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F7Evapotraonspiration was not factored in the nitrate loading methods. However, Eto will be a art of wastewater management and consequently nitrate-nitrogen loading through cover uptake. e effluent and soil environment under the disposal fields may be a requirement of EHD. If higher than expected nitrate-nitrogen impact is observed, EHD may require a denitrification mitigation system to be installed. In addition, monitoring may also be required of the new domestic well for the Church Complex. A careful accounting of the water usage must be done to properly manage the wastewater disposal system. Therefore, it is recommended that a flowmeter be placed in the fresh water supply from the domestic well. Since the wastewater effluent will be pressurized for both the drip irrigation and conventional leachlines, a flowmeter placed after the effluent pump will record wastewater flow volumes for comparison with domestic irrigation water use. To keep organic loading to a minimum, garbage disposals (grinders) cannot be installed in the Church or Multipurpose Building kitchens. Additionally, due to the indigenous clay soils, water softeners also cannot be installed. The sodium liberated by water softeners will disperse and deflocculate the clay lattice soil structure and render the clay soil completely impermeable. Regarding the nitrate-nitrogen loading to the underlying groundwater, it is important to recognize that when adding one concentration of a solute (e.g.,NO3 N in wastewater recharge) to another concentration of a solute (e.g., NO3 N in groundwater),where both solutes are in ppm, the result is not cumulative or the sum of the two solutes. Parts per million is amass ratio (mg per106 mg). For example, the Nr(the resultant average concentration of nitrate-nitrogen in wastewater recharge in ppm of NO3-N), was determined to be 7.4 ppm by the Hantzsche-Finnemore Equation. This equals 7.4 milligrams of nitrate in 106 milligrams of water(one liter). If this 7.4 ppm concentration is added to the same volume of water(1 x 106 milligrams) of the concentration determined in the underlying water table, which was 19.6 ppm NO3 N (88 ppm NO3), then the resultant concentration is now: 7.4 milligrams per liter+ 19.6 milligrams per liter=27 milligrams in 2 x 106 milligrams (2 liters, or parts per 2 million) of water. Therefore, to convert back to ppm, the numerator and denominator must be divided by 2 with the result of 13.5 milligrams per 1 x 106 milligrams, or 13.5 ppm NO3-N. On a mass ratio basis, there will be a dilution effect of the nitrate concentration in the water table from the resultant recharge wastewater(Nr) as long as the unconfined water table aquifer has a higher nitrate concentration than the recharge water(32.9 ppm NO3 recharge vs. 88 ppm NO3 water table). Consequently, degradation of the waters of the State of California do not occur in violation of the Porter-Cologne Water Act. Sources contributing nitrate to the underlying groundwater in this locale include indigenous soil concentrations from decomposing organic matter, lightning/rainfall,past and present upgradient agricultural fertilizer inputs, septic systems (particularly sumps and pits), lawn/landscape fertilization and naturally occurring geological deposits. Of these sources; however, it appears that only past and present upgradient agricultural fertilizer inputs, decomposing organic matter and naturally occurring geological deposits are contributing nitrate to the groundwater underlying the Church property. Factors decreasing the groundwater nitrate concentration include denitrification, groundwater movement(both vertical and horizontal), well pumping and hydraulics, and cleaner water recharge contributing to a dilution effect. Page -24- Chesney Consulting