| HOME | HELP | FEEDBACK | SUBSCRIPTIONS | ARCHIVE | SEARCH | TABLE OF CONTENTS |
|
|
|
|||||||
|
|||||||||
a Department of Plant and Soil Sciences, Oklahoma State University, Stillwater, OK 74078
b School of Natural Resources, The Ohio State University, Columbus, OH 43210
c Veterinary Medicine Diagnostic Laboratory, University of Missouri-Columbia, Columbia, MO 65205
d Department of Statistics, Oklahoma State University, Stillwater, OK 74078
* Corresponding author (basta.4{at}osu.edu).
Received for publication February 2, 2003.
 |
ABSTRACT |
|---|
 TOPNOTES ABSTRACT INTRODUCTIONMATERIALS AND METHODSRESULTS AND DISCUSSIONCONCLUSIONSREFERENCES |
|---|
Abbreviations: GE, gastric extraction • IE, intestinal extraction • IVG, in vitro gastrointestinal • PBET, physiologically based extraction test • SRM, standard reference material
|
INTRODUCTION |
|---|
|
TOPNOTESABSTRACTINTRODUCTIONMATERIALS AND METHODSRESULTS AND DISCUSSIONCONCLUSIONSREFERENCES |
|---|
Lead is considered a possible human carcinogen by the International Agency for Research on Cancer (2002) as well as a probable human carcinogen by the United States Environmental Protection Agency (USEPA, 1996b). Human exposure to Pb can occur through the consumption of contaminated foods or drinking water, incidental ingestion of soil or dust, inhalation of Pb-containing particles from ambient air, ingestion of paint chips from Pb-painted surfaces, use of medications in the form of folk remedies, inhalation of automobile emissions, or from working in occupations involving exposure to Pb fumes and dust (Adriano, 2001, p. 349–410; United States Department of Health and Human Services, 1999). Lead is a toxic element, and exposure results in a variety of effects in humans. In both adults and children, the main target of lead toxicity is the central nervous system (United States Department of Health and Human Services, 1999). Acute exposure to high levels of Pb may result in gastrointestinal symptoms (cramping, colicky abdominal pain, nausea, and vomiting), brain damage, kidney damage, lowered sperm production, miscarriages, and possibly death. Chronic exposure to Pb may result in effects on the blood (anemia), central nervous system (CNS), blood pressure, kidneys, and vitamin D metabolism (United States Department of Health and Human Services, 1999). Central nervous system effects on adults consist of subtle behavior changes, fatigue, and impaired concentration. Children are more susceptible to Pb exposure because they absorb and retain approximately 50% more in proportion to their body weight (Mushak et al., 1989). Exposure of children to Pb may result in impaired neurological development (both cognitive and behavioral) as evidenced by deficits in intelligence scores, speech and language processing, attention, and classroom performance (da la Burde and Choate, 1972; Grant and Davis, 1989; Needleman et al., 1979, 1990; Rummo et al., 1979; Winneke, 1995).
Lead is ubiquitous in the environment primarily as a result of anthropogenic activities; the United States Department of Health and Human Services (1999) estimates that 89.4% of the total environmental release of Pb in 1996 (including Pb going to landfills) was to soil. Lead ranks first on the priority list of hazardous substances found at Superfund sites (based on its frequency at sites, its toxicity, and its potential for human exposure) and has been identified in soils from 675 of the 1026 National Priorities List (NPL) hazardous waste sites (Adriano, 2001, p. 349–410; United States Department of Health and Human Services, 1999). Concentrations as high as 60000 mg kg–1 have been reported in soils adjacent to a smelter in Missouri (Palmer and Kucera, 1980). Additionally, soils adjacent to Pb-painted houses may contain >10000 mg kg–1 (USEPA, 1986). The incidental ingestion of soil by children is an important pathway in the assessment of public health risks due to exposure of metal-contaminated soils. Most risks from Pb in ingested soil or waste materials are associated with the fraction of the soil or waste material that is available for absorption from the gastrointestinal tract into the circulatory system. The amount of Pb absorbed through the gastrointestinal tract (bioavailable Pb) may be described in absolute or relative terms. Absolute bioavailability (ABA), also referred to as the oral absorption fraction, is equal to the absorbed dose/ingested dose as described by Eq. [1]:
 | [1] |
Relative bioavailability (RBA) is the ratio of the ABA of Pb present in some test material (study soil) compared with the ABA of Cd in an appropriate reference material (Eq. [2]):
 | [2] |
Lead acetate, a readily soluble form of Pb and thus easily absorbed from the gastrointestinal tract, is used as the reference material in the critical toxicity study reported in the Integrated Risk Information System (IRIS; USEPA, 1996b). Relative bioavailability can be determined experimentally without specifically measuring absolute bioavailability. For example, the tissue concentration of Pb in animals dosed with study soil can be compared with tissue concentration of Pb in animals dosed with reference material. In this case, relative bioavailability is defined by Eq. [3]:
 | [3] |
Often, baseline risk assessments used for contaminated sites assume that the relative bioavailability of Pb in soil is 60%, which is the default value used by the Integrated Exposure and Uptake Biokinetic (IEUBK) model for lead in children (USEPA, 1994). However, because of the different geochemical and physical forms of Pb present in contaminated soils and waste, the relative bioavailability of Pb may be different than the default IEUBK value.. Therefore, a more accurate estimation of the relative bioavailability of metal contaminants (e.g., Pb and As) in waste materials from hazardous waste sites has been assessed using in vivo animal dosing trials and used for risk assessment.
Less expensive in vitro chemical extraction methods that simulate gastrointestinal biochemistry have been developed to estimate relative bioavailable Pb (Ellickson et al., 2001; Hamel et al., 1998; Ruby et al., 1992, 1996), As (Rodriguez et al., 1999), and Cd (Schroder et al., 2003). The amount of contaminant dissolved in the gastrointestinal environment and available for absorption is termed "bioaccessible" (Ruby et al., 1999). Most in vitro methods are sequential extractions with two distinct extraction steps: (i) a gastric phase extraction that simulates the acidic biochemical stomach environment and (ii) a subsequent intestinal phase extraction that simulates the biochemical environment of the small intestine. The fraction of the contaminant dissolved by the in vitro procedure, the "bioaccessible" contaminant, has been used to estimate the relative bioavailability of the contaminant in soil (Ruby et al., 1999). While many different in vitro methods have been developed to estimate bioaccessible Pb, few have related their results to relative bioavailable Pb as measured by an animal model. The in vitro physiologically based extraction test (PBET), which does not use food in the extraction to mimic fasting conditions, has been correlated with relative bioavailable Pb as estimated by two animal models (weanling rats and swine) (Medlin, 1997; Ruby et al., 1996, 1999). The in vitro gastrointestinal (IVG) method developed by Rodriguez et al. (1999) is an accurate predictor of relative bioavailable As in contaminated soils and waste materials as estimated by a juvenile swine model while utilizing food in the extraction procedure. Recently, Schroder et al. (2003) showed that the IVG method was correlated with in vivo relative bioavailable Cd using a juvenile swine model. The objective of this study was to determine the ability of the IVG method of Rodriguez et al. (1999), with and without food, to predict relative bioavailable Pb in contaminated soil as measured by in vivo juvenile swine dosing trials.
|
MATERIALS AND METHODS |
|---|
|
TOPNOTESABSTRACTINTRODUCTIONMATERIALS AND METHODSRESULTS AND DISCUSSIONCONCLUSIONSREFERENCES |
|---|
In Vivo Swine Dosing Study
In vivo relative bioavailable Pb in contaminated soil was determined by in vivo dosing trials using standard operating procedures (Casteel, 1995). Male swine (5–6 wk old) weighing 10 to 12 kg were dosed for 15 d with varying concentrations of Pb in substrates. Five swine were randomly assigned to treatment groups consisting of a dosing group, a negative control group (no substrate), and a positive control group that received oral lead acetate. All swine were individually housed in stainless steel cages and daily fed a powdered grower's diet (referred to as "dough" in this paper), which approximated 5% of body weight (Ziegler Bros., Gardner, PA). The diet was commercially formulated to have a protein content of approximately 19% and contained <0.2 mg Pb kg–1 diet. After a 7-d acclimation period, the swine were dosed with contaminated soil that was placed in a 5- to 10-g doughball of moistened grower diet. The swine were dosed twice daily to mimic childhood Pb ingestion, which is likely to occur between meals while children are in a fasted or semi-fasted state. A dose of 6.25 mg soil per kg body weight per day was used with half of the first dose being delivered at 0900 h after an overnight fast and the second half of the dose being delivered at 1500 h after a 4-h fast. All swine were fed 2 h after dosing.
Tissue Analyses
Blood (1.0 mL) was mixed with 9.0 mL of a matrix modifier consisting of 0.2% v/v trace metal nitric acid, 0.5% v/v Triton X-100, and 0.2% w/v ammonium phosphate in deionized distilled water before analyses. Kidney or liver (1.0 g) were digested overnight at 90°C in 2.0 mL of concentrated trace metal HNO3 (i.e., extremely low levels of Pb) and diluted to a final volume of 10.0 mL with deionized distilled water (>18 ohm). Femurs were oven-dried overnight at 100°C and were ashed in a muffle furnace at 450°C for 48 h. Aliquots of ashed femurs (200 mg) were dissolved in 10.0 mL of a 1:1 mixture of trace metal HNO3 (i.e., extremely low levels of Pb) and deionized distilled water. All samples were filtered through 0.45-mm membrane filters before analyses by graphite furnace atomic absorption spectroscopy (GFASS). Blanks, spikes and duplicate analyses were conducted every 20 samples to meet quality assurance–quality control (QA–QC) requirements. Relative Pb bioavailability was estimated using measured Pb concentrations in blood, liver, kidney, and bone.
Calculation of In Vivo Relative Bioavailability
Relative bioavailability was calculated from Eq. [3]. Lead acetate was selected as reference material in our study because it is a readily soluble form of Pb that was used in critical toxicity studies as reported in the Integrated Risk Information System. More specifically, for each study substrate, the amount of Pb bioaccumulated in tissue (e.g., µg Pb L–1 for blood and mg Pb kg–1 kidney, liver, or bone) was plotted as a function of Pb dosed (e.g., µg Pb kg–1 body weight d–1) for both reference material and study substrate. The resulting best-fit straight lines (calculated by linear regression) for both the reference material and the study substrate were used to estimate the relative bioavailability. Relative bioavailability was calculated by dividing the slope for the study substrate by the slope for the reference material.
In Vitro Gastrointestinal Method
Bioaccessible Pb was estimated in our study using the IVG method developed by Rodriguez et al. (1999). The IVG method is a two-step sequential extraction: a gastric solution extraction followed by an intestinal solution extraction. An equivalent amount of the dosing vehicle (200 g of wet feed termed "dough") was added to the gastric solution to mimic the in vivo dosing of 100 mg soil to 5 g of dough. Gastric solution was 0.15 M NaCl and 1% porcine pepsin (Sigma Chemical Company, St. Louis, MO; Catalog no. P7000). The in vitro method was conducted using 1-L glass jars in a water bath at body temperature (37°C). Soil (4.0 g) was placed in 600 mL of gastric solution to which either 0 g (e.g., no dough) or 200 g of dough was added. The pH of the gastric solution was adjusted to pH 1.8 with trace-metal-grade HCl. Anaerobic conditions were maintained by constantly bubbling argon through the solution; pH was continuously monitored and adjusted to 1.8 throughout the 1-h procedure. Mixing (to simulate gastric mixing) was maintained during the procedure using individual paddle stirrers set at a speed of 100 rpm. After 1 h, 40 mL of gastric solution, removed for Pb analysis, was replaced with 40 mL of fresh gastric solution. Subsequently, the extraction solution was modified to simulate intestinal solution by adding saturated NaHCO3 solution to adjust the pH to 5.5 followed by the addition of 2.10 g of porcine bile extract (Sigma Chemical Company; Catalog no. B8631) and 0.21 g of porcine pancreatin (Catalog no. P1500). A small amount of anti-foam agent (decanol) was added to each reaction vessel. After 1 h, 40 mL of intestinal solution was collected for Pb analysis. Gastric and intestinal solution samples were centrifuged (5211 x g) for 15 min and filtered through 0.45-µm membrane filters immediately after their collection. The samples were acidified to pH of 2 using trace metal HCl, and Pb was determined using ICP–AES.
In Vitro Bioaccessibility Calculations
Bioaccessible Pb was calculated by dividing the Pb concentration measured in the in vitro gastric or intestinal solutions by the total soil Pb content (e.g., USEPA Method 3050).
Statistical Analysis
Analysis of variance using PROC MIXED (SAS Institute, 2001) was performed to evaluate the effects of the extraction step (gastric or intestinal) and method (dough or no dough addition) on bioaccessible Pb. The data were analyzed as a split plot arrangement in a randomized complete block design. The combination of replicate and soil were used as blocks, method was the whole plot factor, and phase was the split plot factor. Simple effects of method given phase and phase given method were analyzed with a SLICE option in the LSMEANS statement. The relationship between mean in vitro bioaccessible Pb and mean in vivo relative bioavailable Pb in different tissues was determined using PROC REG (SAS Institute, 2001).
|
RESULTS AND DISCUSSION |
|---|
|
TOPNOTESABSTRACTINTRODUCTIONMATERIALS AND METHODSRESULTS AND DISCUSSIONCONCLUSIONSREFERENCES |
|---|
|
|
Dough versus No Dough
Lead extracted by the IVG GE was greater than Pb extracted by the IVG IE for the 18 individual soils for both dough and no dough methods (Table 2). Mean IVG GE Pb was also greater than mean IVG IE Pb for the soils using both methods (p < 0.001; Table 2). In part, the reduction of measured Pb between IVG GE and IVG IE can be attributed to the reduced solubility of Pb in the higher solution pH of the IE as compared with the GE (pH 5.5 vs. 1.8). During our study, mean Pb in the IE without dough decreased by approximately 97% as compared with mean GE Pb without dough. Our results are similar to those of Ruby et al. (1996), who showed that solubilized Pb decreased by 74% upon entering the small intestine step during the PBET due to adsorption and precipitation reactions removing Pb from solution as the pH increased.
Comparison of the dough vs. no-dough methods shows that the mean Pb of 16.6% for the combined GE and IE without using dough in the extraction was greater than the mean Pb extracted of 11.8% for the combined GE and IE using dough in the extraction (p = 0.003; Table 2). There was a significant interaction between method and extraction phase (e.g., gastric vs. intestinal) (p = 0.011). This was evident in the comparison of the simple effects of extraction phase for the given method. Mean IVG GE Pb of 32.2% without dough in the extraction was significantly greater than mean IVG GE Pb of 23.0% using dough in the extraction (p < 0.001) (Table 2). However, mean IVG IE Pb of 1.06% without dough in the extraction was not significantly greater than mean IVG IE Pb of 0.56% using dough in the extraction (p = 0.689; Table 2). Our results are similar to those of Ruby et al. (1993) who reported that the addition of rabbit chow to an in vitro procedure reduced the mass solubilized Pb during the stomach phase by approximately 10.8%.
In a review on human bioavailability, Ragan (1983) reported that the solubility and absorption of Fe, Cd, and Pb may be lowered by dietary components such as oxalates, phosphates, and phytates. The presence of food reduces absorption of ingested water-soluble Pb (e.g., lead chloride, lead nitrate, lead acetate) by humans primarily due to the presence of calcium and phosphate (Blake and Mann, 1983; Blake et al., 1983; Heard and Chamberlain, 1982; Rabinowitz et al., 1980). Madalonni et al. (1998) dosed human volunteers with contaminated soil from Bunker Hill, ID, and reported that the absorption of Pb was greatly affected by the presence of food in the gastrointestinal systems of test subjects. Their study reported the absorption of Pb in fasted test subjects as 26% and the absorption of Pb in fed test subjects as 2.5%. Phytic acid (myoinositol hexaphosphate) or its salt, phytate, is an important plant constituent accounting for up to 90% of total phosphorus in cereals, legumes, and oilseeds (Reddy et al., 1982). Phytic acid is capable of forming strong complexes with various metal cations under physiological conditions (Nolan et al., 1987). Wise (1981)(1983) conducted both acute (8 d) and chronic studies (6 mo) involving the addition of calcium phytate to Pb-contaminated diets fed to mice and reported that calcium phytate reduced blood Pb levels. Rose and Quarterman (1984) fed rats a diet containing 200 mg Pb kg–1 supplemented with phytate (10 g kg–1) or calcium (6 g kg–1) and found that the addition of phytate or calcium separately reduced the accumulation of Pb in bone, blood, and liver. They also reported that the greatest reduction in tissue accumulation of Pb occurred when phytate and calcium were fed together. Bullock et al. (1995) investigated the effect of phytate on the in vitro solubility of Al, Ca, Hg, and Pb as a function of pH at 37°C. They varied the Pb to phytate ratio across the pH range of 3.0 to 7.0 and found that the solubility of Pb varied with both pH and the Pb to phytate molar ratio. Lead solubility in their study was greatly reduced by the formation of Pb–phytate precipitates. Maximum reduction in Pb solubilities occurred at a Pb to phytate ratio of approximately 3:1 with reductions ranging from 96% (pH = 3.0) to 88% (pH = 7.0). The calcium–phytate complex has a strong affinity for both Pb and Cd (Wise, 1983). Also, Wise and Gilburth (1981) reported that almost complete binding of both Cd and Pb occurred at Ca to phytate ratios that are common in stock diets of laboratory animals. It is possible that Pb–phytate complexes or insoluble complexes involving phytic acid and Ca with Pb coprecipitating the complex were formed during the in vitro extraction of soils using dough, which resulted in lower bioaccessible Pb as compared with the extractions that did not use dough.
The dough material has a phosphorus content of 7580 mg kg–1. A considerable amount of P was dissolved in the IVG methods. Results show that the inclusion of dough increased soluble P in the IVG GE solution from 53.9 to 1900 mg L–1 without soil. Similarly, inclusion of dough increased soluble P in the IVG IE from 64.5 to 1740 mg L–1 without soil. Results show that the inclusion of dough increased soluble P in the IVG GE solution from 49.1 to 1810 mg L–1 with contaminated SRM 2710 soil. Similarly, inclusion of dough increased soluble P in the IVG IE from 56.7 to 1570 mg L–1 with contaminated SRM 2710 soil. The equilibrium geochemical speciation model MINTEQA2 (Version 4.0) was used to investigate the possibility that the addition of dough to the IVG procedure resulted in precipitation of inorganic Pb phosphorus compounds, thus lowering measured concentrations of in vitro Pb (USEPA, 1999). In vitro concentrations of Ca, Pb, Fe, P, Zn, Na, Cl, and solution pH were used as model inputs. Total dissolved P was assumed to be present as orthophosphate ion, which would be consistent with the most likely scenario to form Pb phosphate mineral precipitate. MINTEQA2 predicted that the IVG GE solutions, with and without dough, were oversaturated with respect to lead phosphate solid phases for the contaminated SRM 2710 soil. MINTEQA2 indicated that 24.6% of the total Pb could precipitate as pyromorphite without dough and that 79.6% of the total Pb could precipitate as pyromorphite with dough, which is consistent with decreased in vitro Pb associated with dough addition during the gastric step of the in vitro procedure. MINTEQA2 predicted that oversaturation occurred for the IVG IE solutions with and without dough. The model predicted that 99.98% of the total Pb could precipitate as pyromorphite without dough, while 99.96% of the total Pb could precipitate as pyromorphite with dough. This is consistent with the results for the soils in our study that show there was not a significant difference between mean IVG IE Pb with dough and mean IVG IE without dough.
Linear Regressions
Concentrations of Pb in blood are the most widely used biomarkers of lead exposure (United States Department of Health and Human Services, 1999). However, approximately 94% of the total body burden of Pb is found in bones with Pb cycling between blood and bone (United States Department of Health and Human Services, 1999). The relationship between blood Pb and gastrointestinal Pb exposure is nonlinear high exposure concentrations. Lead in bone is considered a more appropriate biomarker of cumulative Pb exposure than Pb in blood (United States Department of Health and Human Services, 1999; USEPA, 1986). Linear regression indicated there was a strong relationship between IVG GE Pb using dough in the extraction and in vivo relative bioavailable Pb estimated using blood data (P < 0.0001, r = 0.93) (Fig. 1A)
. Regression analysis showed there was a strong relationship (P < 0.0001, r = 0.80) between IVG IE Pb using dough in the extraction and in vivo relative bioavailable Pb estimated using blood data (Fig. 1B). A strong relationship was found between IVG GE Pb without using dough in the extraction and in vivo relative bioavailable Pb using blood data (P < 0.0001, r = 0.89) (Fig. 1C). However, a significant relationship between IVG IE Pb (no dough) and in vivo relative bioavailable Pb using blood data was not found (P = 0.121, r = 0.38) (Fig. 1D). Strong relationships also existed between IVG GE Pb using dough in the extraction and estimated in vivo relative bioavailable Pb using other tissues (e.g., liver, kidney, and bone) with regression coefficients ranging from 0.76 to 0.85 (Table 3). Strong relationships were also found between IVG IE Pb using dough in the extraction and in vivo relative bioavailable Pb as estimated by the other tissues with regression coefficients ranging from 0.56 to 0.80 (Table 3). Significant relationships were also found between IVG GE (no dough) and in vivo relative bioavailable Pb using the other tissues, and regression coefficients ranged from 0.81 to 0.93 (Table 3). Conversely, within the IE without dough in the extraction, only the relationship between IVG Pb and in vivo relative bioavailable Pb using bone data was significant (P = 0.049, r = 0.47) (Table 3). Ruby et al. (1996) showed that the stomach phase of the PBET at pH values of 1.3 and 2.5 was highly correlated with in vivo relative bioavailable Pb as measured by a weanling rat model with blood as the target organ (r2 = 0.93 for both pH values, n = 7). Their study reported a weaker relationship (r2 = 0.76) between intestinal bioaccessible Pb and in vivo relative bioavailable Pb. In a review article on bioavailability of inorganics in soils, Ruby et al. (1999) cited a study by Medlin (1997) and indicated that the stomach phase of the PBET was strongly correlated (r2 = 0.79, n = 15) with a "weighted estimate" (i.e., blood weighted 3:1 over each tissues) of in vivo relative bioavailable Pb from a young swine model. However, correlations between the intestinal phase of the PBET and in vivo relative bioavailable Pb were not reported in the review. In general, the results of our study are very similar to those reported by Ruby et al. (1996)( 1999) in that the GE without dough was highly correlated with in vivo relative bioavailable Pb as estimated with all tissues.
|
|
|
CONCLUSIONS |
|---|
|
TOPNOTESABSTRACTINTRODUCTIONMATERIALS AND METHODSRESULTS AND DISCUSSIONCONCLUSIONSREFERENCES |
|---|
|
NOTES |
|---|
|
TOPNOTESABSTRACTINTRODUCTIONMATERIALS AND METHODSRESULTS AND DISCUSSIONCONCLUSIONSREFERENCES |
|---|
|
REFERENCES |
|---|
|
TOPNOTESABSTRACTINTRODUCTIONMATERIALS AND METHODSRESULTS AND DISCUSSIONCONCLUSIONSREFERENCES |
|---|
Related articles in JEQ:
This article has been cited by other articles:
|
|
 |
|
  B. Welfringer and G. J. Zagury Evaluation of Two In Vitro Protocols for Determination of Mercury Bioaccessibility: Influence of Mercury Fractionation and Soil Properties J. Environ. Qual., October 29, 2009; 38(6): 2237 - 2244. [Abstract] [Full Text] [PDF]
|
|
|
|
|
|
D. G. Beak, N. T. Basta, K. G. Scheckel, and S. J. Traina Bioaccessibility of Lead Sequestered to Corundum and Ferrihydrite in a Simulated Gastrointestinal System J. Environ. Qual., October 27, 2006; 35(6): 2075 - 2083. [Abstract] [Full Text] [PDF]
|
|
|
|
|
|
O. Furman, D. G. Strawn, G. H. Heinz, and B. Williams Risk Assessment Test for Lead Bioaccessibility to Waterfowl in Mine-Impacted Soils J. Environ. Qual., February 2, 2006; 35(2): 450 - 458. [Abstract] [Full Text] [PDF]
|
|
|
|
 |
|
 G. S. Plumlee, S. A. Morman, and T. L. Ziegler The Toxicological Geochemistry of Earth Materials: An Overview of Processes and the Interdisciplinary Methods Used to Understand Them Reviews in Mineralogy and Geochemistry, January 1, 2006; 64(1): 5 - 57. [Full Text] [PDF]
|
|
| ||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||||
| HOME | HELP | FEEDBACK | SUBSCRIPTIONS | ARCHIVE | SEARCH | TABLE OF CONTENTS |
| The SCI Journals | Agronomy Journal | Crop Science | |||
| Journal of Natural Resources and Life Sciences Education |
Vadose Zone Journal | ||||
| Soil Science Society of America Journal | Journal of Plant Registrations | The Plant Genome | |||
