Accounting for potassium and magnesium in irrigation water quality assessment.
Recycled wastewaters generated by municipalities and farms in California are being reused increasingly for irrigation, both to expand available water resources and to avoid discharge to surface waters, with the current statewide goal being to reuse 2.5 million acre-feet of wastewater by 2030 (Weber et al. 2014). However, the high salinity and sodium (Na) concentrations characteristic of recycled wastewaters pose a significant challenge to their sustainable reuse for crop production (Assouline et al. 2015; Laurenson et al. 2012; Platts and Grismer 2014a, 2014b). Adding to this challenge, several recent studies (Arienzo et al. 2012; Buelow et al. 2015; Marchuk et al. 2013; Rengasamy and Marchuk 2011; Smith et al. 2015) have documented deleterious effects on soil hydraulic properties caused by high concentrations of potassium (K) and magnesium (Mg), which are typical of recycled wastewaters (Buelow et al. 2015; Laurenson et al. 2012; Weber et al. 2014). The potential consequences include negative impacts on infiltration, water availability and plant growth. Buelow et al. (2015), who investigated California soils, in particular have called for further research to understand the high-risk scenarios that may arise when irrigating with potassium-rich wastewaters. We note in passing that recycled wastewaters are not the only concern of the kind discussed here. High concentrations of Mg occur naturally in groundwater in and near the Coast Range in California because of their serpentine geology (Ben Faber and Mark Battany, UC ANR Cooperative Extension, personal communication, 2015).
High concentrations of potassium and magnesium are typically found in recycled wastewaters and can have negative impacts on infiltration, water availability and plant growth. [Graphic omitted]
All of the studies cited indicated that the negative impacts of K and Mg on the saturated soil hydraulic conductivity place them between the extremes of Na as the worst soil dispersant and calcium (Ca) as the best soil flocculant: Na > K > Mg > Ca. In general, flocculation has a positive impact on soil permeability while dispersion has a negative impact. Although this ordering of negative impacts on soil hydraulic properties among the four cations was documented quantitatively 60 years ago (Quirk and Schofield 1955) and has often been discussed in reviews (Keren 1984; Levy 2012), it has not yet been incorporated into standard irrigation water quality criteria. As noted by Rengasamy and Marchuk (2011) and Buelow et al. (2015), the need to do this has become urgent because of increasing need to reuse wastewaters for irrigation, which is expected to grow exponentially in California during the next few decades (Weber et al. 2014).
In respect to the impacts of Na on soil permeability, the sodium adsorption ratio (SAR) has long been the standard diagnostic parameter for sodicity hazard (U.S. Salinity Laboratory Staff 1954):
where each chemical element symbol indicates a concentration in millimoles of charge per liter (mmolc/L). SAR can be related through rigorous thermodynamic arguments to the exchangeable sodium percentage (Oster and Sposito 1980), a key soil property impacting permeability (Bresler et al. 1982; Keren 1984; Levy 2012; Shainberg and Letey 1984). Similarly, a potassium adsorption ratio (PAR) has been defined with K concentration replacing that of Na (U.S. Salinity Laboratory Staff 1954); but, as noted above, there are as yet no guidelines based on PAR in standard reference publications related to irrigation water quality assessment (Ayers and Westcot 1985; Rhoades et al. 1992; Tanji and Kielen 2002; Tyagi and Minhas 1998; Wallender and Tanji 2012). (See sidebar, 'Development of water quality guidelines for irrigated agriculture in California.')
CROSS, a new irrigation water quality parameter
Building on earlier conceptual work by Rengasamy and Sumner (1998), Rengasamy and Marchuk (2011) have proposed a generalization of SAR which quantifies both the differing effects of Na and K as dispersing cations diminishing soil permeability and the differing effects of Mg and Ca as flocculating cations enhancing soil permeability. This new parameter, the cation ratio of structural stability (CROSS), incorporates the inverse of the critical flocculation (or coagulation) concentration (Rengasamy and Sumner 1998; Sposito 2008) for a cation as a measure of its 'relative flocculating power,' which is taken as a chemical basis for distinguishing cations that promote soil particle aggregation from those that promote soil particle dispersion. Rengasamy and Sumner (1998) reported critical flocculation concentrations (CFCs) for Na-, K-, Mg- and Ca-saturated clays extracted from four soils, which they then used to calculate the average relative flocculating power of each cation by dividing its average CFC for the four soils into the average CFC for Na-clay, taken as a reference. Compared to Na, the average relative flocculating power of K, Mg and Ca for the four soils was found to be 1.8 [+ or -] 0.3, 27 [+ or -] 5 and 45 [+ or -] 8, respectively. Thus a measure of the dispersing power of K relative to Na would be 1.0/1.8 = 0.56 and a measure of the flocculating power of Mg relative to Ca would be 27/45 = 0.60. Rengasamy and Marchuk (2011) then proposed the following generalization of SAR:
where we have added a subscript f to indicate that the two numerical coefficients in CROSS are based on the relative flocculating power of K and Mg. Rengasamy and Marchuk (2011) tested CROSS[sub.f] as a diagnostic water quality parameter by comparing it to SAR in obtaining high correlation with the percent dispersible clay in four Australian soils. Although SAR did correlate significantly with percent dispersible clay, the correlation with CROSSf was greatly superior. Similarly, Marchuk and Rengasamy (2012) reported a highly significant linear correlation between CROSSf and the salt concentration (expressed conventionally as electrical conductivity) required to flocculate three Australian soils. They concluded that, by including the dispersive effects of K in addition to Na and differentiating the flocculating effects of Mg from Ca, CROSSf performed better than SAR in predicting soil clay dispersion and flocculation.
Additional insight into the significance of CROSS can be had by generalizing Equation (2):
where a and b are numerical coefficients to be determined by a suitable method and
are generalizations of SAR and PAR, respectively. According to the ordering of negative cation impacts on soil permeability as determined by Quirk and Schofield (1955), Na > K > Mg > Ca. (See sidebar, 'Why do cations with the same valence have different effects on soil permeability?') Therefore, the coefficients a and b in Equation (3) are both expected to have values < 1, as they do in Equation (2). Equation (3) suggests further that CROSS can be interpreted as the weighted sum of a generalized SAR and PAR, with the weighting factor a < 1 interpreted as a measure of the lesser negative impact of PAR∗ on soil permeability relative to SAR∗. The coefficient b < 1 can be interpreted as a multiplier of the actual concentration of Mg to produce an 'effective concentration' of Mg. This smaller effective concentration reflects the lower flocculating power of Mg relative to Ca. Evidently the concentration of Mg in an irrigation water would have to be 1/b times larger than that of Ca so as to have the same positive impact as Ca on soil permeability. Since b < 1, SAR < SAR∗ and PAR < PAR∗, which implies that CROSS ≥ SAR for any water composition. Therefore, the use of CROSS as a diagnostic tool to evaluate irrigation water quality according to standard criteria (Ayers and Westcot 1985) will result in a more conservative assessment of potential soil management problems. (See sidebar, 'Using CROSS to assess irrigation water quality.')
In their seminal study of cation effects on soil permeability, Quirk and Schofield (1955) defined the cation concentration low enough to result in a 10% to 15% reduction in the saturated hydraulic conductivity, after leaching with water of known composition for a prescribed time-period, as the threshold concentration (TEC). The TEC is a widely adopted, convenient measure of the impact of cations on soil permeability (Buelow et al. 2015; Quirk 2001; Shainberg and Letey 1984). Accordingly, we tested Equation (3) as a diagnostic water quality parameter by examining how well it correlates with TEC values we calculated (table 4) using laboratory data reported by Jayawardane et al. (2011) and Arienzo et al. (2012) for a Sodosol from the Riverina region of Australia which had been irrigated with winery wastewater (Smith et al. 2015). Like many irrigated California soils, this soil is high (> 50%) in smectite clay minerals and has alkaline pH (> 8), with a surface horizon of clay loam texture overlying a subsurface horizon of medium clay texture.
A linear correlation between CROSSf in Equation (2) and the TEC values in table 4 is shown in figure 1A. This correlation is good enough to confirm the hypothesis that negative soil permeability effects of K and Mg are important. Figure 1B shows the much-improved linear correlation between the generalized CROSS in Equation (3) and TEC that we obtained using an optimization technique to provide best-fit values of the coefficients a and b (Duan et al. 1993; Rosenbrock 1960). The optimized CROSS is:
where 'opt' designates optimization. Comparison of figure 1A with figure 1B shows that use of Equation (6) instead of Equation (2) improves the correlation of CROSS with TEC dramatically.
TABLE 4: Sodium (SAR) and potassium adsorption ratio (PAR), threshold concentration (TEC) and cation concentrations in applied water leading to a 15% reduction in the saturated hydraulic conductivity of surface and subsurface layers in a calcareous soil from the Riverina region of Australia [Table omitted]
Fig. 1: Correlations between the cation ratio of structural stability (CROSS), with the coefficients for K and Mg based on their (A) relative flocculating power (CROSS[sub.f]) or (B) statistically optimized (CROSS[sub.opt]), and the threshold concentration (TEC, mmol[sub.c]/L) in applied water leading to a 15% reduction in the relative saturated hydraulic conductivity of a calcareous soil from the Riverina region of Australia (Arienzo et al. 2012). RMS represents the root-mean-square. [Figure omitted]
The optimized values of the coefficients a and b in Equation (6) can be interpreted chemically as follows. The electrolyte concentration required to cause flocculation of soil clays is usually considerably greater than that which results in the dispersion of soil clays (Quirk 2001). In light of this fact, the TEC values for Na and K reported by Quirk and Schofield (1955), which relate to soil clay dispersion, might be better suited to estimate the a coefficient in CROSS than the CFC values Rengasamy and Marchuk (2011) used. Under this hypothesis, the value for a should equal the ratio of TEC for K (67 mmol[sub.c]/L) to that for Na (250 mmol[sub.c]/L) as determined by Quirk and Schofield (1955), which is 0.27. The optimized value of a in Equation (6), which indicates the dispersive power of K to be about one-third that of Na, is consistent with this estimate.
Our optimized b coefficient, however, is not approximately equal to a, as it is in Equation (2). Following the discussion given above, its very small value implies that the concentration of Mg needs to be about an order of magnitude larger than that of Ca in order to have the same positive effect as Ca in promoting soil flocculation. This large difference can, in fact, be deduced from directly examining the data in table 4. For example, the TEC values associated with SAR40 Ca and SAR40 Mg are 66.0 and 517.0 mmol[sub.c]/L, respectively. Here the coefficient a plays no role; the coefficient b (and, therefore, Mg) is solely responsible for the second, much larger value of TEC. According to Equation (6), CROSSopt for TEC = 517 mmolc/L is equal to 147. In this case CROSSopt is equal to SAR∗. Since SAR = 40, SAR∗ is 3.67 times larger than SAR, implying b = 0.0743, which agrees with the optimized value.
Sixty years of research on soil permeability as affected by irrigation water quality have established that the decreasing order of negative impacts of the four major cations follows the sequence: Na > K > Mg > Ca. Current irrigation water quality guidelines (Ayers and Westcot 1985) omit K entirely and consider Mg to have no negative impacts on soil hydraulic properties. The new irrigation water quality parameter, CROSS (Rengasamy and Marchuk 2011), a generalization of SAR, accounts for the negative impacts of K and Mg on soil permeability. We found an excellent correlation between a suitably optimized CROSS and TEC, a standard measure of the reduction in soil permeability under leaching, for a Sodosol irrigated with winery wastewater having significant concentrations of K and Mg (fig. 1B). Thus we propose the substitution of CROSS for SAR in irrigation water quality guidelines as a generalization of sodicity hazard to include the relative deleterious impact on soil hydraulic properties of the four common cations.
Aylmore LAG, Sills JD. Characterization of soil structure and stability using modulus of rupture-exchangeable sodium percentage relationships. Aust J Soil Res 1982. 20 :213-24. 10.1071/SR9820213
Arienzo M, Christen EW, Jayawardane NS, Quayle WC. The relative effects of sodium and potassium on soil hydraulic conductivity and implications for winery wastewater management. Geoderma 2012. 173-174 :303-10.
Assouline S, Russo D, Silber A, Or D. Balancing water scarcity and quality for sustainable irrigated agriculture. Water Resour Res 2015. 51 :3419-36. 10.1002/2015WR017071
Ayers RS, Westcot DW. Water quality for agriculture. FAO Irrig. Drain. Pap. 29, Rev.1. 1985. Rome, Italy:FAO.
Bresler E, McNeal BL, Carter DL. Saline and Sodic Soils 1982. Berlin, Germany:Springer-Verlag.
Buelow MC, Steenwerth K, Parikh SJ. The effect of mineral-ion interactions on soil hydraulic conductivity. Agr Water Manage 2015. 152 :277-85. 10.1016/j.agwat.2015.01.015
Dontsova KM, Norton LD. Clay dispersion, infiltration and erosion as influenced by exchangeable Ca and Mg. Soil Sci 2002. 167 :184-93. 10.1097/00010694-200203000-00003
Duan QY, Gupta VK, Sorooshian S. Shuffled complex evolution approach for effective and efficient global minimization. J Optimiz Theory Appl 1993. 76 (3) :501-21. 10.1007/BF00939380
Fireman M, Bodman GB. The effect of saline irrigation water upon the permeability and base status of soils. Soil Sci Soc Am Proc 1939. 4 :71-7.
Jayawardane NS, Christen EW, Arienzo M, Quayle WC. Evaluation of the effects of cation combinations on soil hydraulic conductivity. Soil Res 2011. 49 :56-64. 10.1071/SR09222
Horn CP. The effect of cations on soil structure. Dip. Agr. Sci 1983. Armidale, Australia:University of New England. Thesis
Keren R. Shainberg L, Shal-hevet J. Potassium, magnesium, and boron in soils under saline and sodic conditions. Soil Salinity under Irrigation: Processes and Management 1984. Berlin, Germany:Springer-Verlag. 7799.
Laurenson S, Bolan NS, Smith E, McCarthy M. Use of recycled wastewater. Aust J Grape and Wine Res 2012. 18 :1-10. 10.1111/j.1755-0238.2011.00170.x
Lesch SM, Suarez DL. A short note on calculating the adjusted SAR index. Amer Soc Agric Eng 2009. 52 (2) :493-6.
Levy GJ. Huang PM, Li Y, Sumner ME. Sodicity. Handbook of Soil Sciences 2012. 2nd ed. Boca Ratón, FL:CRC Press. Resource Management and Environmental Impacts. Chap. 18
Levy GJ, vander Watt HvH. Effect of exchangeable potassium on the hydraulic conductvity and infiltration rate of some South African soils. Soil Sci 1990. 149 :69-77. 10.1097/00010694-199002000-00002
Marchuk A, Rengasamy P, McNeill A, Kumar A. Nature of the clay-cation bond affects soil structure as verified by X-ray computed tomography. Soil Res 2013. 638 :44-50.
Oster JD, Sposito G. The Gapon coefficient and the exchangeable sodium percentage-sodium adsorption ratio relation. Soil Sci Soc Am J 1980. 44 :258-60. 10.2136/sssaj1980.03615995004400040024x
Platts BE, Grismer ME. Chloride levels increase after 13 years of recycled water use in the Salinas Valley. Calif Agr 2014a. 68 (3) :68-74.
Platts BE, Grismer ME. Rainfall leaching is critical for long-term use of recycled water in Salinas Valley. Calif Agr 2014b. 68 (3) :75-81.
Quirk JP. The significance of the threshold and turbidity concentrations in relation to sodicity and microstructure. Aust J Soil Res 2001. 39 :1185-1217. 10.1071/SR00050
Quirk JP, Schofield RK. The effect of electrolyte concentration on soil permeability. J Soil Sci 1955. 6 :163-78. 10.1111/j.1365-2389.1955.tb00841.x
Reeve RC, Bower CA, Brooks RH, Gwchwend FB. A comparison of the effects of exchangeable sodium and potassium upon the physical condition of soils. Soil Sci Soc Am Proc 1954. 18 :130-2. 10.2136/sssaj1954.03615995001800020004x
Rengasamy P, Sumner ME. Sumner ME, Naidu R. Processes involved in sodic behaviour. Sodic Soil: Distribution, Properties, Management and Environmental Consequences 1998. New York:Oxford University Press. 3550.
Rengasamy P, Marchuk A. Cation ratio of soils structural stability (CROSS). Soil Res 2011. 49 :280-5. 10.1071/SR10105
Rhoades JD, Kandiah A, Mashali AM. The use of saline waters for crop production. FAO Irrig. Drain. Pap. 48. 1992. Rome, Italy:FAO.
Rosenbrock HH. An automatic method for finding the greatest or least value of a function. Computer J 1960. 3 :175-84. 10.1093/comjnl/3.3.175
Shainberg I, Letey J. Response of soils to sodic and saline conditions. Hilgardia 1984. 52 (2) :1-57. 10.3733/hilg.v52n02p057
Smith CJ, Oster JD, Sposito G. Potassium and magnesium in irrigation water quality assessment. Agr Water Manage 2015. 157 :59-64. 10.1016/j.agwat.2014.09.003
Sposito G. The Chemistry of Soils 2008. 2nd ed. New York:Oxford University Press.
Suarez DL. Relation between pHc and Sodium Adsorption Ratio (SAR) and an alternate method of estimating SAR of soil or drainage waters. Soil Sci Soc Amer J 1981. 45 :469-75. 10.2136/sssaj1981.03615995004500040020x
Tanji KK, Kielen NC. Agricultural drainage water management in arid and semi-arid areas. FAO Irr. Drain. Pap. 61. 2002. Rome, Italy:FAO.
Tyagi NK, Minhas PS. Agricultural salinity management in India. 1998. Karnal, India:Soil Salinity Research Institute.
U.S. Salinity Laboratory Staff. Diagnosis and Improvement of Saline and Alkali Soils. Handbook No. 60. 1954. Washington, DC:USDA.
Vyshpolsky F, Mukhamedjanov K, Bekbaev U, et al. Optimizing the rate and timing of phosphogypsum application to magnesium-affected soils for crop yield and water productivity enhancement. Agric Water Manage 2010. 97 :1277-86. 10.1016/j.agwat.2010.02.020
Wallender WW, Tanji KK. ASCE Manuals and Reports on Engineering Practice No. 71. Agricultural Salinity Assessment and Management 2012. Reston, VA:American Society of Civil Engineers.
Weber E, Grattan SR, Hanson BR, et al. Recycled water causes no salinity or toxicity issues in Napa vineyards. Calif Agr 2014. 68 (3) :59-67. 10.3733/ca.v068n03p59
Zhang XC, Norton LD. Effect of exchangeable Mg on saturated hydraulic conductivity, disaggregation and clay dispersion of disturbed soils. J Hydrol 2002. 26 :194-205.
J.D. Oster is Emeritus Specialist, Department of Environmental Sciences, UC Riverside; G. Sposito is Chancellor's Professor, Emeritus, Department of Environmental Science, Policy and Management, UC Berkeley; C.J. Smith is Fellow, CSIRO Agriculture, Canberra, Australia.
Support for Dr. Smith was provided by the Australian Water Recycling Centre of Excellence and the CSIRO Water for a Healthy Country Research Flagship, and Dr. Sposito was supported in part by an appointment as Chancellor's Professor, Emeritus, administered through the College of Natural Resources, UC Berkeley.
We thank California Agriculture Associate Editor Dr. K. Bali and two reviewers for their helpful comments on a draft version of this paper, as well as Nat Dellavalle, whose comments to Dr. J.D. Oster about permeability problems of a soil caused by high levels of K was the 'spark' that initiated our work with CROSS.
Development of water quality guidelines for irrigated agriculture in California
The quality of water for irrigated agriculture is based on the effect the water can have on crop growth and on soil permeability. The salt concentration in irrigation water is the primary factor that affects crop growth: water quality decreases as the salt concentration increases. Water quality impacts on soil permeability are more complicated. Two opposing factors need to be considered: salt concentration, as estimated conventionally by electrical conductivity (EC), and sodicity hazard, as reflected in the sodium adsorption ratio (SAR), which is calculated according to Equation (1) using the concentrations of Na, Ca and Mg in the irrigation water. The effects of EC and SAR on soil permeability are opposite to one another: permeability increases with increasing EC, whereas permeability decreases with increasing SAR. Consequently, soil permeability is maintained by an optimal combination of high EC and low SAR. The irrigation water quality guidelines based on this optimization that are used to assess possible negative impacts on soil permeability (table 1) are those proposed by Ayers and Westcot (1985).
These well-known guidelines omit K from consideration. One reason for this omission is that Na concentrations in irrigated soils are usually much higher than those of K, but the more important reason is that the iconic USDA Handbook 60 (U.S. Salinity Laboratory Staff 1954) concludes that 'exchangeable K has only a slight or no adverse effect upon the physical properties of soils.' This conclusion was influenced by 'measurements made recently at the Laboratory on samples of seven soils adjusted to various levels of exchangeable sodium and exchangeable potassium (Fig. 1).' The cited Fig. 1 displays the ratio of air permeability to water permeability as a function of both exchangeable sodium percentage (ESP) and exchangeable potassium percentage (EPP). This ratio increases exponentially with ESP, whereas for EPP there is no increase for three of the seven soils examined, while the increase is small for the other four. In parallel with this perspective concerning K, Mg was considered to have positive effects equal to those of Ca on soil permeability, leading Handbook 60 to group the two bivalent cations together in promoting and maintaining good soil structure. Bresler et al. (1982) have noted, however, that this customary grouping in fact may not reflect the true status of Mg, which, like K, is typically masked by the two- to fivefold greater concentration of Ca over Mg in irrigation waters.
TABLE 1: Interpretive guidelines for assessing the combined effect of SAR and EC in irrigation water on soil infiltration problems [Table omitted]
Interestingly, at about the same time that Handbook 60 was discounting K when assessing the impacts of irrigation water quality on soil permeability, it was becoming known that the negative impact on soil permeability of K was in fact not negligible and that the positive impacts of Ca and Mg on permeability were not equal. Quirk and Schofield (1955), inspired by research on the effects of salt concentration on the permeability of agricultural soils in California (Fireman and Bodman 1939), reported what appears to be the first systematic investigation to quantify the separate effects of Na, K, Mg and Ca on the saturated soil hydraulic conductivity. They equilibrated soil pads with concentrated Cl solutions of Na, K, Ca or Mg, then leached the pads with a series of more dilute Cl solutions of the same cation. Their results showed decreases in the hydraulic conductivity over a 5-hour period of leaching which clearly depended on the type of cation. The magnitude of these decreases followed the order: Na > K > Mg > Ca.
|Printer friendly Cite/link Email Feedback|
|Author:||Oster, J.D.; Sposito, Garrison; Smith, Chris J.|
|Date:||Apr 1, 2016|
|Previous Article:||Precision overhead irrigation is suitable for several Central Valley crops.|
|Next Article:||Community and home gardens increase vegetable intake and food security of residents in San Jose, California.|