This work was supported by a Food from Thought Commercialization Grant, which is funded from the Canada First Research Excellence Fund. Canadian Wollastonite provided industrial financial support as part of this Grant.

1. Soil sampling method and core collection
<ol>
	<li>Divide the mapped and a demarcated agricultural land area of interest into different plots based on the land elevation, historical crop yield, and/or land management strategy. Determine the leveling of each plot using a GPS receiver, classify crop yield based on historical farm records (below-average, average, above-average), and the land management strategy used for each plot (types of soil amendments used, if any). Place the flags at the boundaries of each plot to ease subsequent sampling. 
	NOTE: Figure 1 shows the sectioning of the rectangular area under study into four plots (A, B, C, D). Such an experimental design and information will be helpful to check the statistical significance of the analyzed data. Furthermore, it can be appropriate for irregular farmlands and be convenient for aligning sampling according to a parameter deemed necessary, from the orientation of crop rows to the direction of terrain, runoff, dominant wind, sun path, etc. These four plots were considered in order to facilitate a field filming campaign.</li>
	<li>Use the directed random sampling method to collect cores across each plot. Subdivide each plot following a grid pattern into 25 sub-plots (Figure 2). Collecting 25 cores is above the traditionally minimum recommend number of cores (15-20).</li>
</ol>
&#8203;<img alt="Figure 1" class="xfigimg" src="/files/ftp_upload/61996/61996fig01.jpg" /> 
Figure 1: Representation of the plots used for sample collection (each plot represents an area of 5 m &#215; 10 m (totally four x 50 m2).&#160;Black flags delimit each plot boundary to ease sampling, and white flags mark locations for deep sampling.&#160;<a href="https://www-jove-com.remotexs.ntu.edu.sg/files/ftp_upload/61996/61996fig01large.jpg" target="_blank">Please click here to view a larger version of this figure.</a>
<img alt="Figure 2" class="xfigimg" src="/files/ftp_upload/61996/61996fig02.jpg" /> 
Figure 2: Sub-sectioning of each plot for collecting core samples (each sub-section represents an area of 1 m x 2 m), based on directed random sampling method.&#160;<a href="https://www-jove-com.remotexs.ntu.edu.sg/files/ftp_upload/61996/61996fig02large.jpg" target="_blank">Please click here to view a larger version of this figure.</a>
<ol start="3">
	<li>Collect core samples from random points within each sub-plot, one per sub-plot. Use a soil probe or a soil core sampler to collect the soil core down to three depth zones of 0-15 cm, 15-30 cm, and 30-60 cm to account for the SIC variation with depth due to silicate soil amendment. 
	NOTE: Depending on the type of soil and the probe/sampler used, a different sampler may be required to collect the 30-60 cm sample.</li>
	<li>Use an extendable auger (or similarly capable sampler) to collect deep soil samples from the white flag locations in Figure 1, down to additional three depth zones of 60-100 cm, 100-175 cm, and 175-250 cm. These samples account for the soil characterization variation within these depths as well as evaluate background SIC level in the investigated land area, down to the upper depth of the naturally occurring pedogenic carbonate horizon. 
	NOTE: Based on the local properties in site (e.g., depth of groundwater table), the deepest zone may be modified in different locations.</li>
	<li>Transport the soil samples into buckets, one for each sampled depth at each plot. Hand-blend the soils in each bucket thoroughly. Place the portable moisture tester into the mixed soil sample. Wait until the moisture content fixes at a stable point on the gauge of the device. Press the holder button and record the value as the real-time moisture content of blended soils.</li>
	<li>Store the composite samples in sealed bags. Label bags properly with information about the plots (A, B, C, or D), the soil depth (0-15 cm, 15-30 cm, 30-60 cm, 60-100 cm, 100-175cm, 175-250 cm), and date of sampling.</li>
</ol>
2. Soil fractionation prior to chemical analysis
<ol>
	<li>Air-dry the soil samples as soon as possible after sampling to minimize the oxidation of soil carbon. For this, place the soil samples in cardboard boxes (2.5&#34; x 3&#34; x 3&#34;) and place the boxes in a drying cabinet at 50 &#176;C for 24-48 h, until the soil is dry. Store the air-dried samples in sample bags until further analysis.</li>
	<li>Prior to soil fractionation, run the soil samples through a 2-mm sieve to remove large fragments of rocks and plant remains.</li>
	<li>Oven-dry the sieved soils by placing the samples in a muffle furnace maintained at 105&#160;&#177; 2 &#176;C for at least 15 h.</li>
	<li>For soil fractionation, place 1 kg of the oven-dried sample onto the top mesh of the sieve shaker consisting of different mesh sizes (710 to 50 &#181;m). Shake the sieves at 60 rpm for 15 min. Pan fractions &#60;50 &#181;m are preferably used for analyses, as this is the pedogenic carbonate-enriched soil fraction. 
	&#8203;NOTE: Other soil fractions can also be tested to yield additional data for verification of SIC accumulation due to enhanced weathering of amended silicates.</li>
</ol>
3. Pedogenic inorganic carbon sequestration determination
<ol>
	<li>To determine the inorganic carbon content of soil samples using calcimetry analysis, place 5 g of a sieved soil sample in an appropriate Erlenmeyer flask. Suspend the sample in 20 mL of ultrapure water. Add 7 mL of 4&#160;M HCl to a small flat-bottomed glass test tube, then place this tube upright inside the flask using a pair of tweezers.</li>
	<li>Carefully attach the flask to the calcimeter by affixing the rubber stopper. The burette water levels on the calcimeter should have been previously adjusted as required, and blanks and CaCO3 standards should have been once run on the calcimeter as needed.</li>
	<li>Shake the flask, thereby knocking over the acid tube, until the water level in the burette reaches a constant value, and no bubbling is observed in the solution (this takes approximately 5 min).</li>
	<li>Calculate the CaCO3-equivalent (CaCO3(eqv)) content of the sample (g,CaCO3(eqv)&#183;(kg,soil)-1) based on the volume change observed in the burette, and the blank and CaCO3 calibration values, using the appropriate calcimetry formula. SIC content is obtained by converting the g,CaCO3(eqv)&#183;(kg,soil)-1 value into kg,CO2&#183;(tonne,soil)-1 or kg,C&#183;(tonne,soil)-1.
	<ol>
		<li>Calculate the CaCO3(eqv) content of the sample using the below formula: 
		<img alt="Equation 1" src="/files/ftp_upload/61996/61996eq1.jpg" />&#160; (4) 
		Where: 
		w (CaCO3(eqv)) = the carbonate content of the oven-dried soil 
		m1&#160;= the mass of the test portion 
		m2 &#8203;= the mean mass of the calcium carbonate standards 
		V1 = the volume of carbon dioxide produced by the reaction of the test portion 
		V2 = the mean volume of carbon dioxide produced by the calcium carbonate standards 
		V3 = the volume change in the blank determinations 
		w (H2O)&#160;= the water content of the dried sample 
		NOTE: steps 3.1 to 3.4 are conducted based on a standard protocol29.</li>
	</ol>
	</li>
	<li>For measuring bulk density (BD) of soil ((tonne,soil)&#183;m&#8722;3), place a sufficiently large aliquot of the oven-dried soil sample in a container with a known volume. Weigh the sample using a scale. The ratio of the dried weight to the volume of the sample is considered as BD. 
	NOTE: The alternative devices for calculating &#34;undisturbed bulk density&#34; are introduced in the discussion.</li>
	<li>Calculate the Areal SIC (kg,CO2&#183;(hectare)&#8722;1) using the following formula: 
	<img alt="Equation 2" src="/files/ftp_upload/61996/61996eq2.jpg" />&#160; (5) 
	Where: 
	A = the surface area 
	DT = depth thickness</li>
	<li>Calculate the Total SIC (SIC 0-60 cm, kg,CO2&#183;(hectare)&#8722;1) for each plot, using the areal SIC values obtained for each depth, as follows: 
	SICPlot A&#160;= SIC0-60 cm&#160;= SIC0-15 cm&#160;+ SIC15-30 cm&#160;+ SIC30-60 cm&#160; (6)</li>
	<li>Add the Total areal SIC (SIC 0-60 cm, kg,CO2&#183;(hectare)&#8722;1) content for each plot (A, B, C, D) investigated, and obtain the average mean as follows: 
	<img alt="Equation 3" src="/files/ftp_upload/61996/61996eq3v2.jpg" />&#160; &#160; (7)</li>
	<li>Divide the Mean areal SIC (kg,CO2&#183;(hectare)&#8722;1) obtained from Eq. 7 by the application rate of silicate mineral/rock used for the soil amendment ((tonne, silicate)&#183;(hectare)&#8722;1). 
	NOTE: This will provide the amount of pedogenic inorganic carbon sequestered in terms of kg of CO2 per tonne of silicate applied (kg, CO2&#183;(tonne, silicate)&#8722;1). If a multi-year investigation is done, or a control plot without silicate amendment is present, this step needs to be modified to account for total sequestration and total amendment over a longer-term, or year-over-year values, or net pedogenic carbon sequestration.</li>
</ol>

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A., et al. <a target="_blank" href="http://www.ncbi.nlm.nih.gov/entrez/query.fcgi?db=PubMed&cmd=Search&doptcmdl=Citation&defaultField=Title+Word&term=Neoformation+of+pedogenic+carbonates+by+irrigation+and+fertilization+and+their+contribution+to+carbon+sequestration+in+soil.">Neoformation of pedogenic carbonates by irrigation and fertilization and their contribution to carbon sequestration in soil.</a> Geoderma. 262, 12-19 (2016).</li><li>Carmi, I., Kronfeld, J., Moinester, M. <a target="_blank" href="http://www.ncbi.nlm.nih.gov/entrez/query.fcgi?db=PubMed&cmd=Search&doptcmdl=Citation&defaultField=Title+Word&term=Sequestration+of+atmospheric+carbon+dioxide+as+inorganic+carbon+in+the+unsaturated+zone+under+semi-arid+forests.">Sequestration of atmospheric carbon dioxide as inorganic carbon in the unsaturated zone under semi-arid forests.</a> Catena. 173, 93-98 (2019).</li><li>Washbourne, C. L., Lopez-Capel, E., Renforth, P., Ascough, P. L., Manning, D. A. C. <a target="_blank" href="http://www.ncbi.nlm.nih.gov/entrez/query.fcgi?db=PubMed&cmd=Search&doptcmdl=Citation&defaultField=Title+Word&term=Rapid+removal+of+atmospheric+CO2+by+urban+soils.">Rapid removal of atmospheric CO2 by urban soils.</a> Environmental Science and Technology. 49 (9), 5434-5440 (2015).</li></ol>

The authors have no conflict of interest.

Given that collecting samples from fertilized agricultural fields is usually difficult, it is suggested that samples should be collected before nutrient application. It is also advisable to avoid collecting samples from frozen fields. The sampling depth may vary in different areas depending on the ease of sampling over the vertical profile, and the depth of the water table. The selected soil sampling device is dependent on the soil structure and depth of interest33. While it is more convenient to use hand probes/augers in the case of shallow samples, usually a more advanced version (e.g., extendable auger) is recommended for recovering subsoil samples33. In the predominance of tight clays or cemented sands, some difficulties may appear during the extracting cores due to friction and torquing of the sampler33. One issue for inorganic carbon verification campaigns is the choice of appropriate interval for tracking the uptake of carbon in soils, as it may be variable over long intervals (e.g., 5 to 10 years)34. Although there is no prescribed frequency for re-sampling, the moderately long intervals (e.g., yearly or bi-yearly) is believed to enhance the chance of reliably tracking SIC changes35.
There are also a few challenges complicating measuring the inorganic carbon using different analyses. First is regarding the possible slow dissolution of carbonate species during calcimetry analysis, especially when there is entrapment of carbonates inside particle aggregates, or even within the original silicate particles; this reduces the contact of the acidic solution, slowing or even impeding the dissolution of carbonates and the resulting degassing of CO2 during calcimetry analysis. The other difficulty that may arise is during mineralogical analysis, in terms of the detection of weathering/sequestration products, and due to the heterogeneity of the soil, which hampers XRD and SEM-EDS analyses, at least by making it more difficult to reach conclusive results36. The fractionation procedure was found to be beneficial in our prior work28 for concentrating the pedogenic carbonates and residual silicates in a single soil fraction (pan fraction), allowing more precise chemical, mineral, and morphological analyses to be done. Other studies have indicated that accumulated organic carbon is more likely to be stored in fine particle aggregation of agricultural soils37,38, similar to the particle analyzed in Figure 5. Furthermore, the higher surface area of fine silicate rock particles leads to a higher weathering rate comparing to the coarser fraction15. However, fractionation could vary from soil to soil and even may not be required for soil containing large amounts of carbonates and silicates. Also, its need or benefit should be further verified for different soil types and various silicate amendments than the ones used in our prior work.
We have demonstrated methods for detecting and analyzing SIC due to application of wollastonite to agricultural soils in the current study. Although these techniques could be utilized for investigating SIC in the soils amended with other enhanced weathering candidates, such as basalt and olivine, the mineral of choice may have different effects on the soil, which should be considered during the analysis. For example, the weathering process may take longer for some minerals compared to others. This is can be due to dissimilar dissolution rate of several minerals, concluding in different mineralization rate in short and long terms. The other issue is concerned with occurrence of precipitated carbonates over vertical profile of the soil, which could vary based on the silicate mineral properties and resulting geochemical condtions of the soil, inductive or not to immediate carbonate precipitation in the shallow soil. Accordingly, amendment of soils with some types of silicates could yield significant pedogenic carbonate formation in deeper layers, in contrast to the shallow accumulation of carbonates due to weathering of wollastonite detected in our studied fields. Core samplers have been widely used for extracting undisturbed samples and measuring undisturbed BD in the field39. Since BD is a function of several climatic parameters and practice settings, and it may vary both spatially and temporally, a reasonable number of replicates is required to yield an acceptable range of BD uncertainty in the study area39. This is particularly necessary for addressing big uncertainties in SICareal calculated estimates, such as the value determined in the current study (i.e., &#177; 39%).
Thermogravimetric analysis (TGA) can also be used to determine the calcium carbonate content in the soil by measuring the mass loss in the temperature range of 500&#8722;800&#8239;&#176;C, which is the decomposition temperature range for CaCO340. Automated carbon analyzer or TGA methods are suitable for analyzing soil samples from smaller confined areas, such as a pot experiment, since these methods require only 20 milligrams of soil sample for analyses. Therefore for agricultural studies, the calcimetry results are deemed more precise and accurate given the larger mass of sample analyzed (10&#8239;g versus 20 milligrams), the triplicate readings obtained, and the use of pure calcium carbonate as the method standard. More details and examples can be found in Haque et al.36. Due to the co-occurrence of geological- and atmospheric-driven pedogenic carbonates in soil, distinguishing between different sources is of significance. Stable isotopic (&#948;13C) and radiogenic (14C) carbon signatures, as well as isotopic oxygen signatures, are regarded as the robust tools for identifying the source of carbon in soil16,41,42,43. Such analysis can further verify the sequestration of atmospheric CO2 in studies aiming to monitor the fate of pedogenic carbonate in soils.
While conventional carbon detection methods (e.g., mass measurement) are suitable for local carbon markets, more systematic methods are required when it comes to verification objectives in regulated markets35. The verification method described here is adaptable for monitoring pedogenic inorganic carbon sequestration in various agricultural soils amended with alkaline earth metal silicate-containing rocks, such as wollastonite, basalt, and olivine. This type of validation is essential for carbon credit programs, which can benefit farmers that sequester carbon in their fields.

CO2 is a major greenhouse gas (GHG), and its concentration in the atmosphere is increasing continuously. Preindustrial global average CO2 was about 315 parts per million (ppm), and as of April 2020, the atmospheric CO2 concentration increased to over 416 ppm, hence causing global warming1. Therefore, it is critical to reduce the concentration of this heat-trapping GHG in the atmosphere. Socolow2 has suggested that to stabilize the concentration of atmospheric CO2 to 500 ppm by 2070, nine &#39;stabilization wedges&#39; will be required, where each stabilization wedge is an individual mitigation approach, sized to achieve 3.67 Gt CO2 eq per year in emissions reduction.
Carbon capture and storage (CCS) is the main technology to reduce the CO2 from the atmosphere, as recommended by the Mission Innovation initiative, launched at the United Nations Climate Change Conference 20153. To capture atmospheric CO2, the three main storage options available are ocean storage, geological storage, and mineral carbonation4. Focusing on mineral carbonation, CO2 is stored by converting alkaline earth metals, mainly calcium- and magnesium-rich silicates, into thermodynamically stable carbonates for geological timeframes (over millions of years)5. For example, olivine, pyroxene, and serpentine group minerals have the potential to undergo mineral carbonation6; however, under normal conditions, these reactions are limited by slow reaction kinetics. Therefore, to speed up the process under ambient conditions, finely comminuted (crushed/milled) forms of these silicates can be applied to agricultural soils, a process referred to as terrestrial enhanced weathering7. Soil is a natural sink to store CO2, presently being a reservoir for 2500 Gt of carbon, which is thrice the atmospheric reservoir (800 Gt carbon)8. Pedogenic processes in soils and subsoils regulate atmospheric CO2 by two major natural pathways, namely the organic matter cycle and the weathering of alkaline earth metal minerals, affecting organic and inorganic carbon pools, respectively9.
It is estimated that almost 1.1 Gt of atmospheric CO2 is mineralized through chemical rock weathering annually10. Silicate rocks rich in calcium and magnesium (e.g., basalt) are regarded as the primary feedstocks for enhanced weathering9,11,12. Once crushed silicate-containing minerals are applied to agricultural fields, they begin to react with CO2 dissolved in soil porewater, concluding with the mineral precipitation of stable carbonates11,13. Olivine14,15, wollastonite (CaSiO3)13, dolerite, and basalt16 are among minerals which have demonstrated carbon sequestration potential through enhanced weathering in previous studies. Despite the greater availability, and hence possibly greater CO2 sequestration capacity, of magnesium silicates, there are concerns about their application for enhanced weathering in croplands due to their potential environmental impact as a result of Cr and Ni leaching and the possible presence of asbestiform particulates11,15,17,18. As a calcium-bearing silicate, wollastonite is herein highlighted as a prime candidate for this process due to its high reactivity, simple chemical structure, being environmentally benign as well as facilitating the production of carbonates due to the weaker bonding of Ca ions to its silica matrix12,19,20,21. Wollastonite that is mined in Kingston, Ontario, Canada, and is presently commercialized by Canadian Wollastonite for agricultural applications, does not contain elevated levels of hazardous metals. The worldwide wollastonite reserves are estimated to be over 100 Mt, with China, India, USA, Mexico, Canada, and Finland as the top productive countries22.
Enhanced weathering of silicate mineral is reckoned to promote soil health, notably crop yield increase and plant growth improvement, leading to the potential reduction in the application of synthetic fertilizers, which can further contribute to GHG emissions reduction11,18,19. Previous studies have reported that the application of Ca-rich silicate minerals to soils supplies basicity for neutralizing acidity in the soil medium, favoring crop production23,24,25. This also impedes toxic metals mobilization, susceptible to acidic conditions, and enhanced weathering could be useful for retarding erosion through soil organic matter increment11.
Equations 1-3 show how pedogenic carbon sequestration as inorganic carbonates is possible by amending soils with wollastonite. Ambient CO2 enters the soil through rainwater or is produced in soil by microbial activity degrading organic compounds. Once in contact with soil porewater, carbonic acid is formed, which dissociates to form bicarbonate and proton (Equation 1). In the presence of plants, root exudates, such as citric acid and maleic acid, are released, which also provide protons in the system. These protons facilitate the dissolution of wollastonite in the soil through releasing Ca ions and leaving behind amorphous silica (Equation 2). The released Ca ions ultimately react with the bicarbonate to precipitate as carbonates (crystalline calcite or other varieties, depending on geochemical conditions) (Equation 3). This formed calcium carbonate becomes part of the soil inorganic carbon (SIC) fraction26.
Ambient CO2 solvation:
2CO2(g) + 2H2O(l) &#8596; 2H2CO3(aq) &#8596; 2HCO3- + 2H+ (1)
Wollastonite dissolution (H+ from the dissociation of carbonic acid and root exudates):
CaSiO3(s) + 2 H+ &#8594; Ca2+ + H2O(l) + SiO2(s)&#160;(2)
Pedogenic inorganic carbonate precipitation:
Ca2+ + 2 HCO3- &#8594;&#160; CaCO3(s)&#8595; + H2O(l) + CO2(g)&#160;(3)
In our recent work, enhanced weathering through the application of wollastonite to agricultural soils, as a limestone-alternative amendment, has been found effective for CaCO3 precipitation in topsoil, both at laboratory and field scales, and over short (few months) and long (3 years) terms. In the field studies, chemical and mineralogical assessments have revealed that the SIC content increases proportionally to wollastonite application dosage (tonne&#183;hectare-1)13. In laboratory studies, the mineralogical analysis showed the presence of pedogenic carbonate due to carbon sequestration19. Pedogenic carbonate formation in soil depends on several factors, most notably: topography, climate, surface vegetation, soil biotic processes, and soil physicochemical properties27. Our previous study23 determined the role of plants (a leguminous plant (green bean) and a non-leguminous plant (corn)) on wollastonite weathering and inorganic carbonate formation in soil. Our ongoing research on the pedogenic carbon formation and migration in soils and subsoils includes investigating the fate of soil carbonates in agricultural soil, first formed in topsoils due to mineral weathering at various depths and over time. According to Zamanian et al.27, the naturally occurring pedogenic carbonate horizon is found farther from the surface as the rate of local precipitation increases, with the top of this horizon commonly appearing between a few centimeters to 300 cm below the surface. Other ambient and soil parameters, such as soil water balance, seasonal dynamics, the initial carbonate content in parent material, soil physical properties, also impact the depth of this occurrence27. Thus it is of significance to sample soils to a sufficient depth at all opportunities to obtain an accurate understanding of the original and the incremental levels of SIC resulting from enhanced weathering of silicates.
At the field scale, an important limitation is the use of low application rates of silicate soil amendments. As there is limited knowledge on the effect of many silicates (such as wollastonite and olivine) on soil and plant health, commercial producers avoid testing higher application rates that could result in significant carbon sequestration. As a result of such low application rates, as well as the large area of crop fields, a research challenge commonly faced is to determine changes in SIC when values are relatively low, and to recover and isolate the silicate grains and weathering products from the soil to study morphological and mineralogical changes. In our past work, we reported on how physical fractionation of the wollastonite-amended soil (using sieving) enabled a better understanding of the weathering process, especially the formation and accumulation of pedogenic carbonates28. Accordingly, the higher contents of wollastonite and weathering products were detected in the finer fraction of soil, which provided reasonably high values during analyses, ensuring more precise and reliable results. The findings highlight the importance of using physical fractionation, through sieving or other segregation means, for reliable estimation of the sequestrated carbon accumulation in silicate-amended soils. However, the degree of fractionation could vary from soil to soil and from silicate to silicate, so it should be further researched.
Accurate measurement of SIC is critical for establishing a standard and scientific procedure that can be adopted by various researchers interested in analyzing the evolution of SIC and (and organic carbon) over time and depth of the soil. Such methodology enables farmers to claim carbon credit as a result of SIC formation in their field soils. The following protocol describes, in detail: (1) a soil sampling method to be used following soil silicate amendment, which accounts for the statistical significance of the analyzed soil data; (2) a soil fractionation method that improves the accuracy of quantifying changes in pedogenic inorganic carbonate pool as a result of enhanced silicate weathering, and (3) the calculation steps used to determine the SIC sequestration rate as a result of soil silicate amendment. For the purpose of this demonstration, wollastonite, sourced from Canadian Wollastonite, is assumed to be the silicate mineral applied to agricultural soils, and the agricultural soils are considered to be similar to those found in Southern Ontario&#39;s farmlands.
The procedure involving amending agricultural soil with wollastonite (e.g., determining the amount of wollastonite to apply per hectare, and the method to spread it over the soil) was described in our previous study13. The study area in our prior and present work is rectangular plots; therefore, the direct random sampling method is appropriate for such studies. This is a commonly used method owing to its low cost, reduced time requirement, and ability to provide adequate statistical uncertainty. Similarly, depending on the various field conditions and the level of statistical significance desired, zonal or grid sampling methods can also be used. Accuracy in soil sampling is essential to reduce statistical uncertainty as a result of sampling bias. When statistics are used, achieving less than 95% confidence (i.e., p &#60; 0.05) is not considered &#34;statistically significant.&#34; However, for certain soil studies, the confidence level may be relaxed to 90% (i.e., p &#60; 0.10) owing to the number of uncontrolled (i.e., naturally varying) parameters in the field conditions that affect the general precision of measurements. In this protocol, two sets of samples are collected in order to investigate SIC content and other chemical, mineral, and morphological properties of the soil throughout its vertical profile.

<table><tbody><tr><td>Analytical scale</td><td>Sartorius</td><td>Quintix 224-S1</td><td>Four decimals.</td></tr><tr><td>Calcimeter</td><td>Eijkelkamp</td><td>Model 08.53</td><td>To determine the wt% CaCO&lt;sub&gt;3&lt;/sub&gt;-equivalent in the sample.</td></tr><tr><td>Drying cabinet/muffle furnace</td><td>Thermo Scientific</td><td>F48055-60</td><td>50&amp;deg;C or 103 &amp;plusmn; 2&amp;deg;C.</td></tr><tr><td>HCl</td><td>Fisher Scientific</td><td>A144S-500</td><td>Reagent grade (36.5%-38.0%).</td></tr><tr><td>HNO&lt;sub&gt;3&lt;/sub&gt;</td><td>Fisher Scientific</td><td>T003090500</td><td>Trace metal analysis grade (69.0%-70.0%)</td></tr><tr><td>Inductively Coupled Plasma Mass Spectrometer (ICP-MS)</td><td>PerkinElmer</td><td>NexION</td><td>To determine the concentration of Ca in the microwave-digested soil.</td></tr><tr><td>Microwave digester</td><td>PerkinElmer</td><td>Titan</td><td>To digest soils in concentrated HNO&lt;sub&gt;3&lt;/sub&gt;.</td></tr><tr><td>pH meter</td><td>Oakton</td><td>700</td><td>Calibrated with standard solutions before each set of measurements; temperature corrected to 25 &amp;deg;C.</td></tr><tr><td>Scanning Electron Microscope -Energy Dispersive Spectroscope (SEM-EDS)</td><td>Oxford</td><td>X-Max20 SSD</td><td>To determine the morphology of soil particulates.</td></tr><tr><td>Sieve shaker</td><td>Retsch</td><td>AS-200</td><td>For soil fractionation.</td></tr><tr><td>Soil auger sampler</td><td>Eijkelkamp</td><td>01-16</td><td>Depths down to 700 cm.</td></tr><tr><td>Soil Dakota probe sampler</td><td>JMC</td><td>PN139</td><td>Depths down to 100 cm.</td></tr><tr><td>Soil probe sampler</td><td>JMC</td><td>PN031</td><td>Depths down to 30 cm.</td></tr><tr><td>Soil moisture meter</td><td>Extech</td><td>MO750</td><td>Measure moisture content up to 50%</td></tr><tr><td>Wavelength Dispersive X-ray Fluorescence spectroscope (WDXRF)</td><td>Malvern Panalytical</td><td>Zetium</td><td>To characterize elemental composition of soil.</td></tr><tr><td>X-ray Diffraction analyzer (XRD)</td><td>Panalytical</td><td>Empyrean</td><td>To characterize mineralogicalbproperties of soil.</td></tr></tbody></table>

monitoring pedogenic inorganic carbon accumulation due to weathering of amended silicate minerals in agricultural soils.

The present study aims to demonstrate a systematic procedure for monitoring inorganic carbon induced by enhanced weathering of comminuted rocks in agricultural soils. To this end, the core soil samples taken at different depth (including 0-15 cm, 15-30 cm, and 30-60 cm profiles) are collected from an agriculture field, the topsoil of which has already been enriched with an alkaline earth metal silicate containing mineral (such as wollastonite). After transporting to the laboratory, the soil samples are air-dried and sieved. Then, the inorganic carbon content of the samples is determined by a volumetric method called calcimetry. The representative results presented herein showed five folded increments of inorganic carbon content in the soils amended with the Ca-silicate compared to control soils. This compositional change was accompanied by more than 1 unit of pH increase in the amended soils, implying high dissolution of the silicate. Mineralogical and morphological analyses, as well as elemental composition, further corroborate the increase in the inorganic carbon content of silicate-amended soils. The sampling and analysis methods presented in this study can be adopted by researchers and professionals looking to trace pedogenic inorganic carbon changes in soils and subsoils, including those amended with other suitable silicate rocks such as basalt and olivine. These methods can also be exploited as tools for verifying soil inorganic carbon sequestration by private and governmental entities to certify and award carbon credits.

The SIC content of soils can be determined using various methods, including an automated carbon analyzer or a calcimeter. The automated carbon analyzer for total soil carbon determination measures the CO2 pressure built-up in a closed vessel30. In calcimetry, the evolved volume of CO2 released after acidification, typically by the addition of concentrated HCl acid, of the carbonate-containing sample is measured. The calcimetry method is relatively simple, involving simple chemical procedures, thus suitable for analyzing many field samples quickly with high precision (i.e., reproducible values) and adequate accuracy (i.e., values close to the accurate carbonate content). In the directed random sampling method used in this study, the samples from each plot are thoroughly hand-blended, then dried to obtain a homogenous representative soil sample prior to analyzing its SIC content. The calcimeter analysis is conducted in triplicates for each sample.
The elemental composition of soil samples can be determined either by Wavelength Dispersive X-ray Fluorescence spectroscopy (WDXRF) or by Inductively Coupled Plasma Mass Spectrometry (ICP-MS). In the case of the latter, soil samples must be acid digested prior to analysis. The mineral composition is best determined by powder X-ray Diffraction (XRD). The resulting diffractogram provides qualitative information about the presence of crystalline mineral phases, which can be quantified via the Rietveld refinement technique, best aided with the use of an internal standard. The elemental and mineralogical composition can be used to infer the depth that silicates and weathering products have reached at sampling time. Therefore, they can confirm the transport from topsoil towards subsoil, where carbonates can be stored for the long-term. The morphology of soil particulates can be studied by a scanning electron microscopy (SEM) and can be combined with energy dispersive spectroscopy (EDS) for semi-quantitative elemental microanalysis. Morphological analysis can be used to identify residual silicates, weathering products and gain a mechanistic understanding of the weathering phenomena (such as dissolving surfaces, newly precipitated crystals, and formation of amorphous materials). Mineralogical and elemental microanalysis results can also be used to further verify the calcimetry results. The presence of accumulated carbonate phases, such as calcite (CaCO3), may be evident in diffractograms and can be found by compositional signature among soil particulates.
Table 1 shows a typical set of data for a wollastonite-amended soil (collected from 0-15 cm and unsieved) compared to a control untreated soil, in terms of the soil pH, the calcimetry results, and the calcium ion concentration obtained using microwave digestion followed by ICP-MS. The pH of the wollastonite-amended soil is higher by 1.15 units compared to the control, and the CaCO3(eqv) content is nearly five times greater than the control. The calcium concentration in the wollastonite-amended soil is also higher, by almost seven times. Alone, ICP-MS cannot differentiate which calcium mineral, such as wollastonite or calcite, is mainly contributing to these calcium concentrations. Still, it is expected that the calcium concentration difference will be more significant than the carbonate difference since the amended soil will have both more wollastonite and more carbonates than the control soil. WDXRF and XRD analysis of these samples can help to further clarify the main oxides and mineral phases present in the samples, respectively.
The CaCO3(eqv) content (calcimeter results) over a vertical profile (0-15, 15-30, and 30-60 cm) are demonstrated in Table 2. Accordingly, the highest content (of unsieved samples) was 10.13 g,CaCO3(eqv)&#183;(kg,soil)-1, detected in 0-15 cm depth zone. The 15-30 cm samples showed the lowest amount of CaCO3(eqv). The CaCO3(eqv) content increased again in 30-60 cm zone. The results from two deep profile samples also suggest the much higher content of carbonates in deeper layers (60-100 cm profile). Based on the results of shallow and deep samples, it is implied that there are two zones enriched in carbonates. The first is the depth zone of 0-15 cm, representative of weathering products due to wollastonite application, given the significant increase versus the control. The other zone includes deeper samples, starting at around 30 cm and increasing to great extent down to 1 m. Since deeper samples are generally indicative of soil&#39;s parent materials, it can be inferred that carbonates at this zone are of geological origin. Table 2 also depicts a comparison of the unsieved and sieved sample (pan fraction) to investigate the impact of fractionation on the carbonate content. Based on this, the carbonate content is slightly higher in the pan fraction, implying possibility of accumulation of carbonates in smaller particles, in agreement with our previous study28.
The various oxides present in the soil can be determined by WDXRF, as exemplified in Table 3 for the control soil. Silica (SiO2) is the main oxide present, which is the primary component of sandy loam soil, and the texture of this sample includes 11 g/kg gravel, 551 g/kg sand, 295 g/kg silt, and 155 g/kg clay. The Ca content of the soil (2.59 wt%) obtained by WDXRF is greater than that determined by ICP-MS (0.96 wt%). This is because the WDXRF result is normalized to 100 wt%, which slightly inflates values as non-detectable components such as organics are not accounted for. Moreover, the digestion method used to prepare samples for ICP-MS likely did not fully dissolve all soil minerals, so ICP-MS values are slightly underestimated. Hence, the use of WDXRF combined with ICP-MS allows for estimating an upper and a lower bound on the true Ca (and Mg) concentration. Thus, they can be used to monitor the transport of silicates and weathering products, including carbonates, as a function of depth.
The XRD pattern of a wollastonite-amended soil is presented in Figure 3. The main peaks present are quartz (SiO2) at 26.65&#176;, and albite (NaAlSi3O8) at 28.07&#176;, which are predominant minerals in sandy loamy soils31. The additional peaks of wollastonite and calcite are also present as a result of wollastonite addition and calcite formation. The calcite is identified by a main peak at 29.40&#176; 2&#952;, and a minor peak at 39.40&#176;. The high calcimeter reading for amended soil is due to the formation of calcite, at least in part as amorphous carbonates that can also form under ambient conditions32. WDXRF and XRD can also help in the characterization of the wollastonite used. The nominal elemental composition of the wollastonite used in this study, sourced from Canadian Wollastonite&#39;s Ontario mine, includes 26% silicon (55% SiO2), 18% calcium (26% CaO), 4.0% magnesium (9% MgO), 1.8% sulfur, 0.11% nitrogen, 0.10% P2O5, 0.10% K2O, 11 ppm copper, and 1.1 ppm zinc. The main mineral phases present in this wollastonite, as determined by XRD analysis, include wollastonite, diopside (CaMgSi2O6), and quartz (SiO2).
Figure 4a shows SEM images of the wollastonite-amended soil after a period of several weeks of weathering. The fine needle-shaped wollastonite is noticeable in the amended soil sample, present along with other larger soil particles. A closer look at these wollastonite particles (Figure 4b) helps to gain a deeper insight into the morphological changes occurring at the surface. The microanalysis of the wollastonite surface is possible by obtaining an elemental mapping of the sample (Figures 4c-f). The EDS spectrum of the mapped area reveals its semi-quantitative chemical profile in Figure 4g. The elemental maps clearly show Si and Ca as the main components of wollastonite. Mg is not a major component of wollastonite, as evidenced by absence of Mg signal from the needle-shaped particles, but it is present in minor quantities in other soil particles, which can include diopside particles. The C map does not distinguish between the carbonate formed on the wollastonite surface and the organic matter already present in the soil, and it is also dominated by carbon signal coming from the carbon tape below the sample. Figure 5 shows spot EDS analysis on the smaller fragments, at 40000x, scattered in the soil sample and shown in Figure 4b (at 2,000x) marked within the yellow circle. Spot EDS analysis at two different points indicates that this fragment is rich in C and O, suggesting that it is made up primarily of organic matter, which matches the amorphous particle morphology. Additionally, by looking at the Ca:Si ratio, SEM-EDS analysis can be potentially used to identify signs of wollastonite weathering in soil, such as leaching of Ca from the wollastonite or the fate of the formed carbonates in the soil.
Using the calcimeter reading of the soil amended with wollastonite, the pedogenic inorganic carbon sequestration rate can be calculated using the steps outlined in section 3 of the Protocol. To this end, the difference of calcimeter reading for analyzed sample and its corresponding control should be calculated for the depth of interest. Then a factor of 0.44 is applied to the difference to convert CaCO3(eqv) to CO2. In case of the 0-15 cm depth samples presented in table 2, deducting the calcimeter reading of the control (2.51 g,CaCO3(eqv)&#183;(kg,soil)-1) from of 0-15 cm depth reading (10.13 g,CaCO3(eqv)&#183;(kg,soil)-1), results in a net amount of 3.35 kg,CO2&#183;(tonne,soil)-1 sequestered at this depth. Considering only the soil thickness of 0.15 m, and a disturbed BD of 1.01 tonne&#183;(m-3) measured in the laboratory, the Areal SIC is then can be calculated using Equation 5. Based on the ratio between undisturbed and disturbed BD and the uncertainty existing in reporting BD due to climatic and land use factors, we have estimated the undisturbed BD of our 0-15 cm layer to be 1.386 &#177; 0.23 tonne&#183;(m-3). Considering the uncertainty present in calcimeter reading, we determined the cumulative uncertainty of calculated SICAreal, using a Gaussian equation for normally-distributed errors method, to be &#177; 39%. Accordingly, we estimate the sequestrated CO2 in the 0-15 cm layer of our field to be 6.96 &#177; 2.71 tonne,CO2&#183;(hectare)&#8722;1. Using similar procedure, the Areal SIC of 15-30 cm and 30-60 cm layers can also be calculated (for this field, control values were not available to demonstrate this calculation). Summing up the values for the full 0-60 cm profile, the estimated sequestrated carbon could be determined in the study area.
<img alt="Figure 3" class="xfigimg" src="/files/ftp_upload/61996/61996fig03.jpg" /> 
Figure 3: XRD diffractogram showing the mineralogical phases present in a wollastonite-amended soil (W: wollastonite, Q: quartz, A: albite, C: calcite). Diffractogram determined by commercial X-ray diffraction and analysi software. The diffractometer operated with Cu K&#945; radiation at 45 kV and 40 mA, and the diffraction patterns were collected over a 2&#952; range of 5-70&#176;. <a href="https://www-jove-com.remotexs.ntu.edu.sg/files/ftp_upload/61996/61996fig03large.jpg" target="_blank">Please click here to view a larger version of this figure.</a>
<img alt="Figure 4" class="xfigimg" src="/files/ftp_upload/61996/61996fig04.jpg" /> 
Figure 4: SEM-EDS analysis. (a) SEM image of a wollastonite-amended soil at 250x and 400 &#181;m scale; (b) closer view of the weathered wollastonite grains present in the soil at 2000x and 50 &#181;m scale; (c-f) EDS elemental mapping of Si, C, Ca, and Mg present in the area visualized in Figure 4b at 2,000x and 50 &#181;m scale; (g) EDS spectrum and semi-quantitative elemental composition of the area visualized in panel b. SEM-EDS data was collected using scanning electron microscope, which was equipped with energy dispersive spectroscopy used for elemental composition analysis of selected areas and spots with an excitation volume at 20 kV. Prior to SEM-EDS analysis, the samples were mounted on carbon tape and sputter-coated with gold. <a href="https://www-jove-com.remotexs.ntu.edu.sg/files/ftp_upload/61996/61996fig04large.jpg" target="_blank">Please click here to view a larger version of this figure.</a>
<img alt="Figure 5" class="xfigimg" src="/files/ftp_upload/61996/61996fig05.jpg" /> 
Figure 5: SEM image of encircled particulate shown in Figure 4b at 40,000x and 2.5 &#181;m scale, and EDS spectrum and semi-quantitative elemental composition of two spots marked on the SEM image. <a href="https://www-jove-com.remotexs.ntu.edu.sg/files/ftp_upload/61996/61996fig05large.jpg" target="_blank">Please click here to view a larger version of this figure.</a>
<table border="1" fo:keep-together.within-page="1" fo:keep-with-next.within-page="always">
	<tbody>
		<tr>
			<td>Sample</td>
			<td>pHa</td>
			<td>Calcimeter measurement (g,CaCO3(eqv)/kg,soil)</td>
			<td>Ca concentration from ICP-MS (mg,Ca/kg,soil)b</td>
		</tr>
		<tr>
			<td>Control (no amendment)</td>
			<td>6.42 &#177; 0.05</td>
			<td>4.5 &#177; 0.5</td>
			<td>9566.6 &#177; 86.8</td>
		</tr>
		<tr>
			<td>Wollastonite amended soil</td>
			<td>7.57 &#177; 0.04</td>
			<td>21.9 &#177; 0.1</td>
			<td>66044.1 &#177; 534.6</td>
		</tr>
		<tr>
			<td colspan="4">aThe pH of the samples was determined using a 1:5 ratio of soil and 0.01M CaCl2&#160;solution, followed by 30 min shaking and 1 h settling time before taking the pH measurement of the clear supernatant (Pansu and Gautheyrou, 2006).</td>
		</tr>
		<tr>
			<td colspan="4">bThe samples were microwave digested in concentrated HNO3 prior to ICP-MS analysis; the use of HF is often recommended for digesting soils and silicates, but is avoided here to reduce the safety risk of the analysis (HF is a very toxic chemical that requires extreme care and appropriate handling).</td>
		</tr>
	</tbody>
</table>
Table 1: Comparison between the untreated control soil and wollastonite-amended soil based on chemical analyses (pH, calcimetry, and ICP-MS).
<table border="1" fo:keep-together.within-page="1" fo:keep-with-next.within-page="always">
	<tbody>
		<tr>
			<td>Sample</td>
			<td>SIC content (g,CaCO3(eqv)/(kg,soil))</td>
		</tr>
		<tr>
			<td>Depth zone of 0-15 cm (pan fraction)</td>
			<td>12.33 &#177; 3.53</td>
		</tr>
		<tr>
			<td>Depth zone of 0-15 cm</td>
			<td>10.13 &#177; 2.68</td>
		</tr>
		<tr>
			<td>Control value of depth zone of 0-15 cm</td>
			<td>2.51 &#177; 0.50</td>
		</tr>
		<tr>
			<td>Depth zone of 15-30 cm</td>
			<td>4.23 &#177; 1.00</td>
		</tr>
		<tr>
			<td>Depth zone of 30-60 cm</td>
			<td>9.20 &#177; 0.09</td>
		</tr>
		<tr>
			<td>Deep profile 1 (0-30 cm)</td>
			<td>4.41 &#177; 0.06</td>
		</tr>
		<tr>
			<td>Deep profile 1 (30-60 cm)</td>
			<td>1.56 &#177; 0.03</td>
		</tr>
		<tr>
			<td>Deep profile 1 (60-100 cm)</td>
			<td>32.32 &#177; 1.36</td>
		</tr>
		<tr>
			<td>Deep profile 2 (0-30 cm)</td>
			<td>4.56 &#177; 0.62</td>
		</tr>
		<tr>
			<td>Deep profile 2 (30-60 cm)</td>
			<td>18.43 &#177; 0.41</td>
		</tr>
		<tr>
			<td>Deep profile 2 (60-100 cm)</td>
			<td>131.54 &#177; 1.89</td>
		</tr>
		<tr>
			<td colspan="2">Samples of depth zone of 0-15 cm were collected using a probe sampler. Samples of depth zones of 15-30 cm and 30-60 cm were collected using a Dakota probe sampler. Deep profile samples were collected using an extended auger sampler.</td>
		</tr>
	</tbody>
</table>
Table 2: The CaCO3(eqv) content in different depths of the soil based on the calcimetry results.
<table border="1" fo:keep-together.within-page="1" fo:keep-with-next.within-page="always">
	<tbody>
		<tr>
			<td>Oxides in soil</td>
			<td>Wt%</td>
		</tr>
		<tr>
			<td>SiO2</td>
			<td>65.19</td>
		</tr>
		<tr>
			<td>Al2O3</td>
			<td>14.76</td>
		</tr>
		<tr>
			<td>Fe2O3</td>
			<td>6.20</td>
		</tr>
		<tr>
			<td>CaO</td>
			<td>3.62</td>
		</tr>
		<tr>
			<td>K2O</td>
			<td>2.98</td>
		</tr>
		<tr>
			<td>P2O5</td>
			<td>2.11</td>
		</tr>
		<tr>
			<td>MgO</td>
			<td>1.69</td>
		</tr>
		<tr>
			<td>Na2O</td>
			<td>1.45</td>
		</tr>
		<tr>
			<td>TiO2</td>
			<td>1.25</td>
		</tr>
		<tr>
			<td>SO3</td>
			<td>0.37</td>
		</tr>
		<tr>
			<td>MnO</td>
			<td>0.16</td>
		</tr>
		<tr>
			<td>BaO</td>
			<td>0.11</td>
		</tr>
		<tr>
			<td>ZrO2</td>
			<td>0.10</td>
		</tr>
	</tbody>
</table>
Table 3: WDXRF data of the composition of the various oxides present in the control soil. Duplicate samples, in loose powder form, were analyzed for 20 min using standardless Omniam method, under helium and at 1 kW power, and concentrations were calculated as oxides.&#160; The average sum before normalization was 69.8 wt%, with the balance being porosity and undetectable light elements (H, C, O, N). The average concentrations of the detected oxides present in amounts greater than 0.10 wt% were selected and normalized to 100%.

Watch this Scientific Journal Video about Monitoring Pedogenic Inorganic Carbon Accumulation Due to Weathering of Amended Silicate Minerals in Agricultural Soils. at JoVE.com

Monitoring Pedogenic Inorganic Carbon Accumulation Due to Weathering of Amended Silicate Minerals in Agricultural Soils.

The verification method described here is adaptable for monitoring pedogenic inorganic carbon sequestration in various agricultural soils amended with alkaline earth metal silicate-containing rocks, such as wollastonite, basalt, and olivine. This type of validation is essential for carbon credit programs, which can benefit farmers that sequester carbon in their fields.

The present study aims to demonstrate a systematic procedure for monitoring inorganic carbon induced by enhanced weathering of comminuted rocks in ...

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5.1K Views.  University of Guelph. De hier beschreven verificatiemethode kan worden aangepast voor de monitoring van pedogene, anorganische koolstofvastlegging in verschillende landbouwgronden, gewijzigd met gesteenten die alkalische silicaten van aardmetaal bevatten, zoals Wollastoniet, basalt en olivijn. Deze methode kan gemakkelijk worden gebruikt door particuliere of overheidsinstanties voor het verifiëren van het anorganische koolstofgehalte in de bodem, aangezien landbouwers in aanmerking komen voor koolstofkrediet met ...

Video: Monitoring Pedogenic Inorganic Carbon Accumulation Due to Weathering of Amended Silicate Minerals in Agricultural Soils.

Measurement of Greenhouse Gas Flux from Agricultural Soils Using Static Chambers

Measurement of greenhouse gas (GHG) fluxes between the soil and the atmosphere, in both managed and unmanaged ecosystems, is critical to understanding the biogeochemical drivers of climate change and to the development and evaluation of GHG mitigation strategies based on modulation of landscape management practices. The static chamber-based method described here is based on trapping gases emitted from the soil surface within a chamber and collecting samples from the chamber headspace at regular intervals for analysis by gas chromatography. Change in gas concentration over time is used to calculate flux. This method can be utilized to measure landscape-based flux of carbon dioxide, nitrous oxide, and methane, and to estimate differences between treatments or explore system dynamics over seasons or years. Infrastructure requirements are modest, but a comprehensive experimental design is essential. This method is easily deployed in the field, conforms to established guidelines, and produces data suitable to large-scale GHG emissions studies.

This article showcases the static chamber-based method for measurement of greenhouse gas flux from soil systems. With relatively modest infrastructure investments, measurements may be obtained from multiple treatments/locations and over timeframes ranging from hours to years.

Measurement of greenhouse gas (GHG) fluxes between the soil and the atmosphere, in both managed and unmanaged ecosystems, is critical to understanding the ...

A CO2 Concentration Gradient Facility for Testing CO2 Enrichment and Soil Effects on Grassland Ecosystem Function

Continuing increases in atmospheric carbon dioxide concentrations (CA) mandate techniques for examining impacts on terrestrial ecosystems. Most experiments examine only two or a few levels of CA concentration and a single soil type, but if CA can be varied as a gradient from subambient to superambient concentrations on multiple soils, we can discern whether past ecosystem responses may continue linearly in the future and whether responses may vary across the landscape. The Lysimeter Carbon Dioxide Gradient Facility applies a 250 to 500 &#181;l L-1 CA gradient to Blackland prairie plant communities established on lysimeters containing clay, silty clay, and sandy soils. The gradient is created as photosynthesis by vegetation enclosed in in temperature-controlled chambers progressively depletes carbon dioxide from air flowing directionally through the chambers. Maintaining proper air flow rate, adequate photosynthetic capacity, and temperature control are critical to overcome the main limitations of the system, which are declining photosynthetic rates and increased water stress during summer. The facility is an economical alternative to other techniques of CA enrichment, successfully discerns the shape of ecosystem responses to subambient to superambient CA enrichment, and can be adapted to test for interactions of carbon dioxide with other greenhouse gases such as methane or ozone.

A CO2 Concentration Gradient Facility for Testing CO2 Enrichment and Soil Effects on Grassland Ecosystem Function

The Lysimeter Carbon Dioxide Gradient Facility creates a 250 to 500 &#181;l L-1 linear carbon dioxide gradient in temperature-controlled chambers housing grassland plant communities on clay, silty clay, and sandy soil monoliths. The facility is used to determine how past and future carbon dioxide levels affect grassland carbon cycling.

Continuing increases in atmospheric carbon dioxide concentrations (CA) mandate techniques for examining impacts on terrestrial ecosystems. Most ...

Measuring Carbon-based Contaminant Mineralization Using Combined CO2 Flux and Radiocarbon Analyses

A method is described which uses the absence of radiocarbon in industrial chemicals and fuels made from petroleum feedstocks which frequently contaminate the environment. This radiocarbon signal &#8212; or rather the absence of signal &#8212; is evenly distributed throughout a contaminant source pool (unlike an added tracer) and is not impacted by biological, chemical or physical processes (e.g., the 14C radioactive decay rate is immutable). If the fossil-derived contaminant is fully degraded to CO2, a harmless end-product, that CO2 will contain no radiocarbon. CO2 derived from natural organic matter (NOM) degradation will reflect the NOM radiocarbon content (usually &#60;30,000 years old). Given a known radiocarbon content for NOM (a site background), a two end-member mixing model can be used to determine the CO2 derived from a fossil source in a given soil gas or groundwater sample. Coupling the percent CO2 derived from the contaminant with the CO2 respiration rate provides an estimate for the total amount of contaminant degraded per unit time. Finally, determining a zone of influence (ZOI) representing the volume from which site CO2 is collected allows determining the contaminant degradation per unit time and volume. Along with estimates for total contaminant mass, this can ultimately be used to calculate time-to-remediate or otherwise used by site managers for decision-making.

Measuring Carbon-based Contaminant Mineralization Using Combined CO2 Flux and Radiocarbon Analyses

A protocol is described wherein CO2 mineralized from organic contaminant (derived from petroleum feedstocks) biodegradation is trapped, quantified, and analyzed for 14C content. A model is developed to determine CO2 capture zone's spatial extent. Spatial and temporal measurements allow integrating contaminant mineralization rates for predicting remediation extent and time.

A method is described which uses the absence of radiocarbon in industrial chemicals and fuels made from petroleum feedstocks which frequently contaminate ...

Methods of Soil Resampling to Monitor Changes in the Chemical Concentrations of Forest Soils

Recent soils research has shown that important chemical soil characteristics can change in less than a decade, often the result of broad environmental changes. Repeated sampling to monitor these changes in forest soils is a relatively new practice that is not well documented in the literature and has only recently been broadly embraced by the scientific community. The objective of this protocol is therefore to synthesize the latest information on methods of soil resampling in a format that can be used to design and implement a soil monitoring program. Successful monitoring of forest soils requires that a study unit be defined within an area of forested land that can be characterized with replicate sampling locations. A resampling interval of 5 years is recommended, but if monitoring is done to evaluate a specific environmental driver, the rate of change expected in that driver should be taken into consideration. Here, we show that the sampling of the profile can be done by horizon where boundaries can be clearly identified and horizons are sufficiently thick to remove soil without contamination from horizons above or below. Otherwise, sampling can be done by depth interval. Archiving of sample for future reanalysis is a key step in avoiding analytical bias and providing the opportunity for additional analyses as new questions arise.

Repeated soil sampling has recently been shown to be an effective way to monitor forest soil change over years and decades. To support its use, a protocol is presented that synthesizes the latest information on soil resampling methods to aid in the design and implementation of successful soil monitoring programs.

Recent soils research has shown that important chemical soil characteristics can change in less than a decade, often the result of broad environmental ...

Continuous Instream Monitoring of Nutrients and Sediment in Agricultural Watersheds

Pollutant concentrations and loads in watersheds vary considerably with time and space. Accurate and timely information on the magnitude of pollutants in water resources is a prerequisite for understanding the drivers of the pollutant loads and for making informed water resource management decisions. The commonly used &#34;grab sampling&#34; method provides the concentrations of pollutants at the time of sampling (i.e., a snapshot concentration) and may under- or overpredict the pollutant concentrations and loads. Continuous monitoring of nutrients and sediment has recently received more attention due to advances in computing, sensing technology, and storage devices. This protocol demonstrates the use of sensors, sondes, and instrumentation to continuously monitor in situ nitrate, ammonium, turbidity, pH, conductivity, temperature, and dissolved oxygen (DO) and to calculate the loads from two streams (ditches) in two agricultural watersheds. With the proper calibration, maintenance, and operation of sensors and sondes, good water quality data can be obtained by overcoming challenging conditions such as fouling and debris buildup. The method can also be used in watersheds of various sizes and characterized by agricultural, forested, and/or urban land.

With the advancement of technology and the rise in end-user expectations, the need and use of higher temporal resolution data for pollutant load estimation has increased. This protocol describes a method for continuous in situ water quality monitoring to obtain higher temporal resolution data for informed water resource management decisions.

Pollutant concentrations and loads in watersheds vary considerably with time and space. Accurate and timely information on the magnitude of pollutants in ...

Measuring and Mapping Patterns of Soil Erosion and Deposition Related to Soil Carbonate Concentrations Under Agricultural Management

Spatial patterns of soil erosion and deposition can be inferred from differences in ground elevation mapped at appropriate time increments. Such changes in elevation are related to changes in near-surface soil carbonate (CaCO3) profiles. The objective is to describe a simple conceptual model and detailed protocol for repeatable field and laboratory measurements of these quantities. Here, accurate elevation is measured using a ground-based differential global positioning system (GPS); other data acquisition methods could be applied to the same basic method. Soil samples are collected from prescribed depth intervals and analyzed in the lab using an efficient and precise modified pressure-calcimeter method for quantitative analysis of inorganic carbon concentration. Standard statistical methods are applied to point data, and representative results show significant correlations between changes in soil surface layer CaCO3 and changes in elevation consistent with the conceptual model; CaCO3 generally decreased in depositional areas and increased in erosional areas. Maps are derived from point measurements of elevation and soil CaCO3 to aid analyses. A map of erosional and depositional patterns at the study site, a rain-fed winter wheat field cropped in alternating wheat-fallow strips, shows the interacting effects of water and wind erosion affected by management and topography. Alternative sampling methods and depth intervals are discussed and recommended for future work relating soil erosion and deposition to soil CaCO3.

Spatial patterns of soil erosion and deposition can be inferred from differences in ground elevation mapped at appropriate time increments. Such changes in elevation are related to changes in near-surface soil carbonates. Repeatable methods for field and laboratory measurements of these quantities and data analysis methods are described here.

Spatial patterns of soil erosion and deposition can be inferred from differences in ground elevation mapped at appropriate time increments. Such changes ...

Measuring Phosphorus Release in Laboratory Microcosms for Water Quality Assessment

Phosphorus (P) is a critical limiting nutrient in agroecosystems requiring careful management to reduce transport risk to aquatic environments. Routine laboratory measures of P bioavailability are based on chemical extractions performed on dried samples under oxidizing conditions. While useful, these tests are limited with respect to characterizing P release under prolonged water saturation. Labile orthophosphate bound to oxidized iron and other metals can rapidly desorb to solution in reducing environments, increasing P mobilization risk to surface runoff and groundwater. To better quantify P desorption potential and mobility during extended saturation, a laboratory microcosm method was developed based on repeated sampling of porewater and overlying floodwater over time. The method is useful for quantifying P release potential from soils and sediments varying in physicochemical properties and can improve site-specific P mitigation efforts by better characterizing P release risk in hydrologically active areas. Advantages of the method include its ability to simulate in situ dynamics, simplicity, low cost, and flexibility.

Accurate quantification of phosphorus (P) desorption potential in saturated soils and sediments is important for P modeling and transport mitigation efforts. To better account for in situ soil-water redox dynamics and P mobilization under prolonged saturation, a simple approach was developed based on repeated sampling of laboratory microcosms.

Phosphorus (P) is a critical limiting nutrient in agroecosystems requiring careful management to reduce transport risk to aquatic environments. Routine ...

Manufacturing Simple and Inexpensive Soil Surface Temperature and Gravimetric Water Content Sensors

Quantifying temperature and moisture at the soil surface is essential for understanding how soil surface biota respond to changes in the environment. However, at the soil surface these variables are highly dynamic and standard sensors do not explicitly measure temperature or moisture in the upper few millimeters of the soil profile. This paper describes methods for manufacturing simple, inexpensive sensors that simultaneously measure the temperature and moisture of the upper 5 mm of the soil surface. In addition to sensor construction, steps for quality control, as well as for calibration for various substrates, are explained. The sensors incorporate a Type E thermocouple to measure temperature and assess soil moisture by measuring the resistance between two gold-plated metal probes at the end of the sensor at a depth of 5 mm. The methods presented here can be altered to customize probes for different depths or substrates. These sensors have been effective in a variety of environments and have endured months of heavy rains in tropical forests as well as intense solar radiation in deserts of the southwestern U.S. Results demonstrate the effectiveness of these sensors for evaluating warming, drying, and freezing of the soil surface in a global change experiment.

Accurately measuring temperature and water content of the upper 5 mm of the soil surface can improve our understanding of environmental controls on biological, chemical, and physical processes. Here we describe a protocol for manufacturing, calibrating, and conducting measurements with soil surface temperature and moisture sensors.

Quantifying temperature and moisture at the soil surface is essential for understanding how soil surface biota respond to changes in the environment. ...

In Situ Soil Moisture Sensors in Undisturbed Soils

Soil moisture directly affects operational hydrology, food security, ecosystem services, and the climate system. However, the adoption of soil moisture data has been slow due to inconsistent data collection, poor standardization, and typically short record duration. Soil moisture, or quantitatively volumetric soil water content (SWC), is measured using buried, in situ sensors that infer SWC from an electromagnetic response. This signal can vary considerably with local site conditions such as clay content and mineralogy, soil salinity or bulk electrical conductivity, and soil temperature; each of these can have varying impacts depending on the sensor technology.
Furthermore, poor soil contact and sensor degradation can affect the quality of these readings over time. Unlike more traditional environmental sensors, there are no accepted standards, maintenance practices, or quality controls for SWC data. As such, SWC is a challenging measurement for many environmental monitoring networks to implement. Here, we attempt to establish a community-based standard of practice for in situ SWC sensors so that future research and applications have consistent guidance on site selection, sensor installation, data interpretation, and long-term maintenance of monitoring stations.
The videography focuses on a multi-agency consensus of best-practices and recommendations for the installation of in situ SWC sensors. This paper presents an overview of this protocol along with the various steps essential for high-quality and long-term SWC data collection. This protocol will be of use to scientists and engineers hoping to deploy a single station or an entire network.

In Situ Soil Moisture Sensors in Undisturbed Soils

The determination of soil water content is a critical mission requirement for many state and federal agencies. This protocol synthesizes multi-agency efforts to measure soil water content using buried in situ sensors.

Soil moisture directly affects operational hydrology, food security, ecosystem services, and the climate system. However, the adoption of soil moisture ...

Enhancing CO2 Sequestration: A Soil Biota Approach to Boost Mineral Weathering

Design and Construction of an Experimental Setup to Enhance Mineral Weathering through the Activity of Soil Organisms

Enhanced weathering (EW) is an emerging carbon dioxide (CO2) removal technology that can contribute to climate change mitigation. This technology relies on accelerating the natural process of mineral weathering in soils by manipulating the abiotic variables that govern this process, in particular mineral grain size and exposure to acids dissolved in water. EW mainly aims at reducing atmospheric CO2 concentrations by enhancing inorganic carbon sequestration. Until now, knowledge of EW has been mainly gained through experiments that focused on the abiotic variables known for stimulating mineral weathering, thereby neglecting the potential influence of biotic components. While bacteria, fungi, and earthworms are known to increase mineral weathering rates, the use of soil organisms in the context of EW remains underexplored. 
 This protocol describes the design and construction of an experimental setup developed to enhance mineral weathering rates through soil organisms while concurrently controlling abiotic conditions. The setup is designed to maximize weathering rates while maintaining soil organisms' activity. It consists of a large number of columns filled with rock powder and organic material, located in a climate chamber and with water applied via a downflow irrigation system. Columns are placed above a fridge containing jerrycans to collect the leachate. Representative results demonstrate that this setup is suitable to ensure the activity of soil organisms and quantify their effect on inorganic carbon sequestration. Challenges remain in minimizing leachate losses, ensuring homogeneous ventilation through the climate chamber, and avoiding flooding of the columns. With this setup, an innovative and promising approach is proposed to enhance mineral weathering rates through the activity of soil biota and disentangle the effect of biotic and abiotic factors as drivers of EW.

Author Spotlight: Unraveling the Role of Earthworms in Enhancing Mineral Weathering for CO2 Removal 

Here we present the construction and operation of an experimental setup to enhance mineral weathering through the activity of soil organisms while concurrently manipulating abiotic variables known to stimulate weathering. Representative results from the functioning of the setup and sample analyses are discussed together with points for improvement.

Enhanced weathering (EW) is an emerging carbon dioxide (CO2) removal technology that can contribute to climate change mitigation. This technology relies ...

Monitoring Pedogenic Inorganic Carbon Accumulation Due to Weathering of Amended Silicate Minerals in Agricultural Soils.

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