Acidification Assessment after Peat Bog Drainage in the Catalan Pyrenees (NE Iberia)
Department of Environment and Soil Sciences, University of Lleida, 25003 Lleida, Spain
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Author to whom correspondence should be addressed.
Quaternary 2019, 2(3), 32; https://doi.org/10.3390/quat2030032
Submission received: 25 June 2019
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Revised: 9 September 2019
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Accepted: 16 September 2019
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Published: 18 September 2019
(This article belongs to the Special Issue Peatlands: Outstanding Witnesses of the Environmental Evolution of Southern Europe)
Abstract
:The Pyrenean range (NE Iberian Peninsula) has some favourable lithological and climatic conditions (iron-rich parent materials and udic moisture regimes) for the formation of acid sulfate soils (ASS) that have not been reported on from the region until now. The analyses of a drained peat bog near València d’Àneu revealed a pH (1:2.5) of 3.7. We hypothesize that it contained sulfidic materials that were oxidized during drainage, which could have caused its acidification. The main goal of this study is to understand the characteristics and the potential acidity of these organic soils and the consequences that this could generate in the current environment. In order to do so, several profiles were described and sampled in the field for chemical and micromorphological analyses. The results show that the oxidation of the newly formed pyrite in the soil or pyrite contained in the Cambro–Ordovician parent material was responsible for the low pH and high electrical conductivity (EC). The soils still contain sulfidic materials at present, which could be oxidized in the future, with the consequent risk for water quality. The results will be useful to evaluate the risk of other peats in the Pyrenees becoming acid sulfate soils if drained.
1. Introduction
Acid sulfate soils (ASS) are soils or sediments with a very low pH due to the oxidation of iron sulfides (termed “actual ASS”), and/or soils containing iron sulfides or other sulfidic materials that have not been exposed to air and oxidised (“potential ASS”) [1,2,3,4,5]. Actual and potential ASS are often found in the same soil profile [6].
Acid sulfate soils worldwide occupy an area of at least 17 million ha [7]. They are mostly located in tropical coastlands but they are also found in higher latitudes, as in several countries in Central and North Europe [8]. While they are generally associated with coastal areas, inland ASS are also profusely reported, mainy in Australia, in Fe-rich areas subjected to waterlogging [8,9].
In the Iberian Peninsula, sulfaquents have been reported in the north, where they occupy an area of only 53.6 km2 [10]. They contain sulfidic materials at a given depth and are permanently saturated with brackish water [11]. They are found in coastal marshes and depressions associated with hydraquents and salids. Sulfaquents also appear in the Ebro Delta and in other Mediterranean coastal areas [12]. When drained or exposed to aerobic conditions, the sulfidic materials oxidize and the soils become extremely acidic (pH < 3.0) since the buffering capacity is too low to neutralize the sulfuric acid formed (e.g., as in the Tinto and Odiel rivers, in the Province of Huelva) [11].
The occurrence of peatlands in the Pyrenees range is widely recognized and some of them have been profusely studied, mostly as a tool to study landscape evolution during the Quaternary [13,14]. On the contrary, no data exist about the possible risks associated with their management.
The Pyrenean range (NE Spain) has some favourable lithological and climatic conditions (iron-rich parent materials and udic moisture regimes) for the formation of acid sulfate soils. In spite of that, they have never been reported until now, probably due to the lack of adequate geomorphic locations with strong reducing conditions. In this context, the earthworks associated with the construction of the C-28 road near València d’Àneu totally modified the morphology of a 2.8 ha old peat bog, partly drained at present, on the right bank of the Bonaigua River, at an altitude of 1500 m above sea level. The peat bog is composed of two clearly differentiated sedimentary units: The upper unit, mainly organic, and the lower unit, containing granite with gravels and some boulders in the transition between the two units [15]. In the shallowest part, a peaty horizon is described in which secondary roots abound and at a greater depth (146 to 150 cm) a silty clay phase of a few centimeters thick is present where the peat practically disappears. From the surface to 2 m deep, stems, tubular roots and plant remains, mainly wood, are present. In this spot, a soil monolith was extracted as part of the Pyrenean Soil Museum Project of the Institut Cartogràfic i Geològic de Catalunya (ICGC). Baltiérrez [16] described the monolith’s profile as having the following sequence: A-H1-H2-H3-2Bg-H4-3Bg-H5 and classified it as Fluvaquentic Haplofibrists [17] or Fibric Histosol [18].
The preliminary analyses revealed a high electrical conductivity (EC) in the first organic horizons reaching levels of 9.23 dS/m at 25 °C and an actual or effective acidity around pH 3.7 (1:2.5 soil:water) and around pH 2.5 (1:5 soil:water). We hypothesize that the old peat bog contained sulfidic materials that were oxidized during the drainage, which could have caused a decrease in pH in organic soils.
Acid sulfate soils are hazardous to natural and managed ecosystems [19]. In particular, potential ASS, when drained, can be responsible for fresh water acidification, which in mountain environments such as the Pyrenees could severely affect aquatic and soil ecosystems. Management techniques to minimize these hazards rely on the correct identification and classification of ASS materials [20].
The aim of this study is the characterization of partly drained peat bog soil in the Catalan Pyrenees in order to determine the origin of the acidity, salinity and net acidity. The results will be useful to locate other spots with acidification risk and eventually to add it to the geological risk programme of the ICGC.
2. Materials and Methods
2.1. Site Description
The study area is located in the Catalan Pyrenees (NE Iberian Peninsula). The characterized peatland is located 63 km from the C-28 road, between Prats de la Vila and Campolado, near València d’Àneu (Figure 1). The altitude is 1150 m asl and it has an extension of around 2.8 ha.
The area has a western Mediterranean climate with an oceanic influence and an average annual precipitation of 1181 mm, which is concentrated in autumn, winter and spring. The average annual temperature is 3 °C, which varies from −4.8 to −1.9 °C during the winter and from 9.2 to 11.6 °C in the summer, for the period 2001–2017. The soil moisture and temperature regimes are udic and frigid, respectively [21].
Geologically, the peat bog of València d’Àneu is located in the Pyrenean Axial Zone, where the substratum is formed by Paleozoic rocks of ages between the Cambro-Ordovician and Upper Ordovician and the overlying Holocene deposits [22]:
- Cambro-Ordovician sedimentary materials: Rhythmic alternation of quartzitic sandstones with feldspars and slaty lutitic layers, with thicknesses ranging from a few centimeters to few decimeters. They form a thick and monotonous series, with some intercalations of black shades or very dark gray with iron sulfides, which give reddish colours when altered.
- Sedimentary materials: Formed by carbonaceous black shales, very rich in organic remains and sulfides. They are characterized by being relatively soft, and have grayish or whitish colours due to their superficial alteration. They are interpreted as marine sediments, deposited in low oxygenated environments that favor the accumulation of organic matter and the precipitation of sulfides.
Finally, Losantos [22] described that the materials found in the peat bog of València d’Àneu possibly accumulated in a glacial excavation pit: Its filling would be formed by a lower section of glacial deposits (conglomerates of granitic blocks), with gravels and boulders in the upper part that would indicate the circulation of surface water on top of the peat, formed with abundant plant remains.
The vegetation that surrounds the peat bog is represented by some deciduous oaks (Quercus sp.) that are combined with hazel trees (Corylus sp.), birches (Betula sp.) and pines (Pinus sp.), and, in many cases, they occupy abandoned fields [16]. The land use of peat bog is mainly forestry, but the central zone is used for cattle grazing.
2.2. Soil Sampling, Morphology and Micromorphology
Three profiles were described and classified in the study area following SINEDARES [23] and Soil Taxonomy [18]. For each profile, 0.5 kg of sample from each horizon was collected. Elements which could interfere with subsequent analyses such as shells, gravel, coal or others were discarded [24].
Furthermore, two undisturbed soil samples (corresponding to two subsurface organic horizons of profiles 1 and 2) were taken for micromorphological analysis following the specifications of Benyarku and Stoops [25]. The blocks were dried at room temperature and impregnated with polyester resin. One vertical thin section (50-mm wide, 130-mm long) was made from each block. Subsequently, they were studied using a polarizing microscope following the guidelines of Stoops [26]. The thin sections were used as a complement to the chemical methods; specifically, to determine the presence of diagnostic minerals such as pyrite, gypsum or jarosite indicating reduction or oxidation processes.
2.3. Laboratory Methods: Physical and Chemical Analysis
In the laboratory, part of each sample was air-dried in a fan-forced oven set at 80 to 85 °C for at least 48 h to minimize oxidation of pyrite [27,28]. All samples were sieved gently to 2 mm before being analyzed. Electrical conductivities (ECs) were determined with a glass electrode (CRISON GLP31) in a 1:5 soil/water suspension following the directions of Jayalath [28].
Organic carbon was measured using the Walkley–Black method, through an acid-dichromate digestion [29]. For those samples exceeding 8% of organic carbon, the ignition method was applied [30]. It consisted of combustion at 550 °C for 6 hours in a muffle furnace (HERON 12-PR).
Soil reaction or pH was determined with a pH meter (HACH, GLP 22) in 1:1 and 1:2.5 soil/water suspensions [25,29]. The potential acidity was also measured with a pH meter in a 1:2.5 soil/1N KCl solution [29]. Finally, the samples were treated with hydrogen peroxide (H2O2) using a 1:1 soil/30% hydrogen peroxide solution, to determine the pH after oxidation of sulfur ions [28].
Qualitative reaction to sulfur and chloride was determined with the reagents BaCl2 and AgNO3 at 10%, respectively. The reaction was positive when the extracts showed a white precipitate [29].
The SPOCAS (peroxide oxidation combined acidity and sulfur) method was applied to obtain the total potential acidity, which is determined as the sum of the soil’s potential sulfidic acidity and the actual acidity on two sub-samples or trails (called acidity trail and sulfur trail), according to the following equation:
Net acidity = potential sulfidic acidity + actual acidity + retained acidity – measured acid neutralising capacity (ANC)/fineness factor
The Actual Acidity is a measure of current acidity in ASS. The potential sulfidic acidity in ASS is defined as the latent acidity released if all sulfide minerals they contain are oxidised [27].
The retained acidity is the acidity stored in largely insoluble compounds such as jarosite and other iron and aluminium sulfate minerals; in other words, it refers to the more recalcitrant sulfidic elements contributing to the net acidity when they progressively oxidize over time [8,27].
The acid neutralising capacity (ANC) indicates the buffering potential of the soil to acidification and to maintain pH to acceptable levels (e.g., pH 6.5–9.0). It depends on the types and quantities of clay minerals, carbonates or other minerals in the soil [27].
The acid trail of the SPOCAS method determines the titratable actual acidity (TAA), titratable peroxide acidity (TPA) and titratable sulfidic acidity (TSA). The TAA is measured in a 1:40 suspension of soil sample/1M KCl, while TPA is measured in a 1:40 soil sample/30% hydrogen peroxide [27,31]. TSA is the difference between TAA and TPA.
The sulfur trail of the SPOCAS method determines the peroxide oxidisable sulfur (SPOS), which is a measure of the reactive sulfides present in the soil sample. It is obtained from the difference between the sulfur determined in the peroxide digest (Sp) and the sulfur extracted by 1M KCl (SKCl) [27].
Finally, the net acidity or ABA (acid base account) equation is calculated according to Ahern et al. [27] depending on the obtained pH KCl ranges.
3. Results and Discussion
3.1. Morphology and General Soil Characteristics of the Profiles
The general physicochemical soil characteristics of the studied area are shown in Table 1 and Table 2. The topsoil has a crumb structure, with hydrophobic properties. The H horizons contain frequent reed residues with varying degrees of decomposition and charcoal fragments. At depths of 67 (profile 1) and 36 cm (profile 2) reddish mottles due to oxidation appear (hues 7.5YR and 5YR). The textures of the mineral horizons are sandy or sandy loam. Bulk densities of the organic horizons vary between 0.18 and 0.49 Mg/m3.
Profiles 1 and 2 were provisionally classified as Fluvaquentic Haplofibrists.
3.2. Organic Matter
Peat bogs are soils formed by the accumulation of organic matter (OM) in areas with poor drainage. Table 2 and Table 3 show that the maximum OM content is normally found at the surface. Down the profile, it gradually decreases in the first few centimeters until reaching a point where it decreases drastically (profile 2). Moreover, profile 1 contains an organic layer at a depth of one meter deeper than the others—below a 2C horizon that represents an intercalation of slope colluvium.
OM contents obtained by the Walkley–Black and calcination methods differ from each other, although the techniques are not comparable. The organic matter values according to the Walkley–Black method (which underestimates soil organic carbon) [30] have a range of 9.6 to 29.1% in the genetic horizons designated as H in the field, while in the rest they do not exceed 15.2%. The results of the calcination method range of 10.4 to 40.4% of organic matter in the organic H horizons.
The Ap horizon of profile 1 has the highest content of organic matter (48.9%, calcination method) compared to those designated in the field as H. The high content of organic matter could be due to ploughing, which mixes materials of the topsoil with the H1 horizon. However, according to soil taxonomy [17] and the Soil Survey Laboratory [30], this horizon would have to be designated as an H horizon, the sequence of genetic horizons of the profile being the following: H1, H2, H3, 2C and H4. In the case of the Oi horizon of profile 2, the organic carbon content does not exceed 20%; therefore, it would be more suitable to designate it as A.
3.3. Micromorphology
A summary of the micromorphological descriptions of the two thin sections of the H horizons of profiles 1 and 2, following the criteria of Zaiets and Poch [32] can be seen in Table 3.
The fabric of both materials is similar: Mainly layered (medium to large organic remains with a subhorizontal orientation referred to the soil surface) and a juxtaposed fine granular structure due to faunal activity. Both materials have an undifferentiated b-fabric due to the masking effect by the organic matter, and the plant residues are phlobaphenized (containing reddish compounds from the oxidation of tannins). The H2 horizon of profile 1 has abundant fan-like arranged prismatic gypsum crystals as pedofeatures (gypsum rosettes), showing the typical prismatic habit of acidic environments [33,34] (Figure 2). It agrees with the positive qualitative reaction to sulfates (Table 1), while in profile 2 it is negative. The origin of gypsum is therefore the oxidation of pyrite-sulfur present in soil and its combination with Ca2+ in the soil solution. The precipitation of gypsum did not buffer all the potential acidity, probably due to the depletion of the Ca2+ source (low Ca2+ availability), since the present pH are strongly acidic, and also because jarosite formed in both profiles (Figure 2). It is found associated with plant rests and also as aggregates, which can be indicative of former pyrite-bearing soils. Indeed, no pyrite framboids have been observed in the horizons, although possible pseudomorphs after pyrite were detected associated with organic remains (Figure 2d). Therefore, we think that the oxidation of fine primary pyrite contained in the Cambro-Ordovician parent material, not observable in thin sections, could be the main cause of the existence of sulfidic materials [34]. The H horizon of profile 2 shows almost no gypsum.
3.4. Electrical Conductivities and Chloride and Sulfate Tests
The electrical conductivity values are highly variable between profiles and within profiles. Profile 1 shows EC (1:5) values of 4 dS/m to 1.7 dS/m at 25 °C, increasing with depth until the deepest horizon, with a value of 8.2 dS/m at 25 °C. Profile 3 is also highly saline, with values between 1.3 and 9.2 dS/m at 25 °C. On the other hand, the EC (1:5) of profile 2 is higher at the topsoil (0.7 dS/m at 25 °C) and decreases with depth. The high values of EC are associated with the qualitative presence of sulfates and not of chlorides; therefore, the salinity would have been developed by oxidation of sulfides.
From the tests, the hypothesis that the origin of the high conductivity in some horizons is the salt applied to the roads to prevent frost can be discarded. Instead, the origin of the high conductivity is the sulfur in the parent material of the study area as indicated by Losantos [22].
3.5. Soil Reaction
In profile 1, the pH in water varies between 2.1 and 4.2 while in profile 2 the range is from 5 to 6.7. Isbell [4] defines that values of pH(w) ≤ 4 are indicative of sulfide oxidation processes. Therefore, all layers of profile 1 undergo sulfide oxidation processes and meet the characteristics of an acid sulfate soil. On the other hand, profile 2 has acidic to neutral pH values, which is why, so far, it has not been designated as an acid sulfate soil.
In profile 2, the pH in KCl presents values, in general, lower than the pH in water, usually between 0.5 and 1 pH units, as is the case in soils with a cation exchange capacity. However, in some horizons of profile 1, the pH (KCl) is equal or higher than the pH(w), indicating that they have a variable charge and are close to the zero point of charge or the isoelectric point, probably caused by amorphous organic matter.
The pH(ox) values of profile 1 are similar along the profile, with the organic horizons having the lowest values, and they comply with the pH(ox) ≤ 2, indicative of a high sulfide content [27]. In contrast, in profile 2, the inorganic horizons, 2Cg1 and 2Cg2 have values higher than 2, 2.6 and 3.8, respectively. These, together with horizon A of profile 3, would confirm their low sulfide content. In addition, the reaction to hydrogen peroxide (30% H2O2) of those samples with lower pH(ox) is strong, indicating high sulfur content.
Finally, the comparison between pH(w) and pH(ox) allows us to designate profile 1 as a current acid sulfate soil, while profile 2 should be a potential acid sulfate soil [28]. However, since profile 2 is completely drained (and oxidized at present) the designation of potential acid sulfate soil would not be correct. Another option would be to designate it as a recently post-active acid sulfate soil. On the other hand, this classification has been made from the data obtained in the laboratory when it is recommended that the assignment of the SSA typology be carried out in the field using the values obtained of pH (F) and pH (FOX), that is, pH in water in the field and pH with peroxide in the field, to avoid redox reactions after taking the samples.
3.6. Peroxide Oxidation Combined Acidity and Sulfur (SPOCAS) Method
The results of the application of this set of analyses are found in Table 4. Profile 1 shows TAA values of 247.6 H+/t to 903.9 mol H+/t, increasing with depth until the deepest horizon, with a value of 903.9 mols H+/t. On the other hand, profile 2 has less acidity, since the values are between 8.5 and 4.8 mol H+/t, the maximum value being 144.2 mol H+/t in H1 horizon. This horizon may still have some acidity resources and it is important to determine the acid sulfate soil type because this acidity could be discharged after a strong rainfall, for example.
The titratable peroxide acidity or TPA is zero in the Oi, 2Cg1 and 2Cg2 horizons of profile 2. It indicates that the soil’s buffering capacity equals the potential acidity from oxidation of sulfides [27]. On the other hand, the TPA > 0 in the rest of the samples indicates the opposite, this means that in profile 1 and some horizons (H1 and H2) in profile 2 there is a varying amount of pyrite and the reactivity of the carbonate is low.
The reacted calcium and magnesium (CaA and MgA) in both profiles are low (not higher than 0.5%). For this reason they should be ignored in the ABA equation [27].
The ‘sulfur trails’ of SPOCAS (SKCl and Sp) are shown in Table 4. The SPOS results obtained in both profiles are between 0.01% and 0.79% and have a maximum of 0.79% in profile 1 (H3) and 0.31% in profile 2 (H1). Generally, high values of SPOS are indicative of reduced or PASS (potential acid sulfate soils) samples because they have a lot of recalcitrant oxidizable sulfur, but may differ on partially oxidized and surface samples [27].
Finally, the net acidity or acid base account equation is calculated using the results of Table 4. Some of the horizons of profile 2 have TPA < 0 and pH ranges between 6.2 and 4.6 units; therefore, net acidity cannot be calculated since, according to the values obtained for the SPOCAS method, they do not represent a risk. The results of net acidity (%S and mol H+/t), SPOS and TAA with unit conversion are shown in Table 5.
In profile 1, the content of actual acidity is between 67.3 mol H+/t and 903.9 mol H+/t; this is directly related to the low pH values and the higher actual acidity values. In profile 2, the values of actual acidity are lower (272.5 and 572.5 mol H+/t). On the other hand, the content of potential acidity is between 34.9 and 489.6 mol of H+/t in profile 1 and lower (192.7 and 102.9 mol of H+/t) in the H horizons of profile 2. These differences between profiles and horizons could be due to:
- The initial content of pyrite in the horizons. The successive accumulation of detrital materials from upslope combined with periods of peat formation could be the cause of varying pyrite contents along the profile, and therefore of variable potential acidity.
- Part of the pyrite content having already been oxidized due to the drainage works. Again, the degree of oxidation varies depending on local profile conditions and also on the position and characteristics of the horizons.
As a consequence, the potential acidity of the study area should be calculated based on the assignment of a profile type. For soils similar to profile 1, the acidity that can be produced is 261 mol H+ while for soils similar to profile 2 it is 22.3 mol.
3.7. Implications for Acidification Risk Assessment in the Pyrenees
Our study is the first record of ASS in the Pyrenees. A comprehensive assessment of the effect of acid effluents due to the drainage of existing peatlands has never been made. In spite of that, acidic drainage has indeed been reported in some small rivers of Pyrenean valleys (pH between 4.4 and 5.2) subjected to alternating dry and wet seasons and causing the precipitation of Al-hydroxysulfates on river gravels [35,36].
The survey and mapping of the geological hazards in Catalonia is at present carried out by the ICGC, which could include these risks as in Bui [37], through a detailed location of peat bogs and of Fe-rich parent materials, together with the analytical characterization of selected sites.
4. Conclusions
The presented scheme provides a nearly complete analytical procedure for the characterization of acid sulfate soils (ASS) present in the first ASS reported in the Catalan Pyrenees. The results permit the distinction between different acid sulfate soil types and provide information about potential acidity. The potential acidity that can be generated in the next few years is 283.3 mol H+ if pH correction methods are not applied. The difference between profiles in terms of potential acidity could be due to: (1) The initial content of pyrite or (2) that part of the pyrite that has already been oxidized. This is reflected in the micromorphology of the profiles, one of them more oxidized (profile 1) and with the sulfate partly buffered by gypsum precipitation, and the other (profile 2) with more jarosite. Besides this first characterization of acid sulfate soil in Catalonia, this study will help to assess potential locations of other ASS in the Catalan Pyrenees with similar conditions (e.g., iron-rich parent material, udic moisture regimes, waterlogging) and to evaluate environmental risks related to their management.
Author Contributions
Conceptualization, R.M.P.; methodology, A.C., M.A.; investigation, A.C.; resources, R.M.P.; writing—original draft preparation, A.C.; writing—review and editing, A.C., R.M.P.; supervision, R.M.P.; funding acquisition, R.M.P.
Funding
This research was funded by Institut Cartogràfic i Geològic de Catalunya (ICGC).
Acknowledgments
We acknowledge José Manuel Plata for the preparation of the soil thin sections.
Conflicts of Interest
The authors declare no conflict of interest.
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Figure 1.
Location of the study site (València d’Àneu, Lleida). The characterized peatland is located 63 km from the C-28 road, between Prats de la Vila and Campolado. The yellow circles indicate the observations made in the field, while the green circles refer to the study pits.
Figure 1.
Location of the study site (València d’Àneu, Lleida). The characterized peatland is located 63 km from the C-28 road, between Prats de la Vila and Campolado. The yellow circles indicate the observations made in the field, while the green circles refer to the study pits.
Figure 2.
Microphotographs of selected features: (a) Gypsum rosettes in profile 1 (left: Parallel polarizers (PPL), right: Crossed polarizers (XPL)); (b) jarosite coating in a plant residue, profile 1 (left: PPL, right: Oblique incident light (OIL)); (c) jarosite hypocoating of around a pore, profile 2 (left: PPL, right: OIL); (d) iron oxide nodules, possibly pseudomorphs after pyrite framboids, profile 2 (left: PPL, right: OIL). PPL: Parallel polarizers, XPL: Crossed polarizers, OIL: Oblique incident light.
Figure 2.
Microphotographs of selected features: (a) Gypsum rosettes in profile 1 (left: Parallel polarizers (PPL), right: Crossed polarizers (XPL)); (b) jarosite coating in a plant residue, profile 1 (left: PPL, right: Oblique incident light (OIL)); (c) jarosite hypocoating of around a pore, profile 2 (left: PPL, right: OIL); (d) iron oxide nodules, possibly pseudomorphs after pyrite framboids, profile 2 (left: PPL, right: OIL). PPL: Parallel polarizers, XPL: Crossed polarizers, OIL: Oblique incident light.
Figure 3.
Variation in depth of the different types of pH obtained for profile 1.
Table 1.
Main physicochemical soil characteristics of profiles 1 and 2. EC: Electrical conductivity; OM: Organic matter; W&B: Walkley–Black method.
Table 1.
Main physicochemical soil characteristics of profiles 1 and 2. EC: Electrical conductivity; OM: Organic matter; W&B: Walkley–Black method.
| Depth (cm) | Horizon | Munsell Colour (moist) | Bulk Density (Mg/m3) | EC(1:5) (dS/m at 25 °C) | Chloride Test | Sulfate Test | OM (%) W&B | OM (%) Calcination | pH(w) 1:1 | pH(w) 1:2.5 | pH(KCl) 1:2.5 | pH(ox) |
|---|---|---|---|---|---|---|---|---|---|---|---|---|
| Profile 1 | ||||||||||||
| 0–18 | Ap | 7.5YR 3/2 | 0.48 | 3.9 | Negative | Positive | 15.2 | 48.9 | 3.4 | 4.2 | 4.0 | 1.6 |
| 19–55 | H1 | 5YR 2/2 | 0.18 | 4.0 | Negative | Positive | 27.7 | 40.4 | 3.3 | 3.4 | 3.1 | 1.3 |
| 56–66 | H2 | 7.5YR 3/2 | 0.49 | 2.8 | Negative | Positive | 9.6 | 10.4 | 3.4 | 3.4 | 3.2 | 1.5 |
| 67–80 | 2C | 2.5YR 4/2 | 0.75 | 1.7 | Negative | Positive | 1.9 | - | 3.4 | 3.6 | 3.2 | 1.9 |
| 81–111 | H3 | 5YR 3/3 | 0.23 | 8.2 | Negative | Positive | 22.1 | 27.6 | 2.1 | 2.3 | 2.3 | 1.0 |
| Profile 2 | ||||||||||||
| 0–12 | Oi | 7.5YR 2/1 | 0.43 | 0.7 | Negative | Negative | 10.7 | 27.1 | 6.3 | 6.5 | 5.7 | - |
| 12–20 | H1 | 5YR 2/2 | 0.37 | 0.4 | Negative | Negative | 29.1 | 32.2 | 5.1 | 5.2 | 4.3 | 1.8 |
| 21–35 | H2 | 7.5YR 4/2 | 0.49 | 0.3 | Negative | Negative | 18.3 | 20.0 | 5.0 | 5.1 | 4.2 | 1.9 |
| 36–45 | 2Cg1 | 10YR 5/2 | 1.10 | 0.1 | Negative | Negative | 2.3 | - | 5.7 | 5.7 | 4.3 | 2.6 |
| 46–65 | 2Cg2 | 10YR 5/2 | 1.34 | 0.04 | Negative | Negative | 1.2 | - | 6.7 | 6.6 | 5.3 | 3.8 |
Table 2.
Selected physicochemical soil characteristics of profile 3. EC: Electrical conductivity; OM: Organic matter; W&B: Walkley–Black method; CEC: Cation exchange capacity.
Table 2.
Selected physicochemical soil characteristics of profile 3. EC: Electrical conductivity; OM: Organic matter; W&B: Walkley–Black method; CEC: Cation exchange capacity.
| Depth (cm) | Horizon | Munsell Colour (moist) | Textural Class (USDA) | EC (1:5) (dS/m at 25 °C) | OM (%) W&B | CEC (cmol(+)/kg) | pH(w) 1:2.5 | pH(w) 1:5 |
|---|---|---|---|---|---|---|---|---|
| 0–20 | A | 10YR 4/3 | Sandy loam | 1.7 | 4.0 | 11.5 | 3.7 | - |
| 21–38 | H1 | 10YR 2/1 | - | 4.7 | 30.2 | 54.8 | - | 2.8 |
| 39–50 | H2 | 2.5YR 3/2 | - | 9.2 | 38.4 | 49.2 | - | 2.3 |
| 51–70 | H3 | 10YR 2/1 | - | 5.9 | 33.9 | 61.4 | - | 3.4 |
| 71–100 | 2Bg | 5/5GY | Sandy loam | 1.4 | 2.2 | 5.6 | 3.7 | - |
Table 3.
Micromorphological description of organic horizons of profiles 1 and 2.
| Feature | Profile 1, Horizon H2 | Profile 2, Horizon H2 |
|---|---|---|
| Porosity and microstructure | 50%, compound packing pores. Fine crumb structure. | 40%, compound packing pores and fissures. Juxtaposed fine crumb structure and fine subangular blocky. |
| Organs and tissues | Large (max 1 cm) reed remains, layered, moderately decomposed, tissue (parenchima) fragments, phlobaphenized, coarse sand size, random and layered. About 20% of the volume. | Medium (2 mm) plant remains, layered, mainly roots and shoots, phlobaphenized. Some fungal sclerotia. About 15% of the volume. |
| Amorphous organic material | Reddish amorphous material, speckled. Undifferentiated b-fabric. | Brownish amorphous material, speckled. Undifferentiated b-fabric. |
| Faunal excrements | Abundant small excrements, as infillings of channels and also associated with plant remains. | Frequent small excrements, as infillings of channels and associated with plant remains. |
| Mineral components | Medium sand of schists and quartzites | Medium sand of schists and quartzites |
| Other pedofeatures | Very abundant gypsum rosettes (fan-like) made of prismatic gypsum crystals, medium sand size. Nodules, coatings and impregnative hypocoatings of jarosite around plant remains. | Very few gypsum rosettes, in plant rests. Nodules, coatings and impregnative hypocoatings of jarosite around plant rests. Hypocoatings and nodules of iron oxides, associated with plant rests. |
Table 4.
SPOCAS results obtained in profiles 1 and 2. TAA: Titratable actual acidity; TPA: Titratable peroxide acidity; TSA: Titratable sulfidic acidity; S(POS): Peroxide oxidisable sulfur; (p): Peroxide; (a): Reactive.
Table 4.
SPOCAS results obtained in profiles 1 and 2. TAA: Titratable actual acidity; TPA: Titratable peroxide acidity; TSA: Titratable sulfidic acidity; S(POS): Peroxide oxidisable sulfur; (p): Peroxide; (a): Reactive.
| Profile and Horizon | pH(KCl) | pH(ox) | TAA | TPA | S(KCl) | S(p) | Ca(KCl) | Ca(p) | Mg(KCl) | Mg(p) | TSA | S(POS) | Ca(a) | Mg(a) |
|---|---|---|---|---|---|---|---|---|---|---|---|---|---|---|
| pH Units | Mol H+/t | %S | %Ca | %Mg | Mol H+/t | %S | %Ca | %Mg | ||||||
| Profile 1 | ||||||||||||||
| A | 4.3 | 2.6 | 247.6 | 1336.0 | 0.57 | 1.2 | 0.99 | 1.29 | 0.04 | 0.06 | 1088.4 | 0.58 | 0.30 | 0.02 |
| H1 | 3.4 | 2.3 | 330.9 | 1490.0 | 0.70 | 1.5 | 0.69 | 0.83 | 0.01 | 0.03 | 1159.1 | 0.79 | 0.14 | 0.02 |
| H2 | 3.8 | 3.1 | 121.9 | 230.2 | 0.38 | 0.4 | 0.34 | 0.34 | 0.01 | 0.01 | 108.3 | 0.06 | 0.00 | 0.00 |
| 2C | 3.8 | 3.0 | 67.3 | 85.0 | 0.19 | 0.2 | 0.18 | 0.20 | 0.00 | 0.01 | 17.6 | 0.06 | 0.02 | 0.00 |
| H3 | 2.8 | 2.0 | 903.9 | 1580.0 | 1.78 | 2.5 | 0.70 | 0.76 | 0.04 | 0.05 | 676.2 | 0.73 | 0.06 | 0.01 |
| Profile 2 | ||||||||||||||
| Oi | 6.2 | 5.4 | 8.5 | 0.0 | 0.03 | 0.2 | 0.56 | 0.46 | 0.05 | 0.05 | < 0 | 0.16 | 0.00 | 0.00 |
| H1 | 4.4 | 3.5 | 144.2 | 572.5 | 0.05 | 0.4 | 0.32 | 1.11 | 0.02 | 0.04 | 428.3 | 0.31 | 0.79 | 0.02 |
| H2 | 4.5 | 3.6 | 63.8 | 272.5 | 0.03 | 0.2 | 0.28 | 0.34 | 0.02 | 0.03 | 208.8 | 0.17 | 0.06 | 0.01 |
| 2Cg1 | 4.6 | 4.1 | 12.3 | 0.0 | 0.02 | 0.0 | 0.06 | 0.08 | 0.01 | 0.01 | < 0 | 0.01 | 0.02 | 0.00 |
| 2Cg2 | 5.4 | 5.8 | 4.8 | 0.0 | 0.02 | 0.0 | 0.07 | 0.08 | 0.01 | 0.01 | < 0 | 0.02 | 0.02 | 0.00 |
Table 5.
Conversions and net acidity results for profiles 1 and 2. s-TAA: Actual acidity with sulfur units; a-SPOS: Potential acidity with acidity units.
Table 5.
Conversions and net acidity results for profiles 1 and 2. s-TAA: Actual acidity with sulfur units; a-SPOS: Potential acidity with acidity units.
| Horizon | s-TAA | a-SPOS | Net Acidity | Net Acidity |
|---|---|---|---|---|
| S% | mol H+/t | S% | mol H+/t | |
| Profile 1 | ||||
| A | 0.40 | 362.99 | 0.98 | 610.6 |
| H1 | 0.53 | 489.60 | 1.32 | 820.5 |
| H2 | 0.20 | 37.42 | 0.26 | 159.3 |
| 2C | 0.11 | 34.93 | 0.16 | 102.2 |
| H3 | 1.45 | 452.81 | 2.18 | 1356.7 |
| Profile 2 | ||||
| H1 | 0.23 | 192.72 | 0.54 | 337.0 |
| H2 | 0.10 | 102.91 | 0.27 | 166.7 |
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MDPI and ACS Style
Catalán, A.; Antúnez, M.; Poch, R.M. Acidification Assessment after Peat Bog Drainage in the Catalan Pyrenees (NE Iberia). Quaternary 2019, 2, 32. https://doi.org/10.3390/quat2030032
AMA Style
Catalán A, Antúnez M, Poch RM. Acidification Assessment after Peat Bog Drainage in the Catalan Pyrenees (NE Iberia). Quaternary. 2019; 2(3):32. https://doi.org/10.3390/quat2030032
Chicago/Turabian StyleCatalán, Alba, Montserrat Antúnez, and Rosa M. Poch. 2019. "Acidification Assessment after Peat Bog Drainage in the Catalan Pyrenees (NE Iberia)" Quaternary 2, no. 3: 32. https://doi.org/10.3390/quat2030032
APA StyleCatalán, A., Antúnez, M., & Poch, R. M. (2019). Acidification Assessment after Peat Bog Drainage in the Catalan Pyrenees (NE Iberia). Quaternary, 2(3), 32. https://doi.org/10.3390/quat2030032
