Isolation of phyllosilicate–iron redox cycling microorganisms from an illite–smectite rich hydromorphic soil

The biogeochemistry of phyllosilicate–Fe redox cycling was studied in a Phalaris arundinacea (reed canary grass) dominated redoximorphic soil from Shovelers Sink, a small glacial depression near Madison, WI. The clay size fraction of Shovelers Sink soil accounts for 16% of the dry weight of the soil, yet contributes 74% of total Fe. The dominant mineral in the clay size fraction is mixed layer illite–smectite, and in contrast to many other soils and sediments, Fe(III) oxides are present in low abundance. We examined the Fe biogeochemistry of Shovelers Sink soils, estimated the abundance of Fe redox cycling microorganisms, and isolated in pure culture representative phyllosilicate–Fe oxidizing and reducing organisms. The abundance of phyllosilicate–Fe reducing and oxidizing organisms was low compared to culturable aerobic heterotrophs. Both direct isolation and dilution-to-extinction approaches using structural Fe(II) in Bancroft biotite as a Fe(II) source, and O₂ as the electron acceptor, resulted in recovery of common rhizosphere organisms including Bradyrhizobium spp. and strains of Cupriavidus necator and Ralstonia solanacearum. In addition to oxidizing biotite and soluble Fe(II) with O₂, each of these isolates was able to oxidize Fe(II) in reduced NAu-2 smectite with as the electron acceptor. Oxidized NAu-2 smectite or amorphous Fe(III) oxide served as electron acceptors for enrichment and isolation of Fe(III)-reducing microorganisms, resulting in recovery of a strain related to Geobacter toluenoxydans. The ability of the recovered microorganisms to cycle phyllosilicate–Fe was verified in an experiment with native Shovelers Sink clay. This study confirms that Fe in the native Shovelers Sink clay is readily available for microbial redox transformation and can be cycled by the Fe(III)-reducing and Fe(II)-oxidizing microorganisms recovered from the soil.

Introduction

Clay size Fe-bearing phyllosilicate phases, along with Fe(III) hydroxides, play a central role in the Fe redox biogeochemistry in natural environments (Amonette, 2002). These two groups of Fe-bearing minerals have contrasting geochemical behavior. Reduction of Fe(III) hydroxides typically results in Fe(II) mobilization, with the potential for redistribution of Fe via diffusion/dispersion and pore fluid advection. In contrast, structural Fe in clay minerals can undergo multiple redox cycles without being mobilized, because Fe remains within the mineral structure and within the system (Dong et al., 2009; Stucki, 2011). Multiple Fe(III) hydroxide reducing and soluble Fe(II)-oxidizing organisms are available as model microbial agents (Lovley et al., 2004; Weber et al., 2006; Emerson et al., 2010; Schmidt et al., 2010; Konhauser et al., 2011). Much less is known about microorganisms involved in phyllosilicate–Fe redox cycling. When 10 Fe(III)-reducing organisms [enriched and isolated with Fe(III) hydroxide as the sole electron acceptor] were tested for growth on a model ferruginous smectite, only eight could reduce structural Fe(III) in the smectite (Kashefi et al., 2008). These findings suggest that phyllosilicate–Fe(III)-reducing and Fe(III) (hydr)oxide-reducing microbial populations may not always overlap. Even less is known about organisms capable of oxidizing structural Fe(II) in smectite. The only culture known to catalyze this reaction is a strain of Desulfitobacterium hafniense (formerly D. frappieri) isolated from a subsurface smectite bedding, which is capable of -dependent structural Fe(II) oxidation (Shelobolina et al., 2003).

The coexistence and aggregation of Fe-bearing phyllosilicates and Fe(III) hydroxides makes it challenging to study the redox cycling of phyllosilicate–Fe in many soils and sediments. Certain non-highly weathered soils, however, may be enriched in phyllosilicates relative to Fe and Al oxides (Brady and Weil, 2008). The loess-derived silty clay loam deposits at Shovelers Sink, near Madison, WI, USA (Clayton and Attig, 1997; Bradbury, 2001) provide an excellent example of this type of soil environment. Shovelers Sink is a small, permanent, remnant glacial depression which originated as a proglacial lake fed by water draining off ice when glaciers covered the Madison area about 15,000 years ago (Clayton and Attig, 1997; Bradbury, 2001). At present Shovelers Sink is a wetland managed as a wildlife conservancy area. The dominant plant species at Shovelers Sink is Phalaris arundinacea (reed canary grass, RCG), which forms a dense, up to 1 m deep root system that is tolerant to prolonged anoxia during times of soil saturation (Barclay and Crawford, 1983). The redoximorphic conditions and high abundance of Fe-bearing phyllosilicates relative to Fe(III) oxides makes Shovelers Sink an ideal setting to study the biogeochemistry of phyllosilicate–Fe redox cycling. The aim of this study was to characterize the biogeochemistry and mineralogy of Shovelers Sink soil, and to enumerate and isolate microorganisms capable of reducing or oxidizing phyllosilicate–Fe.

Materials and Methods

Study Site and Sample Collection

Soil and groundwater samples were collected from Shovelers Sink site located in the Cross Plains unit of the Ice Age National Scientific Reserve, c.a. 50 m from Mineral Point Road and 17 m from the pond. Soils were collected (January 2007, July 2007, June 2008, and September 2009) with a stainless steel coring device. Fluid from below the water table was collected in 50-ml plastic tubes. Core sections were placed in sterile sample collection plastic bags and immediately delivered to the laboratory. All core sections were placed into an anaerobic chamber filled with N₂:H₂ mix (95:5), homogenized, and dispensed into serum bottles or pressure tubes for immediate experimentation, or into large Pyrex bottles with thick rubber stoppers for storage and/or later use. After removal from the anaerobic chamber, all bottles were flushed with O₂-free N₂ (passed over reduced, hot copper filings) to remove H₂ from the headspace. Soil water was filtered through a 0.2-μm syringe filter and frozen prior to analysis by ion chromatography.

Separation and Analysis of Grain Size Fractions

Soils were size fractionated by wet-sieving and centrifugation (Jackson, 1969; Gee and Bauder, 1986). Wet-sieving was performed in the anaerobic chamber using water made anoxic by bubbling with N₂. 1000 ml Pyrex bottles containing 900 ml water each were bubbled for 2 h. No gravel size particles (>2 mm) were found in the materials. Sand (50 μm–2 mm) size materials were removed by sieving (USA Standard Testing Sieves, VWR Scientific). The remaining silt (2 μm–50 μm) and clay (<2 μm) grain size fractions were separated by centrifugation in sealed plastic bottles under N₂. The settling time for the clay size fraction was calculated for a particle density of 2.6 g/cm³ using Stokes’ Law. A small portion of each size fraction was used to determine the dry weight per unit volume of soil suspension. These subsamples were dried at 105°C and wet/dry sample weight factors were calculated from weight differences before and after drying.

Total Fe(II) and Fe(III) in the size fractions was determined by the hydrofluoric acid (HF) extraction followed by the 1,10-Phenanthroline assay as described by Stucki (1981) and modified by Komadel and Stucki (1988). Fe(III) oxyhydroxide contents were determined by citrate–bicarbonate–dithionite (CDB) extraction (Mehra and Jackson, 1980) and ferrozine analysis (Stookey, 1970). All Fe measurements were performed in triplicate. Organic carbon was measured with a Leco CHN analyzer at the UW–Madison Soil and Plant Analysis Laboratory.

Determination of Steady State H₂ Concentrations

To determine steady state dissolved H₂ concentration in the porewater within representative soil samples, c.a. 30 g of each sample were placed into 60 ml serum bottles under an N₂ atmosphere. H₂ concentration in the headspace was monitored over time with a reduction gas analyzer (ta3000 Gas Analyzer, Trace Analytical, Ametek) until stability was reached.

Transmission Electron Microscopy

Transition electron microscopy (TEM) analyses were carried out using a FEI Titan 80–200 aberration corrected scanning/transmission electron microscope associated with an EDAX AMETEK high resolution energy-dispersive X-ray spectroscopy (EDS) detector and Gatan image filtering system, and operated at 200 kV. The samples were mixed with distilled water and ultrasonicated for ∼3 min. A drop of the resulting suspension was placed on a lacey-carbon coated Cu grid and air-dried.

X-ray Diffraction

X-ray diffraction (XRD) analyses were done using a Scintag Pad V Diffractometer with CuKα radiation. The instrument used an accelerating voltage of 45 kV, a current of 40 mA, a 2-mm divergence slit, 4-mm incident scatter slit, 1-mm diffracted beam scatter slit, and 0.5-mm receiving slit. Scan parameters used were a step size of 0.02° and a dwelling time of 2 s. Oriented aggregate mounts were prepared by pasting clay-DI water suspension on glass slides and air drying. A drop of ethylene glycol was added directly to the surface of the oriented clay mount with a glass rod for ethylene glycol treatment. Oriented aggregate mounts were heated at 550°C for 3 h in the furnace for heat treatment.

Most Probable Number Analysis

Microorganisms were enumerated by the most probable number (MPN) method (Woomer, 1994). Strict anaerobic laboratory technique (Miller and Wolin, 1974) was used to quantify anaerobic Fe(III)-reducing bacteria. An anaerobic basal bicarbonate-buffered freshwater (FW) medium (Lovley and Phillips, 1988) was dispensed into 27 ml anaerobic pressure tubes (Bellco Glass, Inc.) under N₂/CO₂ (80:20%). The tubes were capped with butyl rubber stoppers and sterilized by autoclaving. The medium for Fe(III)-reducing bacteria contained either 100 mM hydrous ferric oxide (HFO) or 0.8 weight% of the Fe(III)-bearing smectite NAu-2 [) where M is the interlayer cation; Keeling et al., 2000] as a terminal electron acceptor, H₂ (3 ml filtered H₂ was added to the headspace) and acetate (10 mM) as the combined electron donor, and 1.3 mM FeCl₂ as a reducing agent. The medium for Fe(II)-oxidizing bacteria contained O₂ as the terminal electron acceptor (3 ml filtered air added to the headspace) and 1.1% Bancroft (Ward Scientific) biotite [(K_0.980, Na_0.025; Ti_0.117; Si_3.048, Al_0.812, Ti_0.140)O₁₀(OH_1.02, F_0.98)] as a source of structural Fe(II). Aerobic heterotrophic bacteria were enumerated in medium containing (gram per liter) PIPES (piperazine-N,N′-bis-2-ethanesulfonic acid) buffer (3.0), NH₄Cl (0.25), NaH₂PO₄·H₂O (0.06), KCl (0.1), yeast extract (0.5), and acetate (0.41).

Isolation of Fe(III)-Reducing Organisms

Smectite-containing MPN cultures were diluted in agarized medium containing 20 mM fumarate and 20 mM acetate with a roll-tube method (Hungate, 1968). An inoculum (1 ml) from the 10-fold serial dilutions of the enrichment culture in a liquid FW medium was added to 27 ml pressure tubes containing 7 ml melted medium. The contents were mixed gently and the pressure tubes were rolled with a tube spinner. The roll-tubes were incubated vertically at room temperature. Individual colonies were transferred to the pressure tubes with 2 ml liquid FW medium containing 0.8% NAu-2 smectite as the electron acceptor and 10 mM acetate as the electron donor.

Isolation of Fe(II)-Oxidizing Organisms

Freshly collected samples and highest positive MPN dilution cultures were serially diluted in biotite/O₂-containing roll-tubes. After orange and red colored individual colonies formed, they were transferred to the pressure tubes with 2 ml liquid FW medium containing 1.1% biotite and 3 ml filtered air. Biotite oxidizing cultures were serially diluted and plated on aerobic heterotrophic medium using 1.5% agar as the solidifying agent.

Biotite oxidizing cultures were tested for their ability to grow via microaerophilic FeCl₂ oxidation. The cultures were grown on a heterotrophic low-organic medium (0.01% yeast extract and 1 mM acetate, with 3 ml of filtered air in the headspace), and then transferred (5% vol/vol inoculum) to anoxic FW medium, to which 1.3 mM FeCl₂ and 1 ml filtered air were added via syringe and needle every other day. After 12 days of cultivation, cell numbers were determined. The aliquots of the culture were fixed with glutaraldehyde. The fixed culture was reacted with ammonium oxalate (28 g/l ammonium oxalate and 15 g/l oxalic acid) in the presence of ca. 1 mM FeCl₂ to dissolve Fe(III) hydroxides. Cells were counted by acridine orange staining and epifluorescence microscopy (Hobbie et al., 1977).

Molecular Biological Methods

The16S rRNA gene sequences of the isolates and enrichment cultures were obtained using standard methodologies as previously described (Shelobolina et al., 2007). 16S rRNA genes were amplified using GM3 and GM4 primer set (Muyzer et al., 1995). For enrichment cultures 16S rRNA genes were cloned using the pGEM-T vector (Promega). The 16S rRNA gene fragments were compared to the GenBank nucleotide database using BLASTN and BLASTX algorithms (Altschul et al., 1990).

Fe Cycling Experiment

An iron cycling experiment was performed in FW medium supplemented with natural Shovelers Sink clay. The clay suspension was bubbled with air for 1 day to oxidize structural Fe(II), after which the clay was dried and mixed with FW medium prior to bubbling with N₂:CO₂ mix and autoclaving. XRD analysis of the clay before and after autoclaving showed no difference suggesting no change in the mineralogy of the clay (data not shown). A small amount of acetate (0.25 mM) was provided as a limited source of electron donor. Eighteen culture tubes were inoculated with G. toluenoxidans strain sa2 isolated from Shovelers Sink soil, and three tubes served as abiotic controls. Fe(III) reduction was allowed to proceed for 10 days. Five millimolar was then added to 12 tubes, and of these tubes nine were inoculated with Fe(II)-oxidizing isolates with three uninoculated tubes serving as controls. No nitrate or Fe(II)-oxidizing culture were added to three tubes in which Fe(III) reduction was allowed to proceed for the rest of the experiment. To evaluate the reaction of structural Fe(II) oxidation with nitrite, three remaining tubes with reduced Shovelers Sink clay were reacted with ca 2.0 mM nitrite.

Concentrations of 0.5 N HCl-extractable Fe(II), and were monitored over time. One milliliter of the culture was centrifuged in the anaerobic chamber at 14 K rpm for 5 min. The supernatant was collected for and dissolved Fe analysis. Samples for Fe analysis were acidified with HCl. The remaining solids were mixed with 0.5 N HCl and extracted for 24 h. Fe(II) in the HCl extracts was quantified using the ferrozine assay as previously described (Lovley and Phillips, 1986). Preliminary studies demonstrated that a 24-h 0.5 N HCl extraction released the same amount of Fe(II) from Shovelers Sink clay as HF extraction (Stucki, 1981). Note that this equivalence applies only to Fe(II), as only a small portion of structural Fe(III) is extracted by 0.5 N HCl (Shelobolina et al., 2004). and concentrations were measured with a Dionex DX-100 ion chromatograph equipped with a AS4-SC IonPac column. Dissolved Fe concentrations were determined by inductively coupled plasma-optical emission spectroscopy (ICP-OES).

Results and Discussion

Biogeochemistry of Shovelers Sink Soil

The soil at Shovelers Sink represents a silt loam interspersed with RCG roots down to the depth of 105 cm (Figure 1). The depth of the water table ranged from 60 to 80 cm. Soils collected in July 2007 were characterized in detail, at which time the water table was located at c.a. 65 cm depth (Figure 2).

FIGURE 1

Figure 1. Photograph of Shovelers Sink soil collected in the vicinity of the water table in July 2007, revealing reduced (gray color), and oxidized (bright yellowish-brown colors) regions indicative of redoximorphic conditions. The bar is 1 cm.

FIGURE 2

Figure 2. Depth distribution of dissolved H₂ (A), Organic Carbon (B), and Fe phases, including citrate–bicarbonate–dithionite (CDB) extractable Fe (C), and hydrofluoric acid (HF) extractable Fe (D) and Fe(II)/Fe_total (E) in Shovelers Sink soil, July 2007. A cartoon on the left shows relative depth of root zone and terminal electron accepting processes (TEAPs): brown for mixed metabolism, green for Fe(III)-reducing zone, and blue for methanogenic zone.

Organic carbon concentrations were highest within the main root zone above 55 cm (1.7–2.5%), intermediate in the vicinity of the water table (1.0–1.2%), and lowest below 80 cm (0.32–0.41%) where few, if any, RCG roots were present (Figure 2B). Total HF-extractable iron (Figure 2C) concentrations ranged between 196 and 333 mmol/kg and showed a trend opposite of that for organic carbon, with Fe concentrations being lowest (166–190 mmol/kg) above a depth of 55 cm, intermediate from the water table down to 105 cm (230–249 mmol/kg), and highest below 105 cm (333–337 mmol/kg). The fraction of total Fe present as Fe(II) was highly variable above the water table (16–50%) and gradually decreased from 38 to 32% below the water table (Figure 2D).

The spatial segregation of terminal electron accepting processes in Shovelers Sink soil was assessed by measuring steady state concentration of dissolved H₂ in incubated soil samples from different depths, according to published criteria (Lovley and Goodwin, 1988; Lovley et al., 1994) and as described in a previous study of clay-rich subsurface sediments (Shelobolina et al., 2004; Figure 2A). Three TEAP zones could be distinguished: a mixed metabolism zone above the water table (0–65 cm depth) characterized by a range of H₂ concentrations from 1.6 to 10.2 nM; a dissimilatory Fe(III)-reducing zone between 65 and 115 cm characterized by H₂ concentrations of 0.4–0.7 nM; and a methanogenic zone below 115 cm with steady state H₂ concentration of 8.1 ± 0.9 nM.

Shovelers Sink is a depression in which water balance is maintained through direct precipitation and runoff from the surrounding landscape. Runoff from nearby farms and households could serve as an additional source of both organic carbon and electron acceptors, e.g., to the system. However, no was detected in fluid from below the water table on any of the sampling events. These results suggest that the localized zones of oxidation observed in the soil (see Figure 1) are driven by release of O₂ from RGC roots, as is well-known for a variety of plants that proliferate in water-logged soils (Armstrong, 1978). The observed redoximorphic features (Figure 1) and porewater steady state H₂ concentrations (Figure 2A) suggest ongoing Fe redox cycling at two scales: (1) at the centimeter-to-decimeter scale within the transition from saturated/anoxic to unsaturated/partially oxic conditions in the vicinity of the water table; and (2) at the microscale around RCG roots both above and below the water table. Soil from the vicinity of the water table (c.a. 65 depth depth in July 2007) was chosen to study microbial Fe redox cycling as it likely contained both Fe(III)-reducing and Fe(II)-oxidizing microorganisms.

Soil Mineralogy

Soil collected from the vicinity of the water table in July 2007 was used to study the abundance and mineralogy of Fe in different grain size fractions. The contribution of silt and clay size materials to total dry weight differed dramatically from their contributions to total HF-extractable iron [Fe(II) + Fe(III)] content (Table 1). Although the silt size fraction dominated Shovelers Sink soil by weight (83% of total dry weight), it contributed only 26% total HF-extractable iron. In contrast, the clay size fraction, which accounted only for 16% of the dry weight of soil, contributed 74% of the total HF-extractable iron. These results demonstrate that the majority of the Fe content of Shovelers Sink soil is contained within the clay size fraction.

TABLE 1

Table 1. Characterization of silt and clay size fractions of Shovelers Sink soil.

The mineralogy of silt and clay size fractions was characterized by conventional TEM, high resolution TEM (HRTEM), and XRD (Figures 3–5). The following mineral phases were identified (by TEM) in the silt size fraction: potassium feldspar, plagioclase, quartz, and mixed layered illite–smectite aggregates (Figure 3). Based on TEM and XRD analyses, the dominant mineral in the clay size fraction was illite–smectite mixed layers (Figures 4 and 5). Clay size materials also contained kaolinite and illite as minor components. No Fe(III) hydroxides were detected in either the silt or clay size fractions during TEM observations. These results are consistent with CDB extractions, which showed that the abundance of Fe(III) oxides was ca. less than 5% of total HF-extractable Fe in the bulk soil (Figure 2) and less than 2.5% in the clay size fraction (Table 1). In summary, gravimetric, chemical, and mineralogical analyses collectively suggest that mixed layer illite–smectite is the geochemically dominant Fe-containing phase in Shovelers Sink soil.

FIGURE 3

Figure 3. TEM image of Shovelers Sink silt size fraction showing flakes of illite–smectite (I/S), quartz (Qz), and potassium feldspar (KF) grains.

FIGURE 4

Figure 4. Mineralogy of Shovelers Sink clay size fraction. (A) TEM image showing flakes of smectite-dominated clay minerals (I/S), quartz (Qz), potassium feldspar (KF), plagioclase, and titania (TiO₂) grains. (B,C) HRTEM image and selected area diffraction pattern taken from the area indicated by the large arrow in (A), showing the curled edge of a clay aggregate with lattice fringes corresponding to (001) smectite with ca. 10-Å layer spacing; the size of this spacing was likely reduced in the vacuum of the TEM. (D) EDAX results for an I/S aggregate. A small amount of potassium is detected, indicating that the smectite contains an illite component.

FIGURE 5

Figure 5. X-ray diffraction analyses of clay size fraction from Shovelers Sink soil showing illite–smectite (I/S) as dominant mineral. Small amounts of illite (I), kaolinite (Ka), and quartz (Qz) also exist. The 13.6-Å [I/S (001)] peak in the untreated sample expanded to 15.2 Å by ethylene glycol treatment, and collapsed to 9.9 Å by heat treatment. The 7.2-Å [kaolinite (001)] and 3.6-A [kaolinite (002)] peaks in the untreated sample disappeared by heating at 550°C.

MPN Enumerations

Both Fe(III)-reducing and Fe(II)-oxidizing microorganisms were detected in MPN enumerations conducted with soil samples from near the water table in July 2007 and in September 2009. The abundance of Fe(III)-reducing organisms (2.4 × 10¹ cells/g wet soil in 2007 and 2.3 × 10⁰ cells/g wet soil in 2009) and Fe(II)-oxidizing organisms (2.9 × 10² cells/g wet soil in 2007 and 2.4 × 10³ cells/g wet soil in 2009) was modest compared to the abundance of total culturable aerobic heterotrophs (1.1 × 10⁶ cells/g wet soil in 2007 and 4.2 × 10⁵ cells/g wet soil in 2009). Analogous results have been reported for groundwater seep environments supporting active Fe redox cycling (Blöthe and Roden, 2009; Roden et al., submitted). Although the much larger densities of culturable aerobic heterotrophs compared to Fe(III)-reducers in these environments could suggest intense competition between the two physiological groups (e.g., for utilization of plant-derived organic materials), it is important to note that previous studies have shown the persistence of large numbers of aerobic bacteria in permanently anoxic environments (Jorgensen and Tiedje, 1993). Thus, the presence of high densities of culturable aerobes in the Shoveler’s sink soil does not necessarily mean that they contribute extensively to in situ carbon metabolism.

Fe(II)-Oxidizing Isolates

Fe(II)-oxidizing organisms were isolated from (1) soil samples collected in July 2007, June 2008, and September 2009, and (2) the highest positive dilutions from MPN studies set up in 2007 and 2009. Biotite was utilized as a solid phase form of Fe(II) for these studies. Unlike reduced smectite, structural Fe(II) in biotite is not subject to spontaneous reaction with O₂, thus permitting the use of O₂ as the electron acceptor for lithotrophic Fe(II) oxidation. Recent studies have demonstrated that the Fe(II)-oxidizing, reducing culture described by Straub et al. (1996) can utilize Fe(II) in biotite as a sole electron donor for chemolithotrophic growth (Shelobolina et al., submitted). Samples and last positive MPN dilution cultures were serially diluted in biotite-containing roll-tubes. After solidification 3 ml of filter sterilized air were added to the headspace. Roll-tubes were incubated vertically at 20–22°C (room temperature). Over a period of 4–8 months, small (0.2–0.5 mm) orange, or in some cases red, colonies formed between the layer of biotite and the layer of agarized medium in a roll-tube. Each colony was transferred to 2 ml liquid medium with biotite provided as the electron donor and O₂ as the electron acceptor. A protracted (4 years) isolation effort (2007–2010) resulted in recovery of 73 biotite oxidizing cultures, which were maintained on liquid medium with biotite and O₂. Eleven cultures capable of oxidizing at least 5% of the structural Fe(II) content in biotite were selected for further study. Culture subsamples were streaked onto aerobic, low carbon medium culture plates. The resulting isolated colonies could be either mixotrophic Fe(II)-oxidizing microorganisms or heterotrophic contaminants. The numerically dominant colony types were tested for microaerophilic growth with FeCl₂ as a soluble Fe(II) sources. Cultures capable of growing to a density of at least 10⁸ cells/ml with a total of c.a. 8 mM FeCl₂ added over time (see Materials and Methods) were identified by 16S rRNA gene sequencing and selected for further study. The isolates so obtained included Bradyrhizobium spp., and strains of Ralstonia solanacearum, and Cupriavidus necator. One strain each was chosen for further study (Table 2). Each of the cultures oxidized 3–4% of structural Fe(II) in biotite with O₂ as the electron acceptor, and each was found to be capable of oxidizing chemically reduced smectite with as the electron acceptor (data not shown).

TABLE 2

Table 2. Fe redox cycling microorganisms isolated from Shovelers Sink soil.

Fe(III)-Reducing Isolate

Ferruginous NAu-2 smectite and hydrous ferric oxide (HFO) were used to enrich Fe(III)-reducing microorganisms from Shovelers Sink soil collected in July 2007 with acetate and H₂ as combined electron donors. Acetate and H₂ were used as these represent the two major sources of electron donor for microbial Fe(III) reduction in anoxic soils and sediments (Lovley et al., 2004). After ca. 2 months of room temperature incubation, small (25 clones each) 16S rRNA gene clone libraries were constructed from 1% enrichment cultures. Both enrichment cultures were dominated by an operational taxonomic unit (OTU) 99% similar to Geobacter toluenoxydans (Kunapuli et al., 2010). G. toluenoxydans strain sa2 was recovered using the roll-tube method with acetate as the electron donor and fumarate as the electron acceptor. Strain sa2 can conserve energy from dissimilatory Fe(III) reduction concomitant with acetate oxidation using a variety of solid phase Fe(III) sources, including Fe(III) hydroxide and ferruginous smectite, but does not utilize nitrate as the electron acceptor.

Microbial Redox Cycling of Fe in Shovelers Sink Clay

A Fe redox cycling experiment was conducted with clay size materials isolated from Shovelers Sink soil collected from ca. 65 cm depth in July 2007 (see Table 1). Although O₂ is a likely electron acceptor for microbial Fe(II) oxidation at Shovelers Sink (see above), was utilized in this model experiment since it does not react spontaneously with phyllosilicate-associated Fe(II). G. toluenoxidans strain sa2 (5% vol/vol inoculum from a culture grown previously for three transfers on limiting acetate/Shovelers Sink clay medium, providing c.a. 10⁶ cells/ml) reduced 2.1 mmol/l Fe(II) over 7 days (Figure 6A). A small increase in aqueous Fe concentration was detected in both abiotic control and the Fe(III)-reducing cultures (35.4 and 50.6 μM, respectively). The source of dissolved Fe cannot be determined with available data. Shovelers Sink clay is a mix of minerals. And although illite–smectite is the main Fe-bearing mineral controlling Fe biogeochemistry in Shovelers Sink soil, the clay size fraction could contain organics-bound or sorbed Fe, as well as small amounts of Fe(III) hydroxide coatings. All of these Fe forms could contribute to aqueous Fe.

FIGURE 6

Figure 6. Reduction of native Fe(III) phyllosilicate in Shovelers Sink soil (clay size fraction) by G. toluenoxidans strain sa2, followed by oxidation of reduced phyllosilicate by the three Fe(II)-oxidizing isolates with as the electron acceptor. (A) 0.5 N HCl-extractable Fe(II); (B) nitrate; (C) nitrite.

After 10 days, an inoculum of each of the three Fe(II)-oxidizing isolates (Table 2) were added to replicate microbially reduced clay suspensions. The Fe(II)-oxidizing inocula (1–5% vol/vol) were grown heterotrophically on organics limited reducing medium until the optical density of the culture at 600 nm stabilized, at which point all organic carbon had presumably been utilized. The inoculum volume was adjusted to provide ca 10⁶ cells/ml. The cultures reoxidized 60–65% (c.a. 1.2 mmol/l) of the Fe(II) generated by G. toluenoxidans strain sa2 (Figure 6A) while consuming 0.82–1.15 mM (Figure 6B). The incomplete reversibility of structural Fe redox cycle has been observed before (Shen and Stucki, 1994) and a possible explanation for this phenomenon is that the collapsing of smectite layers as the result of Fe(III) reduction makes a portion of structural Fe(II) inaccessible (Stucki, 2011).

No Fe(II) oxidation or consumption took place in absence of Fe(II)-oxidizing organisms. Although all of the Fe(II)-oxidizing isolates are denitrifying bacteria, substantial amounts of (0.35–0.67 mM) were produced during Fe(II) oxidation (Figure 6C). The Shovelers Sink soil used in the Fe cycling experiment contained 1–2% associated organic carbon (see Figure 2). The possibility therefore existed that produced during organotrophic oxidation of associated organic carbon could have reacted chemically (abiotically) with Fe(II) in the reduced clay, thereby contributing to the Fe(II) oxidation activity shown in Figure 6A. We deemed this pathway unlikely given that each of the isolated strains reduced nitrate directly to N₂ with no significant accumulation in organotrophic medium (data not shown). Nevertheless, a separate experiment was conducted to evaluate the extent to which reaction of Fe(II) with may have been responsible for the observed Fe(II) oxidation. Nitrite (2 mM) was added to a suspension of microbially reduced Shovelers Sink clay, and the concentrations of Fe(II) and were followed over time (Figure 7). The rate of chemical Fe(II) oxidation by nitrite (c.a. 0.018 mmol/l/day; Figure 7) was three to six times less than the rate of oxidation in the microbial Fe cycling experiment (0.058–0.118 mmol/l/day; Figure 6A). This result indicates that enzymatic activity was primarily responsible for nitrate-dependent oxidation of reduced Shovelers Sink clay. Similar conclusions were reached in a prior study of microbial nitrate-dependent oxidation of other types of solid phase Fe(II) compounds in which significant accumulation of took place (Weber et al., 2001). Thus, although the organic matter associated with Shovelers Sink clay brings uncertainty into the exact stoichiometry of Fe/N interactions, the results of this experiment clearly confirm that Fe in the native Shovelers Sink clay is readily available for microbial redox transformation and can be cycled by the Fe(III)-reducing and Fe(II)-oxidizing microorganisms recovered from the soil.

FIGURE 7

Figure 7. Chemical oxidation of microbially reduced Shovelers Sink soil (clay size fraction) by nitrite.

Implications for Phyllosilicate–Fe Biogeochemistry

Our studies confirm the presence of both phyllosilicate–Fe(III)-reducing and phyllosilicate–Fe(II)-oxidizing organisms in a redoximorphic soil, the biogeochemical conditions of which are consistent with ongoing phyllosilicate–Fe redox cycling in the vicinity of the water table and O₂-releasing plant roots. Several solid phase Fe redox cycling isolates were recovered from this soil using model Fe(II) and Fe(III) containing phyllosilicates as the electron donor or acceptor, including the Alphaproteobacterium Bradyrhizobium sp, Betaproteobacteria C. necator and R. solanacearum, and Deltaproteobacterium G. toluenoxydans. The recovery of a Geobacter species as an agent of Fe(III) reduction at Shovelers Sink is not surprising, as members of the Geobacteraceae often dominate soil and sediment Fe(III)-reducing microbial populations (Lovley et al., 2004), and multiple species in this family are known to reduce structural Fe(III) in phyllosilicates (Lovley et al., 1998; Kostka et al., 1999; Kashefi et al., 2008; Shelobolina et al., 2008). Geobacter sp. dominated both, smectite and HFO containing enrichment cultures and therefore was well adjusted to using both Fe(III)-bearing phases as the electron acceptor. Although a previous study (Kashefi et al., 2008) suggested that phyllosilicate–Fe(III)-reducing and Fe(III) (hydr)oxide-reducing microbial populations may not always overlap, no specific agents adjusted to using one or another solid phase Fe(III) were recovered at Shovelers Sink.

The microorganisms recovered as potential agents of phyllosilicate–Fe(II) oxidation are all common rhizosphere bacteria. Bradyrhizobium spp. are well-known as N₂ fixing bacteria that form a symbiotic relationship with plants, especially soybeans, and are widely utilized in agriculture (Hume and Blair, 1992). In contrast, R. solanacearum is a soil-born plant pathogen causing leaf wilting in tomato, pepper, and potato plants as well as many other plant species (Denny, 2005). C. necator (including former Ralstonia eutropha strains) is a versatile soil bacterium known as an aromatic and chloroaromatic compounds degrader and a non-obligate bacterial predator of the bacteria and fungi (Makkar and Casida, 1987; Lykidis et al., 2010).

Various strains of Bradyrhizobium spp. and C. necator (R. eutropha) can grow autotrophically with H₂ as the electron donor (Bowien and Kusian, 2002; Schwartz et al., 2003; Franck et al., 2008). In addition, a B. japonicum strain USDA110 is capable of thiosulfate-based chemolithotrophy (Masuda et al., 2010). None of phytopathogenic R. solanacearum strains were reported to grow autotrophically (Palleroni and Doudoroff, 1971). However, a recently recovered Ralstonia sp. strain HM08-01, 98% similar to R. solanacearum, can oxidize soluble Fe(II) under microaerophilic conditions (Swanner et al., 2011). Our studies suggest a new role for these common rhizosphere bacteria, i.e., oxidation of structural Fe(II) in phyllosilicates. Further research with chemically defined substrates, such as FeCl₂ and Fe(II)-NTA, is required to determine exact stoichiometry of Fe(II) oxidation by Shovelers Sink isolates.

The importance of native Fe(III) phyllosilicates as an electron acceptor for organic matter oxidation coupled to dissimilatory Fe(III) reduction in soils and sediments has been increasingly recognized (Kukkadapu et al., 2006; Stucki and Kostka, 2006; Komlos et al., 2008; Dong et al., 2009). In contrast, the role of microbial catalysis in phyllosilicate–Fe(II) oxidation has not received much attention, and to date only one organism is known to carry-out this reaction (Shelobolina et al., 2003). Our work thus significantly expands the range of organisms known to participate in phyllosilicate–Fe(II) oxidation. The ability of common rhizosphere bacteria to carry-out this process has significant implications not only for phyllosilicate–Fe redox geochemistry, but also for phyllosilicates diagenesis, e.g., low-temperature microbially driven smectite-to-illite transition, that may accompany Fe cycling in smectite and affect plant nutrition (Shen and Stucki, 1994; Stucki, 2011).

Conflict of Interest Statement

The authors declare that the research was conducted in the absence of any commercial or financial relationships that could be construed as a potential conflict of interest.

Acknowledgments

With thank Cynthia A. Stiles and Matilde M. Urrutia from UW–Madison Soil Science Department for introducing us to the Shovelers Sink site. This research was supported by the U.S. Department of Energy (DOE), Office of Biological and Environmental Research (BER) Subsurface Biogeochemical Research (SBR) Program through grant ER64172-1027487-001191; and the SBR Scientific Focus Area (SFA) at the Pacific Northwest National Laboratory (PNNL).

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