg TP L−1 Consent Decree limit would have been exceeded and would have ranged from a low of 2 months in 2009 to a high of 9 months in 2005. Based on the CDN, the limit exceeded only for 1 month in each year from 2006 through 2008. Based on the FPTIN, the 10 μg TP L−1 limit would have been exceeded and would have ranged from a low of 1 month in 2007 to a high of 7 months in 2005 and 2008. Based on the CDN, the limit only exceeded for 1 month in each year from 2006 through 2008. Since TP is rapidly removed from canal water intruded into the Refuge marsh, one cannot expect a water quality sampling station located 2 km from the source to reliably detect violations. This may be the primary reason why there have been very few months when TP concentration has exceeded the limit since 1992 or part four of the four-part test annual 15 μg L−1 limit since 2006.

The Loxahatchee National Wildlife Refuge (Refuge) developed throughout millennia as a system with waters low in nutrients. Today, the Refuge wetlands are impacted by inflows containing elevated nutrient concentrations originating from agricultural sources. Surface water samples were collected monthly at 48 marsh and five canal sites from June, 2004 through May, 2011 and analyzed water quality trends by sampling perimeter, transition, and the interior zones based on distance from the canal towards the Refuge interior. Nutrient, inorganic ion, and C concentrations generally decreased with distance from the canal to the Refuge interior. These water quality parameters also decreased from the canal to the Refuge interior, but less sharply. This finding suggests that there has been less canal water intrusion into the Refuge during the sampling period. The origin of the high Ca and Cl concentrations in canal water is most likely from intrusion of connate seawater into the canal. The reason for the improved water quality from June, 2004 to June 2011 can be attributed to an improved STA1-East performance since 2005. Additionally, canal water that originally by-passed treatment in STA1-East and STA1-West, and flowed into the L-7 canal through the S-6 pump, is now diverted farther south into STA2 for treatment.

Anionic polyacrylamide (PAM) is a linear, water-soluble anionic polymer that is widely used for erosion control and water quality protection. There has been an issue whether this formulation could possibly have negative effects on soil microbial diversity by altering microbial binding to soil particles or to one another and thus restricting their mobility and role in carbon and nutrient cycling. We conducted an 8-year study annually applying ultra-high rates of PAM to soil and then monitored impacts on soil bacterial diversity. In July and August, we measured active soil bacterial and fungal biomass and microbial diversity in soils receiving 0 (control), 2,691, and 5,382 kg active ingredient PAM ha−1. Active microbial biomass in soil was 19–33 % greater in the untreated control than soil treated with 2,691 or 5,382 kg of active ingredient PAM ha−1. Active bacterial biomass in soil was 21–31 % greater in the control treatment than in soil treated with 2,691 or 5,382 kg of active ingredient PAM ha−1 in August, but not July. Active fungal biomass in soils was 38–50 % greater in the control treatment than soil treated with 2,691 or 5,382 kg of active ingredient PAM ha−1 in July, but not August. Molecular methods were used to access the bacterial diversity, richness, and evenness in an agricultural soil that received 0 (control), 2,691, and 5,382 kg of active ingredient PAM ha−1. We found that although soil receiving these massive PAM application rates and prolonged exposure may reduce active bacterial and fungal biomass, PAM application did not substantially or consistently affect bacterial structural diversity, richness, or evenness in this agricultural soil.

More than half of the original Everglades system has been lost to drainage and development. What remains is primarily included within the boundaries of the Everglades Protection Area (EPA) comprising three water conservation areas (WCAs) and the Everglades National Park (Park) that receive inflows containing elevated nutrient concentrations. Six large constructed wetlands called stormwater treatment areas (STAs) were constructed to improve water quality. All WCAs and the Park trend analyses indicate that the concentrations of most nutrients in the WCAs and Park are decreasing. In general, nutrient concentrations in all WCAs were higher during the pre-STA period than after the STA became operational. Trend analysis suggests that agricultural best management practices (BMPs) lead to a large initial reduction in nutrient concentrations in the EPA. As STAs were brought online, although still declining, the rate of decline of nutrient concentration in the WCAs was lower than that of the period during initial BMP implementation. Substantially smaller amounts of nutrients from farmland runoff and leaching are being delivered to the STAs for treatment; these results indicate that the STAs may have a limited effect on nutrient concentrations in the WCAs and the Park. However, managers must improve both BMPs and the efficacy of STAs to remove nutrients from water delivered to the EPA if the Everglades ecosystem is to be restored.

The Loxahatchee National Wildlife Refuge (Refuge) is affected by inflows containing elevated contaminant concentrations originating from agricultural and urban areas. Water quality was determined using three networks: the Northern Refuge (NRN), the Southern Refuge (SRN), and the Consent Decree (CDN) monitoring networks. Within these networks, the Refuge was divided into four zones: (1) the canal zone surrounding the marsh, (2) the perimeter zone (0 to 2.5 km into the marsh), (3) the transition zone (2.5 to 4.5 km into the marsh), and (4) the interior zone (>4.5 km into the marsh). In the NRN, alkalinity (ALK) and conductivity (SpC) and dissolved organic carbon, total organic carbon, total dissolved solids (TDS), Ca, Cl, Si, and SO(4) concentrations were greater in the perimeter zone than in the transition or interior zone. ALK, SpC, and SO(4) concentrations were greater in the transition than in the interior zone. ALK, SpC, and TDS values, Ca, SO(4), and Cl had negative curvilinear relationships with distance from the canal toward the Refuge interior (r(2) = 0.78, 0.67, 0.61, 0.77, 0.62, and 0.57, respectively). ALK, TB and SpC, and Ca and SO(4) concentrations decreased in the canal and perimeter zones from 2005 to 2009. Important water quality assessments using the SRN and CDN cannot be made due to the sparseness and location of sampling sites in these networks. The number and placement monitoring sites in the Refuge requires optimization based on flow pattern, distance from contaminant source, and water volume to determine the effect of canal water intrusion on water quality.

The presence of pesticides in groundwater has been documented in several large-scale studies and numerous small-scale investigations. Pesticide leaching through soil has been identified as a major cause for the occurrence of these chemicals in surface and groundwater. We developed matrix-based fertilizers (MBFs) that have been shown to reduce N and P leaching. We tested the efficacy of the ionic bonds in the MBFs to reduce 2,4-dichlorophenoxyacetic acid (2,4-D), metolachlor, thiophanate methyl, carbaryl, diazinon, and malathion leaching in soil columns. After 7 days 2,4-D, thiophanate methyl, carbaryl, and malathion did not leach in sufficient quantities to determine if the MBF fertilizers reduced leaching compared with the control and the slow-release fertilizer Polyon®. The MBF fertilizers leached from five to 30 times less metolachlor than the control and Polyon® treatment. Treatments with MBF fertilizers leached from two to 72 times less diazinon than the control treatment. The MBF fertilizer treatment leached from eight to 268 less diazinon than columns receiving Polyon®. The MBF formulations allow compounds with both anionic and cationic charges to bind with the Al(SO4)3 3H2O and/or Fe2(SO4)3 3H2O-lignin-cellulose matrix. When pesticides are added to the soil amended with matrix-based fertilizers, the ion exchange matrix will likely bind the metolachlor and diazinon to the Al(SO4)3 3H2O and/or Fe2(SO4)3 3H2O-starch-cellulose-lignin matrix thereby substantially reducing leaching. The MBFs could be used to limit both nutrients and pesticide leaching from agricultural fields.

The Loxahatchee National Wildlife Refuge (Refuge) is impacted by inflows containing elevated contaminant concentrations originating from agricultural and urban areas. Water quality was analyzed using the Enhanced Refuge (ERN), the four-part test (FPTN), and the Consent Decree (CDN) monitoring networks within four zones in the Refuge. The zones were defined as the canal surrounding the marsh, the perimeter, the transition, and the interior zones. Although regression coefficients for ALK and SpC, and Ca, Cl, and SO4 concentrations with distance from the canal were lower using the FPTN than when using the ERN, using the FPTN to measure water quality parameters in the Refuge would give similar results as the ERN. Most of the ERN and FPTN sites are located in the northern and central areas of the Refuge. Water is deeper in the southern Refuge, and on an area basis contains a greater volume of water than the northern and central Refuge and therefore, water flow from the canal into the marsh in the northern and southern Refuge may differ. Numerous water quality monitoring sites must be added to the ERN and FPTN in the southern area to characterize water quality in the southern Refuge with confidence.

The Loxahatchee National Wildlife Refuge (Refuge) developed as a system with waters low in nutrients. Today, the Refuge wetlands are impacted by inflows containing elevated nutrient concentrations originating from agricultural sources. We analyzed water quality sampled at 54 sites in the Refuge. The Refuge was divided into northern, central, and southern latitudinal areas and then perimeter, transition, and the interior zones based on distance from the canal towards the Refuge interior. In the perimeter zone, total dissolved solids (TDS), silicon (Si), and total phosphorus (TP) concentrations in water were higher in the northern than the central area and TDS, Si, SO4, and TP concentrations in water were higher in the central than the southern area. In general TDS, Ca, Cl, Si, SO4, and TP loads in the northern perimeter, transition, and interior zones decreased from 2005 to 2009. The decrease is less pronounced in the central and southern areas than the northern area. As water flowed southward for over 30 km from the northern to the southern area in the perimeter zone, most water quality parameters analyzed were reduced in the water column. However, large amounts of Ca and Cl were added to the water column indicating that canal water is continually diffusing and intruding into the Refuge in all zones. In the perimeter zone, and to a lesser degree in the transition zone, the Refuge has accumulated substantial amounts of Ca, Si, SO4, and TP in vegetation and soils during the sampling period.

The Loxahatchee National Wildlife Refuge (Refuge) developed as a system with waters low in nutrients. Today, the Refuge wetlands are impacted by inflows containing elevated nutrient concentrations originating from agricultural sources flowing into canals surrounding the west side and from urban and horticultural areas flowing into canals surrounding the eastern side of the Refuge. We analyzed water quality sampled at 40 sites divided into eastern and western areas and four zones in the Refuge. We defined four zones as the canals surrounding the Refuge marsh, the perimeter zone, the transition zone, and the interior zone. The canal receiving agricultural inflows had greater alkalinity and conductivity (SpC), Si and SO4 but lower turbidity and total suspended solids than the canal receiving urban and horticultural inflows. Alkalinity, total dissolved solids (TDS), SpC, Ca, Cl, and SO4 concentrations were greater in the perimeter than in transition and interior zones. Alkalinity and SpC values and SO4 concentrations were greater in the transition than in interior zone. Alkalinity, SpC, and TDS values and Ca, SO4, and Cl concentrations correlated in negative curvilinear relationships with distance from the canal (r (2) = 0.78, 0.70, 0.61, 0.78, 0.64, 0.57, respectively). Analysis of multiple water quality parameters may reveal the complexity of interactions that might be overlooked in a simple single parameter analysis. These data show an impact of canal water containing high nutrient concentrations on water quality flowing from the canal towards the Refuge interior.

The influence of manure application to pasture soils on bacterial and fungal biomass and the atrazine (2 chloro-4[ethylamino]-6[isopropylamino]-s-triazine) and 2,4-D (2,4 dichlorophenoxyacetic acid) mineralization was assessed in microcosms using radiometric techniques. Additions of 5 tonnes manure ha(-1) yr(-1) were made to three pasture soils over 20 yr in western Oregon at a rate of 0.42 t ha(-1) each month. No manure or fertilizer was added to control treatments. We found greater amounts of total fungal and bacterial biomass in soils that received added manure. There were no differences among active bacterial and fungal biomass between pasture soils that received manure application and pasture soils that received no manure. Greater amounts of atrazine and 2,4-D were mineralized when manure was applied than when soil received no manure or fertilizer. Greater amounts of atrazine and 2,4-D were mineralized in the spring than in summer, fall or winter. Results of this study indicate that the application of dairy manure to pasture soils will significantly increase herbicide degradation rates.

We tested the efficacy of matrix-based fertilizers (MBFs) to reduce Escherichia coli and Enterococcus spp., NH(4), NO(3), dissolved reactive phosphorus (DRP), and total phosphorus (TP) in leachate and soil after dairy manure application in greenhouse column studies. The MBFs are composed of inorganic N and P in compounds that are relatively loosely bound (MBF8) to more tightly bound (MBF9) mixtures using combinations of starch, cellulose, lignin, Al(2)(SO(4))(3)18H(2)O, and/or Fe(2)(SO(4))(3)3H(2)O to create a matrix that slowly releases the nutrients. One day after the first dairy manure application, E. coli numbers were greater in leachate from control columns than in leachate from columns receiving MBFs. After three dairy manure applications, E. coli and Enterococcus spp. numbers in leachates were not consistently different between controls and columns receiving MBFs. When MBF8 was applied to the soil, the total amount of DRP, TP, NH(4), and NO(3) in leachate was lower than in the control columns. Bermudagrass receiving MBFs had greater shoot, root, and total biomass than grass growing in the control columns. Grass shoot, root, and total biomass did not differ among columns receiving MBFs. Nitrogen and phosphorus bound to the Al(2)(SO(4))(3)18H(2)O or Fe(2)(SO(4))(3)3H(2)O-lignin-cellulose matrix become gradually available to plants over the growing season. The MBF8 and MBF9 formulations do not depend on organic or inorganic coatings to reduce N and P leaching and have the potential with further testing and development to provide an effective method to reduce N and P leaching from soils treated with animal waste.

We measured Escherichia coli, and Enterococcus sp. numbers in soil and on fresh radish (Raphanus sativus L.) at 1, 7, 14, 28, 54, and 84 days after the addition of high and low amounts of solid dairy manure in combination with chisel tillage to a 20 cm depth (deep) or roller tillage to a 10 cm depth (shallow). When the high or low amount of solid dairy manure was added to the soil, E. coli populations in soil were higher in the 54 days following manure addition compared to the control treatment. Dairy manure addition increased Enterococcus sp. in soils compared to the control treatment for the entire 84 days sampling period. At harvest, which was 84 days after application, we did not detect E. coli in radish in rhizosphere soil or on radish roots. Addition of solid dairy manure increased Enterococcus sp. numbers in radish rhizosphere soil and on radish roots. We suggest that fresh animal manure be applied to soil at least 120 days prior to planting to allow die-off of human pathogenic bacteria and reduce the incidence of bacterial adhesion on or bacterial colonization of ready to eat vegetables.