Gut-Associated Denitrification and In Vivo Emission of Nitrous Oxide by the Earthworm Families Megascolecidae and Lumbricidae in New Zealand

Previous studies have documented the capacity of European earthworms belonging to the family Lumbricidae to emit the greenhouse gas nitrous oxide (N₂O), an activity attributed primarily to the activation of ingested soil denitrifiers. To extend the information base to earthworms in the Southern Hemisphere, four species of earthworms in New Zealand were examined for gut-associated denitrification. Lumbricus rubellus and Aporrectodea rosea (introduced species of Lumbricidae) emitted N₂O, whereas emission of N₂O by Octolasion cyaneum (an introduced species of Lumbricidae) and emission of N₂O by Octochaetus multiporus (a native species of Megascolecidae) were variable and negligible, respectively. Exposing earthworms to nitrite or nitrate and acetylene significantly increased the amount of N₂O emitted, implicating denitrification as the primary source of N₂O and indicating that earthworms emitted dinitrogen (N₂) in addition to N₂O. The alimentary canal displayed a high capacity to produce N₂O when it was supplemented with nitrite, and alimentary canal contents contained large amounts of carbohydrates and organic acids indicative of fermentation (e.g., succinate, acetate, and formate) that could serve as sources of reductant for denitrification. nosZ encodes a portion of the terminal oxidoreductase used in denitrification. The nosZ sequences detected in the alimentary canals of L. rubellus and O. multiporus were similar to those retrieved from soil and were distantly related to sequences of uncultured soil bacteria and genera common in soils (i.e., Bradyrhizobium, Azospirillum, Rhodopseudomonas, Rhodospirillum, Pseudomonas, Oligotropha, and Sinorhizobium). These findings (i) suggest that the capacity to emit N₂O and N₂ is a general trait of earthworms and not geographically restricted, (ii) indicate that species belonging to different earthworm families (i.e., Megascolecidae and Lumbricidae) may not have equal capacities to emit N₂O, and (iii) also corroborate previous findings that link this capacity to denitrification in the alimentary canal.Earthworms are dominant members of the soil fauna and affect the structure and fertility of soils (5, 20, 22, 23). Various species of European earthworms belonging to the family Lumbricidae (e.g., Aporrectodea caliginosa, Lumbricus rubellus, and Octolasion lacteum) emit dinitrogen (N₂) and the greenhouse gas nitrous oxide (N₂O), and their burrowing activities and feeding habits in combination with in situ conditions can influence the emission of nitrogenous gases from soils that they inhabit (1, 2, 13, 17, 25, 27, 39).The microbiology of the earthworm alimentary canal has been addressed in numerous studies (3, 4, 6, 9, 14, 16, 32). The alimentary canal of the earthworm is anoxic, in marked contrast to the aerated material that earthworms ingest (14, 39). Anoxia and other in situ conditions of the alimentary canal appear to stimulate soil microbes capable of surviving under anaerobic conditions during passage through the gut (3, 4). Soils are rich in denitrifying bacteria (37), and the capacity of European earthworms to emit nitrogenous gases has been attributed primarily to the in situ activity of ingested denitrifying bacteria that appear to be highly active under the anoxic conditions of the earthworm alimentary canal (12, 15, 17, 25, 39). However, it is not known if the capacity to emit nitrogenous gases is a general trait of earthworms independent of their taxonomic family or geographic location. The main objectives of this study were to examine the capacity of Southern Hemisphere earthworms in New Zealand to emit N₂O and to determine if this capacity was linked to denitrifying bacteria in the alimentary canal.     

Association of Novel and Highly Diverse Acid-Tolerant Denitrifiers with N2O Fluxes of an Acidic Fen

Wetlands are sources of denitrification-derived nitrous oxide (N₂O). Thus, the denitrifier community of an N₂O-emitting fen (pH 4.7 to 5.2) was investigated. N₂O was produced and consumed to subatmospheric concentrations in unsupplemented anoxic soil microcosms. Total cell counts and most probable numbers of denitrifiers approximated 10¹¹ cells·g_DW⁻¹ (where DW is dry weight) and 10⁸ cells·g_DW⁻¹, respectively, in both 0- to 10-cm and 30- to 40-cm depths. Despite this uniformity, depth-related maximum reaction rate (v_max) values for denitrification in anoxic microcosms ranged from 1 to 24 and −19 to −105 nmol N₂O h⁻¹· g_DW⁻¹, with maximal values occurring in the upper soil layers. Denitrification was enhanced by substrates that might be formed via fermentation in anoxic microzones of soil. N₂O approximated 40% of total nitrogenous gases produced at in situ pH, which was likewise the optimal pH for denitrification. Gene libraries of narG and nosZ (encoding nitrate reductase and nitrous oxide reductase, respectively) from fen soil DNA yielded 15 and 18 species-level operational taxonomic units, respectively, many of which displayed phylogenetic novelty and were not closely related to cultured organisms. Although statistical analyses of narG and nosZ sequences indicated that the upper 20 cm of soil contained the highest denitrifier diversity and species richness, terminal restriction fragment length polymorphism analyses of narG and nosZ revealed only minor differences in denitrifier community composition from a soil depth of 0 to 40 cm. The collective data indicate that the regional fen harbors novel, highly diverse, acid-tolerant denitrifier communities capable of complete denitrification and consumption of atmospheric N₂O at in situ pH.Nitrous oxide (N₂O) is a potent greenhouse gas with a global warming potential that is 300-fold higher than that of CO₂, and its concentration increased from 270 ppb in 1750 to 319 ppb in 2005 (17). N₂O can be produced in soils during denitrification, nitrification, the dissimilatory reduction of nitrate to nitrite and/or ammonium (hereafter referred to as dissimilatory nitrate reduction), or the chemical transformation of nitrite or hydroxylamine (5, 7, 49). The percentage of N₂O produced in any of these processes is variable, depending mainly on the redox potential, pH, and C/N ratio (49). In anoxic ecosystems such as waterlogged soils, most of the N₂O is considered to be denitrification derived (7, 9). Complete denitrification is the sequential reduction of nitrate to dinitrogen (N₂) via nitrite, nitric oxide (NO), and N₂O (75). The main product of denitrification varies with the organism and in situ conditions and is usually either N₂O or N₂ (68). N₂O can occur as a by-product during dissimilatory nitrate reduction when accumulated nitrite interacts with nitrate reductase to form N₂O (59). The production of N₂O by dissimilatory nitrate reducers is favored in environments with large amounts of readily available organic carbon (65). Thus, their contribution to nitrate-dependent production of N₂O in soils is likely insignificant compared to that of denitrifiers.The oxidoreductases involved in denitrification are termed dissimilatory nitrate reductase (Nar, encoded by narGHJI, or Nap, encoded by napEDABC), nitrite reductase (Nir, encoded by nirK and nirS), NO reductase (cNor and qNor, encoded by norBC and norB, respectively), and N₂O reductase (Nos, encoded by nosZ) (75). Nitrate reductase is also found in dissimilatory nitrate reducers (60). narG can therefore be used as a molecular marker to assess both denitrifiers and dissimilatory nitrate reducers, whereas nosZ is specific for the assessment of denitrifiers (25, 43, 48).Denitrification in soils is regulated by temperature, pH, substrate (i.e., carbon) availability, and water content (10, 24, 66). Although denitrification increases with increasing temperature, it can still occur at temperatures below 0°C (10, 24). Low temperatures appear to limit the activity of N₂O reductase more severely than other enzymes involved in denitrification and thus yield higher relative amounts of denitrification-derived N₂O (24). Although denitrification activity usually decreases under acidic conditions, the relative percentage of N₂O to total denitrification-derived nitrogenous gases increases with increasing acidity, a result attributed to the sensitivity of N₂O reductase to low pH (27, 70). However, denitrifier communities can be adapted to the in situ pH of the system (40, 58, 73).Wetlands are ecosystems in which denitrification is likely a dominant source of emitted N₂O (7, 44, 45). The identification and analysis of main drivers for N₂O production (i.e., the microbiota catalyzing N₂O production and consumption) is thus of major concern in such environments. Fens are specialized wetlands characterized by soil acidity (67). However, information on acid-tolerant denitrifier communities of such wetlands is scarce. It is hypothesized that fens harbor a diverse, hitherto unknown, denitrifier community that is adapted to in situ conditions and associated with N₂O fluxes (i.e., fen denitrifiers are acid tolerant and have a high affinity for nitrate and N₂O). Thus, the main objectives of the present study were to evaluate the capacities of denitrifier communities of an N₂O-emitting fen (20) to produce or consume N₂O and to determine if a novel and diverse denitrifier community was associated with these capacities.     

Insights into the Effect of Soil pH on N2O and N2 Emissions and Denitrifier Community Size and Activity

The objective of this study was to investigate how changes in soil pH affect the N₂O and N₂ emissions, denitrification activity, and size of a denitrifier community. We established a field experiment, situated in a grassland area, which consisted of three treatments which were repeatedly amended with a KOH solution (alkaline soil), an H₂SO₄ solution (acidic soil), or water (natural pH soil) over 10 months. At the site, we determined field N₂O and N₂ emissions using the ¹⁵N gas flux method and collected soil samples for the measurement of potential denitrification activity and quantification of the size of the denitrifying community by quantitative PCR of the narG, napA, nirS, nirK, and nosZ denitrification genes. Overall, our results indicate that soil pH is of importance in determining the nature of denitrification end products. Thus, we found that the N₂O/(N₂O + N₂) ratio increased with decreasing pH due to changes in the total denitrification activity, while no changes in N₂O production were observed. Denitrification activity and N₂O emissions measured under laboratory conditions were correlated with N fluxes in situ and therefore reflected treatment differences in the field. The size of the denitrifying community was uncoupled from in situ N fluxes, but potential denitrification was correlated with the count of NirS denitrifiers. Significant relationships were observed between nirS, napA, and narG gene copy numbers and the N₂O/(N₂O + N₂) ratio, which are difficult to explain. However, this highlights the need for further studies combining analysis of denitrifier ecology and quantification of denitrification end products for a comprehensive understanding of the regulation of N fluxes by denitrification.Denitrification is the microbial reduction of NO₃⁻ via NO₂⁻ to gaseous NO, N₂O, and N₂, which are then lost into the atmosphere (36). It therefore results in considerable loss of nitrogen, one of the most limiting nutrients for crop production in agriculture (20). Denitrification is also of environmental concern since, together with nitrification, it is the main biological process responsible for N₂O emissions (7). N₂O is a potent greenhouse gas which has a global warming potential about 320 times greater than that of CO₂ and has a lifetime of approximately 120 years (32). In the stratosphere, N₂O can also react with O₂ to produce NO, which induces the destruction of stratospheric ozone (8). N₂O can be released into the atmosphere by incomplete denitrification due to the effect of environmental conditions on the regulation of the different denitrification reductases (14, 41, 51), but it has recently been suggested that it could also be due to lack of nitrous oxide reductase in some denitrifiers (19, 41). Since N₂O is an intermediate in the denitrification pathway, both the amount of N₂O produced and the N₂O/(N₂O + N₂) ratio are important in understanding and predicting N₂O fluxes from soils.The main environmental factors known to influence the N₂O/(N₂O + N₂) ratio are pH, organic carbon and NO₃⁻ availability, water content, and O₂ partial pressure (50). Soil pH is one of the most important factors influencing both denitrification and N₂O production (43). In general, the denitrification rate increases with increasing pH values (up to the optimum pH) while, in contrast, the N₂O/(N₂O + N₂) ratio decreases (50). This relationship has been characterized in laboratory experiments (9, 45), but it is not clear whether the same relationships exist in the field because of methodological limitations of in situ measurement of N₂ emissions (16). Nevertheless, ¹⁵N tracing experiments based on the addition of a labeled denitrification substrate to soil offer a useful tool to quantify emissions of both N₂O and N₂ in situ (47, 49). Soil pH is also an important factor influencing denitrifier community composition (35, 39), which can be an important driver of denitrification activity and N₂O emissions (5, 21). A recent study reported a negative relationship between the proportion of bacteria genetically capable of reducing N₂O within the total bacterial community and the N₂O/(N₂O + N₂) ratio, with both being strongly correlated with soil pH (38).The objective of the present study was to explore the effect of changes in soil pH on in situ N₂O and N₂ emissions, denitrifying enzyme activity (DEA), and potential N₂O production. In addition, we also investigated whether differences in N fluxes could be related to changes in the size of the microbial community possessing the different denitrification genes. A field experiment was conducted using replicated grassland plots in which the soil pH was modified by addition of either acid or hydroxide to the soil. A ¹⁵N tracer method was used to provide information on N emissions. In addition to measuring potential denitrification activity, the size of the denitrifier community was determined by real-time PCR quantification of the denitrification genes.     

Potential of Aerobic Denitrification by Pseudomonas stutzeri TR2 To Reduce Nitrous Oxide Emissions from Wastewater Treatment Plants

In contrast to most denitrifiers studied so far, Pseudomonas stutzeri TR2 produces low levels of nitrous oxide (N₂O) even under aerobic conditions. We compared the denitrification activity of strain TR2 with those of various denitrifiers in an artificial medium that was derived from piggery wastewater. Strain TR2 exhibited strong denitrification activity and produced little N₂O under all conditions tested. Its growth rate under denitrifying conditions was near comparable to that under aerobic conditions, showing a sharp contrast to the lower growth rates of other denitrifiers under denitrifying conditions. Strain TR2 was tolerant to toxic nitrite, even utilizing it as a good denitrification substrate. When both nitrite and N₂O were present, strain TR2 reduced N₂O in preference to nitrite as the denitrification substrate. This bacterial strain was readily able to adapt to denitrifying conditions by expressing the denitrification genes for cytochrome cd₁ nitrite reductase (NiR) (nirS) and nitrous oxide reductase (NoS) (nosZ). Interestingly, nosZ was constitutively expressed even under nondenitrifying, aerobic conditions, consistent with our finding that strain TR2 preferred N₂O to nitrite. These properties of strain TR2 concerning denitrification are in sharp contrast to those of well-characterized denitrifiers. These results demonstrate that some bacterial species, such as strain TR2, have adopted a strategy for survival by preferring denitrification to oxygen respiration. The bacterium was also shown to contain the potential to reduce N₂O emissions when applied to sewage disposal fields.Wastewater treatment processes produce one of the major greenhouse effect gases, nitrous oxide (N₂O) (7, 25, 30). The global warming potential of N₂O relative to that of carbon dioxide (CO₂) is 298 for a 100-year time horizon, and its concentration in the atmosphere continues to increase by about 0.26% per year (9). Nitrogen removal in wastewater treatment plants is essentially based on the activities of nitrifying and denitrifying microorganisms, both of which are inhabitants of activated sludge. Nitrifying bacteria aerobically oxidize ammonium to nitrite (NO₂⁻) and nitrate (NO₃⁻), which are then reduced anaerobically by denitrifying bacteria to gaseous nitrogen forms, such as N₂O and dinitrogen (N₂). It has long been known that N₂O can be produced during both nitrification and denitrification processes of wastewater treatment (3, 19, 23), but the cause of N₂O emission during the nitrification process was not clear. We recently showed, however, using activated sludge grown under conditions that mimicked a piggery wastewater disposal, that N₂O emission during the nitrification process depends on denitrification by ammonia-oxidizing bacteria (Nitrosomonas) (18). On the other hand, it is believed that denitrifying bacteria produce N₂O as a by-product when anaerobiosis is insufficient during the denitrification process, because N₂O reductase is the enzyme that is most sensitive to oxygen (6). Piggery wastewater, in particular, contains a high concentration of ammonia, and N₂O emission tends to take place during the nitrogen removal process (5, 10). Experiments on the removal of ammonia and organic carbon by the aerobic denitrifier Pseudomonas stutzeri SU2 (24) and the heterotrophic nitrifier-aerobic denitrifier Alcaligenes faecalis no. 4 (16, 17) have been reported as examples of bioaugmentation in piggery wastewater treatment. Reduction of N₂O emissions from pig manure compost by addition of nitrite-oxidizing bacteria has also been reported (11). However, there have been no reports of methods for reducing N₂O emissions by bioaugmentation using aerobic denitrifying bacteria.Takaya et al. isolated the aerobic denitrifying bacterium Pseudomonas stutzeri TR2 (26). The denitrification activity of strain TR2 was monitored in batch and continuous cultures, using denitrification and artificial wastewater media, and the strain was found to keep a distinct activity (producing N₂ from NO₃⁻) and to produce a very low level of N₂O at a dissolved oxygen (O₂) concentration of 1.25 mg liter⁻¹. Therefore, strain TR2 should be useful in the future for reducing N₂O emissions from wastewater treatment plants by bioaugmentation. To investigate the feasibility of using strain TR2 for future application to wastewater treatment processes, we examined its denitrification activity, N₂O production, growth rate, and expression of denitrifying genes in batch cultures, using a medium that mimics the composition found in nitrogen removal wastewater plants. Comparison of the properties of strain TR2 with those of well-characterized denitrifying bacteria revealed characteristics of the strain that favor denitrification, although it can also respire oxygen.     

Novel Denitrifying Bacterium Ochrobactrum anthropi YD50.2 Tolerates High Levels of Reactive Nitrogen Oxides

Most studies of bacterial denitrification have used nitrate (NO₃⁻) as the first electron acceptor, whereas relatively less is understood about nitrite (NO₂⁻) denitrification. We isolated novel bacteria that proliferated in the presence of high levels of NO₂⁻ (72 mM). Strain YD50.2, among several isolates, was taxonomically positioned within the α subclass of Proteobacteria and identified as Ochrobactrum anthropi YD50.2. This strain denitrified NO₂⁻, as well as NO₃⁻. The gene clusters for denitrification (nar, nir, nor, and nos) were cloned from O. anthropi YD50.2, in which the nir and nor operons were linked. We confirmed that nirK in the nir-nor operon produced a functional NO₂⁻ reductase containing copper that was involved in bacterial NO₂⁻ reduction. The strain denitrified up to 40 mM NO₂⁻ to dinitrogen under anaerobic conditions in which other denitrifiers or NO₃⁻ reducers such as Pseudomonas aeruginosa and Ralstonia eutropha and nitrate-respiring Escherichia coli neither proliferated nor reduced NO₂⁻. Under nondenitrifying aerobic conditions, O. anthropi YD50.2 and its type strain ATCC 49188^T proliferated even in the presence of higher levels of NO₂⁻ (100 mM), and both were considerably more resistant to acidic NO₂⁻ than were the other strains noted above. These results indicated that O. anthropi YD50.2 is a novel denitrifier that has evolved reactive nitrogen oxide tolerance mechanisms.Environmental bacteria maintain the global nitrogen cycle by metabolizing organic and inorganic nitrogen compounds. Denitrification is critical for maintenance of the global nitrogen cycle, through which nitrate (NO₃⁻) or nitrite (NO₂⁻) is reduced to gaseous nitrogen forms such as N₂ and nitrous oxide (N₂O) (19, 47). Decades of investigations into denitrifying bacteria have revealed their ecological impact (9), their molecular mechanisms of denitrification (13, 25, 47), and the industrial importance of removing nitrogenous contaminants from wastewater (31, 36). Bacterial denitrification is considered to comprise four successive reduction steps, each of which is catalyzed by NO₃⁻ reductase (Nar), NO₂⁻ reductase (Nir), nitric oxide (NO) reductase (Nor), and N₂O reductase (Nos). The reaction of each enzyme is linked to the electron transport chain on the cellular membrane and accompanies oxidative phosphorylation, implying that bacterial denitrification is of as much physiological significance as anaerobic respiration (25, 47). Most denitrifying bacteria are facultative anaerobes and respire with oxygen under aerobic conditions. Because denitrification is induced in the absence of oxygen, it is considered an alternative mechanism of energy conservation that has evolved as an adaptation to anaerobic circumstances (13, 47).Nitrite and NO are hazardous to bacteria, since they generate highly reactive nitrogen species (RNS) under physiological conditions and damage cellular DNA, lipid, and proteins (28, 37). Denitrifying bacteria are thought to be threatened by RNS since they reduce NO₃⁻ to generate NO₂⁻ and NO as denitrifying intermediates. Furthermore, denitrifying bacteria often inhabit environments where they are exposed to NO₂⁻ and NO and hence high levels of RNS. Recent reports suggest that pathogenic bacteria invading animal tissues are attacked by NO generated by macrophages (12). Such bacteria involve denitrifiers, and some of them, for example, Neisseria meningitidis (1) and Pseudomonas aeruginosa, acquire resistance to NO by producing Nor (44). The utilization (reduction) of NO by Brucella increases the survival of infected mice (2). These examples suggest that production of a denitrifying mechanism affects bacterial survival of threats from both endogenous and extracellular RNS. However, the mechanism of RNS tolerance induced by denitrifying bacteria is not fully understood.Ubiquitous gram-negative Ochrobactrum strains are widely distributed in soils and aqueous environments, where they biodegrade aromatic compounds (11), organophosphorus pesticides (45), and other hydrocarbons (38) and remove heavy metal ions such as chromium and cadmium (24). Having been isolated from clinical specimens, Ochrobactrum anthropi is currently recognized as an emerging opportunistic pathogen, although relatively little is known about its pathogenesis and factors contributing to its virulence (7, 30). Manipulation systems have been developed to investigate these issues at the molecular genetic level (33). Some O. anthropi strains have been identified as denitrifiers (21), although the denitrifying properties of these strains have not been investigated in detail. This study was undertaken to examine the denitrifying properties of O. anthropi in more detail. O. anthropi YD50.2 was selected for this study and was isolated herein. The strain denitrified high levels of NO₂⁻ (up to 40 mM) to dinitrogen under anaerobic conditions. The strain was highly resistant to acidified NO₂⁻ under nondenitrifying aerobic conditions. These results indicate that O. anthropi YD50.2 has mechanisms that produce tolerance to RNS.     

Combined Gel Probe and Isotope Labeling Technique for Measuring Dissimilatory Nitrate Reduction to Ammonium in Sediments at Millimeter-Level Resolution

Dissimilatory NO₃⁻ reduction in sediments is often measured in bulk incubations that destroy in situ gradients of controlling factors such as sulfide and oxygen. Additionally, the use of unnaturally high NO₃⁻ concentrations yields potential rather than actual activities of dissimilatory NO₃⁻ reduction. We developed a technique to determine the vertical distribution of the net rates of dissimilatory nitrate reduction to ammonium (DNRA) with minimal physical disturbance in intact sediment cores at millimeter-level resolution. This allows DNRA activity to be directly linked to the microenvironmental conditions in the layer of NO₃⁻ consumption. The water column of the sediment core is amended with ¹⁵NO₃⁻ at the in situ ¹⁴NO₃⁻ concentration. A gel probe is deployed in the sediment and is retrieved after complete diffusive equilibration between the gel and the sediment pore water. The gel is then sliced and the NH₄⁺ dissolved in the gel slices is chemically converted by hypobromite to N₂ in reaction vials. The isotopic composition of N₂ is determined by mass spectrometry. We used the combined gel probe and isotopic labeling technique with freshwater and marine sediment cores and with sterile quartz sand with artificial gradients of ¹⁵NH₄⁺. The results were compared to the NH₄⁺ microsensor profiles measured in freshwater sediment and quartz sand and to the N₂O microsensor profiles measured in acetylene-amended sediments to trace denitrification.Nitrate accounts for the eutrophication of many human-affected aquatic ecosystems (19, 21). Sediment bacteria may mitigate NO₃⁻ pollution by denitrification and anaerobic ammonium oxidation (anammox), which produce N₂ (13, 18). However, inorganic nitrogen is retained in aquatic ecosystems when sediment bacteria reduce NO₃⁻ to NH₄⁺ by dissimilatory nitrate reduction to ammonium (DNRA) (5, 12, 16, 39). Hence, DNRA contributes to rather than counteracts eutrophication (23). DNRA may be the dominant pathway of dissimilatory NO₃⁻ reduction in sediments that are rich in electron donors, such as labile organic carbon and sulfide (4, 8, 17, 38, 55). High rates of DNRA are thus found in sediments affected by coastal aquaculture (8, 36) and settling algal blooms (16).DNRA, denitrification, and the chemical factors that control the partitioning between them (e.g., sulfide) should ideally be investigated in undisturbed sediments. The redox stratification of sediments involves vertical concentration gradients of pore water solutes. These gradients are often very steep, and their measurement requires high-resolution techniques, such as microsensors (26, 42) and gel probes (9, 54). If, for instance, the influence of sulfide on DNRA and denitrification is to be investigated, one wants to know exactly the sulfide concentration in the layers of DNRA and denitrification activity, as well as the flux of sulfide into these layers. This information can easily be obtained using H₂S and pH microsensors (22, 43). It is less trivial to determine the vertical distribution of DNRA and denitrification activity in undisturbed sediments. Denitrification activity can be traced using a combination of the acetylene inhibition technique (51) and N₂O microsensors (1). Acetylene inhibits the last step of denitrification, and therefore, N₂O accumulates in the layer of denitrification activity (44). This method underestimates the denitrification activity in sediments with high rates of coupled nitrification-denitrification because acetylene also inhibits nitrification (50).The vertical distribution of DNRA activity in undisturbed sediment has, to the best of our knowledge, never been determined; thus, the microenvironmental conditions in the layer of DNRA activity remain unknown. Until now, the influence of chemical factors on DNRA and denitrification in sediments has been assessed by slurry incubations (4, 12, 30), by flux measurements with sealed sediment cores (7, 47) or flowthrough sediment cores (16, 27, 37), and in one case, in reconstituted sediment cores sliced at centimeter-level resolution (39). Here, we present a new method, the combined gel probe and isotope labeling technique, to determine the vertical distribution of the net rates of DNRA in sediments. The sediments remain largely undisturbed and the NO₃⁻ amendments are within the range of in situ concentrations. The DNRA measurements can be related to the microprofiles of potential influencing factors measured in close vicinity of the gel probe. This allows DNRA activity to be directly linked with the microenvironmental conditions in the sediment.     

Environmental Factors Shape Sediment Anammox Bacterial Communities in Hypernutrified Jiaozhou Bay,China

Bacterial anaerobic ammonium oxidation (anammox) is an important process in the marine nitrogen cycle. Because ongoing eutrophication of coastal bays contributes significantly to the formation of low-oxygen zones, monitoring of the anammox bacterial community offers a unique opportunity for assessment of anthropogenic perturbations in these environments. The current study used targeting of 16S rRNA and hzo genes to characterize the composition and structure of the anammox bacterial community in the sediments of the eutrophic Jiaozhou Bay, thereby unraveling their diversity, abundance, and distribution. Abundance and distribution of hzo genes revealed a greater taxonomic diversity in Jiaozhou Bay, including several novel clades of anammox bacteria. In contrast, the targeting of 16S rRNA genes verified the presence of only “Candidatus Scalindua,” albeit with a high microdiversity. The genus “Ca. Scalindua” comprised the apparent majority of active sediment anammox bacteria. Multivariate statistical analyses indicated a heterogeneous distribution of the anammox bacterial assemblages in Jiaozhou Bay. Of all environmental parameters investigated, sediment organic C/organic N (OrgC/OrgN), nitrite concentration, and sediment median grain size were found to impact the composition, structure, and distribution of the sediment anammox bacterial community. Analysis of Pearson correlations between environmental factors and abundance of 16S rRNA and hzo genes as determined by fluorescent real-time PCR suggests that the local nitrite concentration is the key regulator of the abundance of anammox bacteria in Jiaozhou Bay sediments.Anaerobic ammonium oxidation (anammox, NH₄⁺ + NO₂⁻ → N₂ + 2H₂O) was proposed as a missing N transformation pathway decades ago. It was found 20 years later to be mediated by bacteria in artificial environments, such as anaerobic wastewater processing systems (see reference 32 and references therein). Anammox in natural environments was found even more recently, mainly in O₂-limited environments such as marine sediments (28, 51, 54, 67, 69) and hypoxic or anoxic waters (10, 25, 39-42). Because anammox may remove as much as 30 to 70% of fixed N from the oceans (3, 9, 64), this process is potentially as important as denitrification for N loss and bioremediation (41, 42, 73). These findings have significantly changed our understanding of the budget of the marine and global N cycles as well as involved pathways and their evolution (24, 32, 35, 72). Studies indicate variable anammox contributions to local or regional N loss (41, 42, 73), probably due to distinct environmental conditions that may influence the composition, abundance, and distribution of the anammox bacteria. However, the interactions of anammox bacteria with their environment are still poorly understood.The chemolithoautotrophic anammox bacteria (64, 66) comprise the new Brocadiaceae family in the Planctomycetales, for which five Candidatus genera have been described (see references 32 and 37 and references therein): “Candidatus Kuenenia,” “Candidatus Brocadia,” “Candidatus Scalindua,” “Candidatus Anammoxoglobus,” and “Candidatus Jettenia.” Due to the difficulty of cultivation and isolation, anammox bacteria are not yet in pure culture. Molecular detection by using DNA probes or PCR primers targeting the anammox bacterial 16S rRNA genes has thus been the main approach for the detection of anammox bacteria and community analyses (58). However, these studies revealed unexpected target sequence diversity and led to the realization that due to biased coverage and specificity of most of the PCR primers (2, 8), the in situ diversity of anammox bacteria was likely missed. Thus, the use of additional marker genes for phylogenetic analysis was suggested in hopes of better capturing the diversity of this environmentally important group of bacteria. By analogy to molecular ecological studies of aerobic ammonia oxidizers, most recent studies have attempted to include anammox bacterium-specific functional genes. All anammox bacteria employ hydrazine oxidoreductase (HZO) (= [Hzo]₃) to oxidize hydrazine to N₂ as the main source for a useable reductant, which enables them to generate proton-motive force for energy production (32, 36, 65). Phylogenetic analyses of Hzo protein sequences revealed three sequence clusters, of which the cladistic structure of cluster 1 is in agreement with the anammox bacterial 16S rRNA gene phylogeny (57). The hzo genes have emerged as an alternative phylogenetic and functional marker for characterization of anammox bacterial communities (43, 44, 57), allowing the 16S rRNA gene-based investigation methods to be corroborated and improved.The contribution of anammox to the removal of fixed N is highly variable in estuarine and coastal sediments (50). For instance, anammox may be an important pathway for the removal of excess N (23) or nearly negligible (48, 54, 67, 68). This difference may be attributable to a difference in the structure and composition of anammox bacterial communities, in particular how the abundance of individual cohorts depends on particular environmental conditions. Anthropogenic disturbance with variable source and intensity of eutrophication and pollution may further complicate the anammox bacterium-environment relationship.Jiaozhou Bay is a large semienclosed water body of the temperate Yellow Sea in China. Eutrophication has become its most serious environmental problem, along with red tides (harmful algal blooms), species loss, and contamination with toxic chemicals and harmful microbes (14, 15, 21, 61, 71). Due to different sources of pollution and various levels of eutrophication across Jiaozhou Bay (mariculture, municipal and industrial wastewater, crude oil shipyard, etc.), a wide spectrum of environmental conditions may contribute to a widely varying community structure of anammox bacteria. This study used both 16S rRNA and hzo genes as targets to measure their abundance, diversity, and spatial distribution and assess the response of the resident anammox bacterial community to different environmental conditions. Environmental factors with potential for regulating the sediment anammox microbiota are discussed.     

Potential Application of N-Carbamoyl-β-Alanine Amidohydrolase from Agrobacterium tumefaciens C58 for β-Amino Acid Production

An N-carbamoyl-β-alanine amidohydrolase of industrial interest from Agrobacterium tumefaciens C58 (βcar_At) has been characterized. βcar_At is most active at 30°C and pH 8.0 with N-carbamoyl-β-alanine as a substrate. The purified enzyme is completely inactivated by the metal-chelating agent 8-hydroxyquinoline-5-sulfonic acid (HQSA), and activity is restored by the addition of divalent metal ions, such as Mn²⁺, Ni²⁺, and Co²⁺. The native enzyme is a homodimer with a molecular mass of 90 kDa from pH 5.5 to 9.0. The enzyme has a broad substrate spectrum and hydrolyzes nonsubstituted N-carbamoyl-α-, -β-, -γ-, and -δ-amino acids, with the greatest catalytic efficiency for N-carbamoyl-β-alanine. βcar_At also recognizes substrate analogues substituted with sulfonic and phosphonic acid groups to produce the β-amino acids taurine and ciliatine, respectively. βcar_At is able to produce monosubstituted β²- and β³-amino acids, showing better catalytic efficiency (k_cat/K_m) for the production of the former. For both types of monosubstituted substrates, the enzyme hydrolyzes N-carbamoyl-β-amino acids with a short aliphatic side chain better than those with aromatic rings. These properties make βcar_At an outstanding candidate for application in the biotechnology industry.N-Carbamoyl-β-alanine amidohydrolase (NCβAA) (EC 3.5.1.6), also known as β-alanine synthase or β-ureidopropionase, catalyzes the third and final step of reductive pyrimidine degradation. In this reaction, N-carbamoyl-β-alanine or N-carbamoyl-β-aminoisobutyric acid is irreversibly hydrolyzed to CO₂, NH₃, and β-alanine or β-aminoisobutyric acid, respectively (43). Eukaryotic NCβAAs have been purified from several sources (10, 25, 33, 39, 42, 44). Nevertheless, only two prokaryotic NCβAAs, belonging to the Clostridium and Pseudomonas genera (4, 29), have been purified to date, although this activity has been inferred for several microorganisms due to the appearance of the reductive pathway of pyrimidine degradation (38, 45). Pseudomonas NCβAA is also able to hydrolyze l-N-carbamoyl-α-amino acids, and indeed, this activity is widespread in the bacterial kingdom (3, 23, 26, 46).β-Amino acids have unique pharmacological properties, and their utility as building blocks of β-peptides, pharmaceutical compounds, and natural products is of growing interest (14). β-Alanine, a natural β-amino acid, is a precursor of coenzyme A and pantothenic acid in bacteria and fungi (vitamin B₅) (7). β-Alanine is widely distributed in the central nervous systems of vertebrates and is a structural analogue of γ-amino-n-butyric acid and glycine, major inhibitory neurotransmitters, suggesting that it may be involved in synaptic transmissions (20). Another important natural β-amino acid is taurine (2-aminoethanesulfonic acid), which plays an important role in several essential processes, such as membrane stabilization, osmoregulation, glucose metabolism, antioxidation, and development of the central nervous system and the retina (9, 28, 33). 2-Aminoethylphosphonate, the most common naturally occurring phosphonate, also known as ciliatine, is an important precursor used in the biosynthesis of phosphonolipids, phosphonoproteins, and phosphonoglycans (5). β-Homoalanine (β-aminobutyric acid) has been used successfully for the design of nonnatural ligands for therapeutic application against autoimmune diseases such as rheumatoid arthritis, multiple sclerosis, or autoimmune uveitis (30). Substituted β-amino acids can be denominated β², β³, and β^2,3, depending on the position of the side chain(s) (R) on the amino acid skeleton (18). β²-Amino acids are not yet as readily available as their β³-counterparts, as they must be prepared using multistep procedures (17).We decided to characterize NCβAA (β-carbamoylase) from Agrobacterium tumefaciens C58 (βcar_At) after showing that some dihydropyrimidinases belonging to the Arthrobacter and Sinorhizobium genera are able to hydrolyze different 5- or 6-substituted dihydrouracils to the corresponding N-carbamoyl-β-amino acids (18, 22). If βcar_At could decarbamoylate the reaction products of dihydrouracils, different β-amino acids would be obtained enzymatically in the same way that α-amino acids are produced via the hydantoinase process (6, 21). We therefore describe the physical, biochemical, kinetic, and substrate specificity properties of recombinant βcar_At.     

Microbial Community Structure and Denitrification in a Wetland Mitigation Bank

Wetland mitigation is implemented to replace ecosystem functions provided by wetlands; however, restoration efforts frequently fail to establish equivalent levels of ecosystem services. Delivery of microbially mediated ecosystem functions, such as denitrification, is influenced by both the structure and activity of the microbial community. The objective of this study was to compare the relationship between soil and vegetation factors and microbial community structure and function in restored and reference wetlands within a mitigation bank. Microbial community composition was assessed using terminal restriction fragment length polymorphism targeting the 16S rRNA gene (total bacteria) and the nosZ gene (denitrifiers). Comparisons of microbial function were based on potential denitrification rates. Bacterial community structures differed significantly between restored and reference wetlands; denitrifier community assemblages were similar among reference sites but highly variable among restored sites throughout the mitigation bank. Potential denitrification was highest in the reference wetland sites. These data demonstrate that wetland restoration efforts in this mitigation bank have not successfully restored denitrification and that differences in potential denitrification rates may be due to distinct microbial assemblages observed in restored and reference (natural) wetlands. Further, we have identified gradients in soil moisture and soil fertility that were associated with differences in microbial community structure. Microbial function was influenced by bacterial community composition and soil fertility. Identifying soil factors that are primary ecological drivers of soil bacterial communities, especially denitrifying populations, can potentially aid the development of predictive models for restoration of biogeochemical transformations and enhance the success of wetland restoration efforts.Wetlands provide more ecosystem services (e.g., flood control, water purification, nutrient cycling, and habitat for wildlife) per hectare than any other ecosystem (16). Riparian wetlands, in particular, are sites of intense biogeochemical activity and play an important role in improving water quality, recycling nutrients, and detoxifying chemicals (41). Changing patterns of land use over the last century have resulted in the loss of over half of the wetlands in the contiguous United States (17) and about 60% of wetlands in the Midwestern United States (82). The loss of ecosystem services through conversion of wetlands to alternative (primarily agricultural) land uses exacerbates nutrient pollution and eutrophication of downstream ecosystems (57). Declines in wetland acreage have continued despite a federal policy goal of no-net-loss of wetland acreage and function adopted in 1990 (7, 55). Wetland mitigation projects provide compensation for impacted wetlands and aim to replace the critical functions provided by wetlands. Despite decades of wetland mitigation, however, restoration efforts frequently fail to reestablish desired levels of ecosystem services. Restoration outcomes remain uncertain, and more information is necessary in order to improve monitoring and assessment of wetland development (13, 18, 50, 80).One approach to wetland compensation is through mitigation banks. These sites are areas that are restored, established, enhanced, or preserved for replacement of wetlands that will be affected by future land use change. Mitigation banks are considered “third-party” compensatory mitigation, where the permittee (e.g., developer planning to destroy a wetland) is responsible for purchasing wetland credits in acreage, but the wetland bank is established and managed by another party (24). Wetland mitigation banks have unique characteristics that distinguish them from smaller individual restoration projects (7, 69, 81). Due to their size, wetland mitigation banks are especially heterogeneous and may have a great deal of within-site variability in hydrology and nutrient status, making it challenging to implement a single restoration design. Thus, wetland mitigation banks require intense management and monitoring for improved success (7, 69, 81).Restoration efforts such as mitigation banks aim to replace chemical, physical, and biological ecosystem functions of wetlands that have been lost through anthropogenic disturbance (24). Monitoring of wetland mitigation sites has largely focused on measures of macro-scale community structure (e.g., vegetation surveys) (52) along with measures of hydrology and soil type (24). Measurement of vegetation is a common proxy for wetland performance but does not provide an accurate assessment of wetland function (6, 52). Quantitative assessment is achievable, however, for ecosystem services such as water quality improvement through nitrate removal, where well-characterized microbial mechanisms underlie denitrification processes.The link between microbial community structure and function in a restoration context is a topic of current interest (33). Relating microbial community composition and dynamics to chemical, physical, and biological variables can help to reveal important ecological drivers of microbial communities and their activities (26, 35, 42). Conserved bacterial functional genes related to specific biogeochemical transformations allow evaluation of the community structure of microbial populations directly involved in these processes (49, 60, 63, 77, 79). Assessing the diversity of microorganisms that are specifically involved in denitrification is possible through amplification of the nosZ gene, which encodes the catalytic subunit of nitrous oxide reductase, the enzyme responsible for the final step of denitrification (60, 63, 66). Phylogenetically diverse microorganisms can carry out denitrification though the majority of previously described denitrifiers belong to subphyla within the Proteobacteria (53, 56, 60, 61). Denitrification is a facultative process that occurs only under anaerobic conditions (53, 75). Complete denitrification to N₂ is more prevalent in anaerobic, saturated wetland ecosystems (14, 76), and incomplete denitrification to N₂O is the less desirable, more common endpoint of denitrification under more aerobic, drier conditions (14, 62). While the environmental factors (e.g., oxygen, carbon, nitrate, and pH) that influence bulk denitrification rates have been well characterized (31, 72), the influence of these factors on the composition of denitrifier communities, particularly in a restoration context, is unclear. Understanding the relationship between the microbial populations responsible for nitrogen transformations and easily measured environmental parameters (e.g., soil chemical and physical measures) could lead to assessment metrics that are linked directly to ecosystem functions such as denitrification and bridge the current gap in functional assessment methods (36, 60, 70).The objectives of this study were (i) to compare the microbial and plant community composition in restored wetlands to the composition in adjacent reference floodplain forest wetlands; (ii) to assess the relationship between microbial community composition (based on terminal restriction fragment length polymorphism [T-RFLP]) and potential denitrification activity throughout the mitigation bank; and (iii) to examine soil factors correlated with microbial community composition using both phylogenetic and functional gene markers. As soil environmental conditions affect microbial community structure and activity, we expected that sites where wetland hydrology and soil chemistry have been successfully restored would harbor microbial assemblages that are similar in composition and denitrification function to those observed in reference wetlands within this mitigation bank.     

Rapid Microarray-Based Genotyping of Enterohemorrhagic Escherichia coli Serotype O156:H25/H?/Hnt Isolates from Cattle and Clonal Relationship Analysis

Since enterohemorrhagic Escherichia coli (EHEC) isolates of serogroup O156 have been obtained from human diarrhea patients and asymptomatic carriers, we studied cattle as a potential reservoir for these bacteria. E. coli isolates serotyped by agglutination as O156:H25/H−/Hnt strains (n = 32) were isolated from three cattle farms during a period of 21 months and characterized by rapid microarray-based genotyping. The serotyping by agglutination of the O156 isolates was not confirmed in some cases by the results of DNA-based serotyping as only 25 of the 32 isolates were conclusively identified as O156:H25. In the multilocus sequence typing (MLST) analysis, all EHEC O156:H25 isolates were characterized as sequence type 300 (ST300) and ST688, which differ by a single-nucleotide exchange in the purA gene. Oligonucleotide microarrays allow simultaneous detection of a wider range of EHEC-associated and other E. coli virulence markers than other methods. All O156:H25 isolates showed a wide spectrum of virulence factors typical for EHEC. The stx₁ genes combined with the EHEC hlyA (hlyA_EHEC) gene, the eae gene of the ζ subtype, as well as numerous other virulence markers were present in all EHEC O156:H25 strains. The behavior of eight different cluster groups, including four that were EHEC O156:H25, was monitored in space and time. Variations in the O156 cluster groups were detected. The results of the cluster analysis suggest that some O156:H25 strains had the genetic potential for a long persistence in the host and on the farm, while other strains did not. As judged by their pattern of virulence markers, E. coli O156:H25 isolates of bovine origin may represent a considerable risk for human infection. Our results showed that the miniaturized E. coli oligonucleotide arrays are an excellent tool for the rapid detection of a large number of virulence markers.Shiga toxin-producing Escherichia coli (STEC) strains comprise a group of zoonotic enteric pathogens (45). In humans, infections with some STEC serotypes may result in hemorrhagic or nonhemorrhagic diarrhea, which can be complicated by the hemolytic uremic syndrome (HUS) (32). These STEC strains are also designated enterohemorrhagic Escherichia coli (EHEC). Consequently, EHEC strains represent a subgroup of STEC with high pathogenic potential for humans. Although E. coli O157:H7 is the most frequent EHEC serotype implicated in HUS, other serotypes can also cause this complication. Non-O157:H7 EHEC strains including serotypes O26:H11/H−, O103:H2/H−, O111:H8/H10/H−, and O145:H28/H25/H− and sorbitol-fermenting E. coli O157:H− isolates are present in about 50% of stool cultures from German HUS patients (10, 42). However, STEC strains that cause human infection belong to a large number of E. coli serotypes, although a small number of STEC isolates of serogroup O156 were associated with human disease (7). Strains of the serotypes O156:H1/H8/H21/H25 were found in human cases of diarrhea or asymptomatic infections (9, 22, 25, 26). The detection of STEC of serogroup O156 from healthy and diseased ruminants such as cattle, sheep, and goats was reported by several authors (1, 11-13, 21, 39, 46, 50, 52). Additional EHEC-associated virulence genes such as stx, eae, hlyA_EHEC, or nlaA were found preferentially in the serotypes O156:H25 and O156:H− (11-13, 21, 22, 50, 52).Numerous methods exist for the detection of pathogenic E. coli, including genotypic and phenotypic marker assays for the detection of virulence genes and their products (19, 47, 55, 57). All of these methods have the common drawback of screening a relatively small number of determinants simultaneously. A diagnostic DNA microarray based on the ArrayTube format of CLONDIAG GmbH was developed as a viable alternative due to its ability to screen multiple virulence markers simultaneously (2). Further microarray layouts working with the same principle but different gene targets were developed for the rapid identification of antimicrobial resistance genes in Gram-negative bacteria (5) and for the rapid DNA-based serotyping of E. coli (4). In addition, a protein microarray for E. coli O serotyping based on the ArrayTube format was described by Anjum et al. (3).The aim of our study was the molecular genotyping of bovine E. coli field isolates of serogroup O156 based on miniaturized E. coli oligonucleotide arrays in the ArrayStrip format and to combine the screening of E. coli virulence markers, antimicrobial resistance genes, and DNA serotyping targets, some of which were partially described previously for separate arrays (2, 4, 5). The epidemiological situation in the beef herds from which the isolates were obtained and the spatial and temporal behavior of the clonal distribution of E. coli serogroup O156 were analyzed during the observation period. The potential risk of the isolates inducing disease in humans was assessed.     

Hitherto Unknown [Fe-Fe]-Hydrogenase Gene Diversity in Anaerobes and Anoxic Enrichments from a Moderately Acidic Fen

Newly designed primers for [Fe-Fe]-hydrogenases indicated that (i) fermenters, acetogens, and undefined species in a fen harbor hitherto unknown hydrogenases and (ii) Clostridium- and Thermosinus-related primary fermenters, as well as secondary fermenters related to sulfate or iron reducers might be responsible for hydrogen production in the fen. Comparative analysis of [Fe-Fe]-hydrogenase and 16S rRNA gene-based phylogenies indicated the presence of homologous multiple hydrogenases per organism and inconsistencies between 16S rRNA gene- and [Fe-Fe]-hydrogenase-based phylogenies, necessitating appropriate qualification of [Fe-Fe]-hydrogenase gene data for diversity analyses.Molecular hydrogen (H₂) is important in intermediary ecosystem metabolism (i.e., processes that link input to output) in wetlands (7, 11, 12, 33) and other anoxic habitats like sewage sludges (34) and the intestinal tracts of animals (9, 37). H₂-producing fermenters have been postulated to form trophic links to H₂-consuming methanogens, acetogens (i.e., organisms capable of using the acetyl-coenzyme A [CoA] pathway for acetate synthesis) (7), Fe(III) reducers (17), and sulfate reducers in a well-studied moderately acidic fen in Germany (11, 12, 16, 18, 22, 33). 16S rRNA gene analysis revealed the presence of Clostridium spp. and Syntrophobacter spp., which represent possible primary and secondary fermenters, as well as H₂ producers in this fen (11, 18, 33). However, H₂-producing bacteria are polyphyletic (30, 31, 29). Thus, a structural marker gene is required to target this functional group by molecular methods. [Fe-Fe]-hydrogenases catalyze H₂ production in fermenters (19, 25, 29, 30, 31), and genes encoding [Fe-Fe]-hydrogenases represent such a marker gene. The objectives of this study were to (i) develop primers specific for highly diverse [Fe-Fe]-hydrogenase genes, (ii) analyze [Fe-Fe]-hydrogenase genes in pure cultures of fermenters, acetogens, and a sulfate reducer, (iii) assess [Fe-Fe]-hydrogenase gene diversity in H₂-producing fen soil enrichments, and (iv) evaluate the limitations of the amplified [Fe-Fe]-hydrogenase fragment as a phylogenetic marker.