Table of Contents Author Guidelines Submit a Manuscript
Applied and Environmental Soil Science
Volume 2009 (2009), Article ID 929120, 7 pages
Research Article

Plant-Soil Relationships of Bromus tectorum L.: Interactions among Labile Carbon Additions, Soil Invasion Status, and Fertilizer

Exotic and Invasive Weed Research Unit, USDA-ARS, 920 Valley Road, Reno, NV 89512, USA

Received 27 April 2009; Revised 24 June 2009; Accepted 1 September 2009

Academic Editor: Amarilis de Varennes

Copyright © 2009 Robert R. Blank and James A. Young. This is an open access article distributed under the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original work is properly cited.


Invasion of western North America by the annual exotic grass Bromus tectorum L. (cheatgrass) has been an ecological disaster. High soil bioavailability of nitrogen is a contributing factor in the invasive potential of B. tectorum. Application of labile carbon sources to the soil can immobilize soil nitrogen and favor native species. We studied the interaction of labile carbon addition (sucrose), with soil invasion status and fertilizer addition on the growth of B. tectorum. Soils were noninvaded (BNI) and B. tectorum invaded (BI). Treatments were control, sucrose, combined fertilizer, and sucrose + fertilizer. The greenhouse experiment continued for 3 growth-cycles. After the 1st growth-cycle, sucrose addition reduced B. tectorum aboveground mass almost 70 times for the BI soil but did not significantly reduce growth in the BNI soil. B. tectorum aboveground mass, after the 1st growth-cycle, was over 27 times greater for BI control soils than BNI control soils. Although sucrose addition reduced soil-solution , tissue N was not significantly lowered, suggesting that reduction of soil available N may not be solely responsible for reduction in B. tectorum growth. Noninvaded soil inhibits growth of B. tectorum. Understanding this mechanism may lead to viable control strategies.

1. Introduction

Soil nutrient availability is a principal determinant in structuring plant communities [13] and if excessive, it can facilitate invasion by weedy plant species [4, 5]. Availability of inorganic soil N is especially robust in determining winners and losers in plant competitive outcomes [6, 7], and high availability can enhance the competitive potential of fast-growing weedy species over slower-growing species [4, 8]. One can cause local extirpation or proliferation of particular plants and alter plant seral stage through manipulation of soil N resources, either through the addition of a soluble N form or sequestration of soil N via the addition of a labile C source such as sucrose [912]. Our research unit and others have demonstrated that multiple sucrose additions over time to the soil can extirpate fast growing exotic annuals and thereby allow more nutrient use efficient native species to establish [1215]. The underlying mechanism for this restoration strategy is that sucrose stimulates the proliferation of soil microorganisms, which uptake and immobilize soil inorganic N resources away from plants [12, 16]. In this lowered available soil N regime, plants with greater N use efficiency, such as native perennials, have an establishment window without undue competition from fast growing annuals [11, 17, 18]. This mechanism, however, may not hold in all situations [19]. Although labile C addition to soil has been shown to lower available N [15, 20], there is no definitive evidence that decreased availability of soil N is the sole or principal determinant controlling competitive outcomes among exotic annuals and native species. For example, ortho-P, rather than N availability, may control competitive interactions for diffuse knapweed (Centaurea diffusa L.) [21]. Moreover, the utility of using a labile C source such as sucrose in restoration of exotic annual grass-dominated communities has pitfalls. If desirable plants do not establish during the period of lowered N-availability, eventually microbial turnover may release a flush of available N and heighten risk of weed reinvasion. In addition, it is unclear if one can generalize that greater available soil N facilitates more growth of invasive annuals relative to native plants [22, 23]. Finally, we are unaware of any studies that have explored the possibility that labile C additions affect plant growth in other ways besides reduced N availability.

Invasion by exotic plants can fundamentally alter soil characteristics relative to those characteristics that evolved during pedogenesis under native vegetation. Biogeochemical cycling, the soil biotic community, and N dynamics may be so changed by plant invasion that the soil begins to follow a different pedogenic trajectory [2427]. Cheatgrass (Bromus tectorum L.) is the most prevalent exotic invasive plant in the Great Basin of the western United States [28]. This annual grass forms tufts up to 2-feet (0.6 m) tall and can germinate in the fall or spring. B. tectorum has the potential to completely alter ecosystems by replacing native vegetation and fostering large-scale catastrophic wildfires. Moreover, invasion by B. tectorum disrupts food-webs, alters soil N dynamics, lowers species diversity, and decreases fungi populations [29, 30]. It is reasonable, then, to suspect that a particular soil invaded by B. tectorum for a period of time might respond differently to treatments such as addition of labile C and fertilizer than that same soil not invaded by B. tectorum. Bromus tectorum invasion increased porosity, altered soil organic matter dynamics, and enhanced microbial decomposition relative to noninvaded sites [31]. Given the potential of B. tectorum to alter soil properties, a reasonable conjecture is that long-term invaded soil may function differently as a growth media than noninvaded sites.

Since 1998, we have monitored an invasion of a winterfat (Krascheninnikovia lanata (Pursh) A.D.J. Neeuse & Smit) community by B. tectorum in the Honey Lake Valley of northeastern California. New colonizations, spreading from the invasion front, are small and widely spaced and often recruit in the canopy of K. lanata. At the same time, in adjacent areas that have been invaded for several years, plants of B. tectorum are far larger and denser. It is only in the 2nd and 3rd years of invasion that plant stature increases markedly and plants become more prevalent in interspace positions. From these observations, it appeared that there was a soil factor in noninvaded areas that was inhibiting initial populations of B. tectorum and that the inhibitory factor was muted upon invasion. The previous observations are consistent with the “biological inertia” theory of plant community invasibility [32]. Based on these observations and previous research the following null hypotheses were proposed for testing.

(1)Immobilization of N, upon sucrose addition, is the controlling factor in the reduction of B. tectorum growth.(2)Growth of B. tectorum will be alike in soils invaded by B. tectorum for several years relative to a similar soil not yet invaded.

2. Materials and Methods

Soil was collected from a winterfat (Krascheninnikovia lanata (Pursh) A.D.J. Neeuse & Smit) community in the Honey Lake Valley of northeastern California, USA (40°08’N, 120°04’W) that is presently being invaded by cheatgrass (Bromus tectorum L.). The A horizon (0 20 cm) was collected from shrub interspace microsites at 2 sites from an area that has been invaded by B. tectorum for at least 4 years (BI) and a nearby noninvaded area (BNI). General properties of soils, taken from a contemporaneous research project at the same study site, are provided in Table 1. Values are average of 4 samples taken throughout the year. Textural class was determined by hand texturing. Organic C quantified after removal of CaCO3 with acid. Available N is NO3- and NH4+ extracted with KCl [33]. Net N mineralization was determined by the difference of total N after 30-day moist aerobic incubation minus that initially present. At each site, soil was obtained by compositing over 100 subsamples from an area of about 100 m2. The two disturbed soils were transported to the greenhouse, homogenized, and immediately filled into tapered containers (15 cm upper diameter, 13.5 cm lower diameter, 16 cm depth, 3 kg for each soil type). Treatments were “control” (only planted and watered), “sucrose” (20 g applied to the soil surface), “fert”, and “sucrose fert”. Fert was applied as 80 mL of aqueous solution containing 4.6 g N as ammoniacal-N (23%), nitrate-N (22%), and urea-N (55%). Five seeds of B. tectorum were sown near the center of each container, and germinating seeds plucked to allow only one to grow. Soil was kept near field capacity with deionized water but watered sparingly to avoid leaching. Aboveground and root mass were harvested after 72-day growth, the soil homogenized, and a 10 g subsample from each container was reserved for soil analyses. Containers were refilled with the same soil, sown with multiple seeds of B. tectorum as before, and grown and harvested for 2 more times. In the 2nd and 3rd growth-cycles, also 72-day total growth, no sucrose was added but fertilizer was added at the same rate. After each harvest, the following parameters were measured: (1) aboveground mass and root mass after drying 48 hours at 60°C, (2) leaf tissue N concentration by the Kjeldahl procedure, and (3) soil-solution concentration of NO3-, and acetate by immiscible displacement [34] with quantification by gradient elution ion chromatography with suppressed conductivity detection. We also randomly collected 4 replicate A horizon samples from BI and BNI areas and sent to a commercial laboratory for microbial characterization by phospholipid fatty acids (PLFA). At the time samples were collected, BI sites had been invaded for at least 4 years. PLFA characterizes the entire microbial community including viable biomass concentrations, community composition, and metabolic status [35].

Table 1: Initial properties of the soils.

The greenhouse experiment was completely randomized as pots were periodically moved through the course of the experiment. The ANOVA was a mixed model with repeated measures on growth-cycle and random error term of pot within soil and treatment [36]. The experiment had 6 replicates soil invasion types (BNI and BI), treatments (control, sucrose, fert, sucrose fert) growth-cycles 144 total pots. Data normalization required transformation of some variables. Confidence intervals at the 95% level were derived for the highest order significant ( ) interactions. Initial soil and PLFA data were analyzed using an unpaired -test.

3. Results

3.1. Initial Properties of Soils

Soil occupied by B. tectorum (BI) for at least 4 years was grossly similar in properties to soil not yet invaded (BNI) (Table 1). BI soil had higher concentrations of C and N, but the C/N was very similar between the two soils. BI soil had a lower pH than BNI soil. BNI and BI soil had very similar N availability and net N mineralization potentials.

After 4-year invasion by B. tectorum, the soil microbial community has been considerably altered as elucidated by phospholipid fatty acids (PLFAs). BI soil has significantly greater total microbial biomass, eukarya biomass, and a greater ratio of bacteria to eukarya than BNI soil (Table 2).

Table 2: Selected results of PLFA analyses for BNI and BI soils.
3.2. Plant Parameters

An interaction among treatment, soil invasion status, and growth-cycle influenced aboveground ( ) and root mass ( ) of B. tectorum (Table 3). In the 1st growth-cycle, aboveground mass of B. tectorum grown in controls was over 27 times less in the BNI soil relative to the BI soil. Overall, this growth differential was reduced in the 2nd growth-cycle and could be partially overcome by addition of fertilizer, especially in the 3rd growth-cycle. For the BNI soil only, sucrose addition did not significantly reduce aboveground or root mass of B. tectorum relative to the controls. Soil treatments had a large impact on B. tectorum growth in the BI soil. Relative to the BI controls, sucrose addition negatively affected B. tectorum growth for the 1st growth-cycle only; aboveground mass was reduced over 68 times and root mass was reduced over 56 times. The sucrose fert treatment produced similar, albeit less, decline in plant mass relative to the controls, reducing aboveground mass over 14 times and root mass over 18 times. Following the 2nd and 3rd growth-cycles, aboveground and root mass of B. tectorum were statistically similar between sucrose amended and control soils. The sucrose fert treatment, however, resulted in much higher growth after the 2nd cycle than the corresponding controls; aboveground mass was over 40 times greater for the BNI soil and over 3 times greater for the BI soil. This significant trend continued after the 3rd growth-cycle, but differences were lower. Growth of B. tectorum tended to be higher upon fertilizer additions relative to controls; but significant increases in aboveground and root biomass only occurred after the 2nd growth-cycle for the fert treatment and only for the BNI soil.

Table 3: Influence of treatment, soil invasion status, and growth-cycle on B. tectorum growth and leaf N concentration.

Leaf N concentration was affected by significant soil growth-cycle and treatment growth-cycle interactions (Table 3). For all growth-cycles, control and sucrose treatments have statistically similar leaf N concentrations. For both soils, the sucrose fert treatment significantly increased tissue N concentration for all growth-cycles relative to the corresponding controls. For the 1st growth-cycle, fertilizer additions did not affect tissue N concentration relative to the control. Relative to controls, the fertilizer treatment significantly increased tissue N concentration after the 2nd and 3rd growth-cycles.

3.3. Soil Parameters

Treatment soil growth-cycle interaction significantly affected soil-solution NO3- concentration (Table 4). After the 1st growth-cycle, NO3- was significantly less in the BNI soil for every treatment except sucrose and sucrose fert compared to the corresponding BI treatments. This response pattern continued after the 2nd growth-cycle except that NO3- was now statistically similar to the fert treatment. After the 3rd growth-cycle, soil-solution NO3- was statistically similar between BI and BNI soils for all treatments, except for the fert treatment. Sucrose addition caused a significant decline in soil-solution NO3- relative the control, but only for the BI soil after the 1st growth-cycle, although there was a strong trend lower for both BI and BNI soil after the 2nd growth-cycle (Table 4). Except for the BNI soil after the 1st growth-cycle, the fert application rate significantly increased soil-solution NO3- for both soils and all growth-cycles, relative to controls. Acetate in the soil-solution was influenced by a treatment main effect (Table 4). Soil-solution acetate concentration was significantly greater for the sucrose and sucrose fert treatment compared to the other treatments.

Table 4: Influence of treatment, soil invasion status, and growth-cycle on soil-solution nitrate and acetate.

4. Discussion

In this container experiment, growth of B. tectorum was strongly affected by treatment, growth cycle, and whether the soil was not yet invaded or invaded for about 4 years by B. tectorum. Myriad traits contribute to the competitive stature of plants and considerable effort has been expended to decipher those traits most predictive of invasive success [37, 38]. A robust predictor of invasion success for some plants is rapid growth during the seedling stage [39]. Thus, the huge variability of B. tectorum growth brought about by sucrose addition, fertilizer addition, and if the soil was previously invaded has enormous ecological significance for its potential control.

In the 1st growth cycle following sucrose addition to a soil previously invaded by B. tectorum (BI), aboveground mass of B. tectorum was reduced, an astonishing 98 percent relative to the control soil. The magnitude of growth reduction of this invasive annual grass is illustrative of why labile carbon sources have been tested in the field as a potential tool to restore invaded rangelands in the western United States [40]. The fact that the growth reduction properties of sucrose were lost after the 1st growth cycle vividly displays that sucrose addition to control invasive weeds like B. tectorum has a very short window of efficacy. It is generally assumed that sucrose and other labile C sources stimulate microbial activity and immobilize mineral N [16, 41, 42]. Moreover, all references that we are aware of implicate this decrease in available soil N as the causative factor in explaining how labile C sources extirpate fast growing exotic annuals from ecosystems [9, 10, 12, 15]. In the present study, we do not dispute that a major cause in the reduction in B. tectorum upon sucrose addition is a consequence of reduced availability of N. Indeed, after the 1st growth cycle, leaf N of B. tectorum grown in sucrose-amended soil was much less than that of B. tectorum grown in control soil. Our data, however, suggest that the sucrose addition causes additional reduction in B. tectorum growth via another mechanism, thus forcing rejection of hypothesis 1. Firstly, after the 2nd and 3rd growth-cycles, B. tectorum growth in sucrose-amended soil was statistically similar to controls; yet soil-solution NO3- was considerably less than in the control soils. These findings suggest that although soil-solution pools of NO3- are likely suboptimal for maximal growth in the sucrose amended soils, B. tectorum was still able to acquire N in similar concentrations as plants grown in the control soils. Secondly, in the 1st growth-cycle, sucrose fert addition to the BI soil significantly reduced the growth of B. tectorum and depressed levels of NO3- in the soil-solution, compared to the corresponding controls; yet, tissue N concentration was statistically greater. Clearly, B. tectorum was able to access a portion of the added N fertilizer, but it did not aid its growth.

What mechanisms, beside immobilization of available N, could reduce B. tectorum growth in sucrose-amended soil? There are myriad interactions with the soil microbial community when a labile C source such as sucrose is added [16]. Organisms capable of utilizing a particular substrate proliferate [43]. These organisms in kind may produce secondary metabolites that can negatively affect plant growth [44]. We suspect that sucrose addition stimulates production of an inhibitory factor that retards the growth of B. tectorum. One possibility is that production of acetate and other metabolites of fermentation, typical of sucrose-amended soil [45], hinders B. tectorum growth. Fermentation metabolites have been shown to retard root elongation and inhibit root initiation [46, 47]. Data from our study indicate a strong relationship between sucrose addition and acetate levels in the soil-solution after the 1st growth cycle (Table 4). Moreover, at least for the 1st growth cycle, the greatest concentrations of acetate corresponded to the greatest reduction in B. tectorum growth (Tables 3 and 4).

Soil invasion status significantly influenced B. tectorum growth therefore forcing rejection of null hypothesis 2. After the first, second, and third growth cycles, respectively, B. tectorum aboveground mass in BNI control soil was 96, 92, and 59 percent less than in the BI control soil. Given the similarity in initial soil properties (Table 1) and that both soils were collected from a similar pre-existing plant community, the growth dichotomy is perplexing. Invasive plants are known to increase soil nutrient availability, particularly N [48]. Long-term occupation of a soil by B. tectorum may have altered or “engineered” the soil to mineralize N at a faster rate than a similar soil initially planted to B. tectorum. Indeed, BI soil has far greater microbial biomass and a greater proportion of eukarya to bacteria than does BNI soil (Table 2). Perhaps the greater abundance of microbes in the BI soil fosters greater availability of N through elevated mineralization. Elevated availability of N greatly increases B. tectorum growth [3, 49], and under most treatments in this study, availability of N was greater for the BI soil (Table 3). If available soil N was the sole factor explaining the dichotomy in B. tectorum growth between the BI and BNI soil, then why did not addition of fertilizer N to the BNI soil in the 1st growth cycle overcome any potential N deficiency? Furthermore, the ratios of both soils are similar and quite low (Table 1) suggesting that N will be available for plant growth as mineralization occurs. As an alternative hypothesis, we propose that soil not yet invaded by B. tectorum has an inhibitory factor. Moreover, this suspect inhibitory factor decreases as time of occupation by B. tectorum increases (Table 3). Our hypothesis is consistent with the Von Holle et al. [32] theory of “biological inertia,” which may involve allelopathic chemicals released by the native community thereby suppressing invading plants. Apparently this suspect inhibitory factor in the BNI soil can be mediated by a combination of sucrose fertilizer as witnessed by the large increase in B. tectorum biomass in the 2nd growth-cycle (Table 3). Such a response suggests that sucrose addition may have encouraged the growth of microorganisms that lessened (decomposed?) the inhibitory factor (see [50] e.g.). At this time, however, we lack definitive evidence concerning the inhibitory nature of freshly-collected soil.

If noninvaded soil is, at least initially, inhibitory to B. tectorum, how does it establish? One possibility is that initial populations of B. tectorum albeit small in stature and widely spaced facilitate alteration of the soil such that the factor(s) responsible for growth inhibition is reduced or eliminated. Invasion by B. tectorum has been shown to alter soil microbial communities and soil food webs relative to what occurs under native species [30]. Greater understanding of the inhibitory effect of fresh noninvaded soil and the pathways by which invasion decreases the inhibitory factor(s) may offer new avenues for control for B. tectorum and other invasive plants.


The authors thank Ms. Fay Allen and Ms. Tye Morgan for greenhouse and laboratory assistance.


  1. G. D. Tilman, “Plant dominance along an experimental nutrient gradient,” Ecology, vol. 65, no. 5, pp. 1445–1453, 1984. View at Publisher · View at Google Scholar
  2. R. Aerts and F. Berendse, “The effect of increased nutrient availability on vegetation dynamics in wet heathlands,” Vegetatio, vol. 76, pp. 63–70, 1988. View at Google Scholar
  3. E. F. Redente, J. E. Friedlander, and T. McLendon, “Response of early and late semiarid seral species to nitrogen and phosphorus gradients,” Plant & Soil, vol. 140, no. 1, pp. 127–135, 1992. View at Google Scholar
  4. L. F. Huenneke, S. P. Hamburg, R. Koide, H. A. Mooney, and P. M. Vitousek, “Effects of soil resources on plant invasion and community structure in Californian serpentine grassland,” Ecology, vol. 71, no. 2, pp. 478–491, 1990. View at Google Scholar
  5. Y. Li and M. Norland, “The role of soil fertility in invasion of Brazilian pepper (Schinus terebinthifolius) in Everglades National Park, Florida,” Soil Science, vol. 166, no. 6, pp. 400–405, 2001. View at Publisher · View at Google Scholar
  6. G. Ettershank, J. A. Ettershank, M. Bryant, and W. G. Whitford, “Effects of nitrogen fertilization on primary production in a Chihuahuan Desert ecosystem,” Journal of Arid Environments, vol. 1, pp. 135–139, 1978. View at Google Scholar
  7. D. Tilman and D. Wedin, “Dynamics of nitrogen competition between successional grasses,” Ecology, vol. 72, no. 3, pp. 1038–1049, 1991. View at Google Scholar
  8. M. A. Vinton and I. C. Burke, “Interactions between individual plant species and soil nutrient status in shortgrass steppe,” Ecology, vol. 76, no. 4, pp. 1116–1133, 1995. View at Google Scholar
  9. W. K. Lauenroth, J. L. Dodd, and P. L. Sims, “The effects of water- and nitrogen-induced stresses on plant community structure in a semiarid grassland,” Oecologia, vol. 36, no. 2, pp. 211–222, 1978. View at Publisher · View at Google Scholar
  10. T. McLendon and E. F. Redente, “Effects of nitrogen limitation on species replacement dynamics during early secondary succession on a semiarid sagebrush site,” Oecologia, vol. 91, no. 3, pp. 312–317, 1992. View at Publisher · View at Google Scholar
  11. P. Alpert and J. L. Maron, “Carbon addition as a countermeasure against biological invasion by plants,” Biological Invasions, vol. 2, no. 1, pp. 33–40, 2000. View at Publisher · View at Google Scholar
  12. M. W. Paschke, T. McLendon, and E. F. Redente, “Nitrogen availability and old-field succession in a shortgrass steppe,” Ecosystems, vol. 3, no. 2, pp. 144–158, 2000. View at Publisher · View at Google Scholar
  13. J. A. Young, R. R. Blank, and W. S. Longland, “Nitrogen enrichment-immobilization to control succession in arid land plant communities,” Journal of Arid Land Studies, vol. 5, pp. 57–60, 1995. View at Google Scholar
  14. J. A. Young, J. D. Trent, R. R. Blank, and D. E. Palmquist, “Nitrogen interactions with medusahead (Taeniatherum caput-medusae ssp. asperum) seedbanks,” Weed Science, vol. 46, no. 2, pp. 191–195, 1998. View at Google Scholar
  15. D. M. Blumenthal, N. R. Jordan, and M. P. Russelle, “Soil carbon addition controls weeds and facilitates prairie restoration,” Ecological Applications, vol. 13, no. 3, pp. 605–615, 2003. View at Google Scholar
  16. M. Alexander, Introduction to Soil Microbiology, John Wiley & Sons, New York, NY, USA, 1977.
  17. F. S. Chapin III, “The mineral nutrition of wild plants,” Review of Ecology and Systematics, vol. 11, pp. 233–260, 1980. View at Google Scholar
  18. E. Garnier, G. W. Koch, J. Roy, and H. A. Mooney, “Responses of wild plants to nitrate availability,” Oecologia, vol. 79, no. 4, pp. 542–550, 1989. View at Publisher · View at Google Scholar
  19. J. D. Corbin and C. M. D'Antonio, “Can carbon addition increase competitiveness of native grasses? A case study from California,” Restoration Ecology, vol. 12, no. 1, pp. 36–43, 2004. View at Publisher · View at Google Scholar
  20. T. R. Seastedt and D. C. Hayes, “Factors influencing nitrogen concentrations in soil water in a North American tallgrass prairie,” Soil Biology and Biochemistry, vol. 20, no. 5, pp. 725–729, 1988. View at Google Scholar
  21. K. N. Suding, K. D. LeJeune, and T. R. Seastedt, “Competitive impacts and responses of an invasive weed: dependencies on nitrogen and phosphorus availability,” Oecologia, vol. 141, no. 3, pp. 526–535, 2004. View at Publisher · View at Google Scholar · View at PubMed
  22. P. N. Lowe, W. K. Lauenroth, and I. C. Burke, “Effects of nitrogen availability on the growth of native grasses exotic weeds,” Journal of Range Management, vol. 55, no. 1, pp. 94–98, 2002. View at Google Scholar
  23. C. Yoder and M. Caldwell, “Effects of perennial neighbors and nitrogen pulses on growth and nitrogen uptake by Bromus tectorum,” Plant Ecology, vol. 158, no. 1, pp. 77–84, 2002. View at Publisher · View at Google Scholar
  24. P. M. Vitousek, L. R. Walker, L. D. Whiteaker, D. Mueller-Dombois, and P. A. Matson, “Biological invasion by Myrica faya alters ecosystem development in Hawaii,” Science, vol. 238, no. 4828, pp. 802–804, 1987. View at Google Scholar
  25. R. El-Ghareeb, “Vegetation and soil changes induced by Mesembryanthemum crystallinum L. in a Mediterranean desert ecosystem,” Journal of Arid Environments, vol. 20, no. 3, pp. 321–330, 1991. View at Google Scholar
  26. P. S. Kourtev, J. G. Ehrenfeld, and W. Z. Huang, “Effects of exotic plant species on soil properties in hardwood forests of New Jersey,” Water, Air, and Soil Pollution, vol. 105, no. 1-2, pp. 493–501, 1998. View at Publisher · View at Google Scholar
  27. R. R. Blank and J. A. Young, “Influence of the exotic invasive crucifer, Lepidium latifolium, on soil properties and elemental cycling,” Soil Science, vol. 167, no. 12, pp. 821–829, 2002. View at Publisher · View at Google Scholar
  28. P. A. Knapp, “Cheatgrass (Bromus tectorum L.) dominance in the Great Basin Desert. History, persistence, and influences to human activities,” Global Environmental Change, vol. 6, no. 1, pp. 37–52, 1996. View at Publisher · View at Google Scholar
  29. R. D. Evans, R. Rimer, L. Sperry, and J. Belnap, “Exotic plant invasion alters nitrogen dynamics in an arid grassland,” Ecological Applications, vol. 11, no. 5, pp. 1301–1310, 2001. View at Google Scholar
  30. J. Belnap and S. L. Phillips, “Soil biota in an ungrazed grassland: response to annual grass (Bromus tectorum) invasion,” Ecological Applications, vol. 11, no. 5, pp. 1261–1275, 2001. View at Google Scholar
  31. J. B. Norton, T. A. Monaco, J. M. Norton, D. A. Johnson, and T. A. Jones, “Soil morphology and organic matter dynamics under cheatgrass and sagebrush-steppe plant communities,” Journal of Arid Environments, vol. 57, no. 4, pp. 445–466, 2004. View at Publisher · View at Google Scholar
  32. B. Von Holle, H. R. Delcourt, and D. Simberloff, “The importance of biological inertia in plant community resistance to invasion,” Journal of Vegetation Science, vol. 14, no. 3, pp. 425–432, 2003. View at Google Scholar
  33. L. G. Bundy and J. J. Meisinger, “Nitrogen availability indices,” in Methods of Soil Analysis. Part 2. Microbiological and Biochemical Properties, R. W. Weaver, S. Angle, P. Bottomley et al., Eds., pp. 951–984, Soil Science Society of America, Madison, Wis, USA, 1994. View at Google Scholar
  34. A. Mubarak and R. A. Olsen, “Immiscible displacement of the soil solution by centrifugation,” Soil Science Society of America Journal, vol. 40, pp. 329–331, 1976. View at Google Scholar
  35. A. Frostegård and E. Bååth, “The use of phospholipid fatty acid analysis to estimate bacterial and fungal biomass in soil,” Biology and Fertility of Soils, vol. 22, no. 1-2, pp. 59–65, 1996. View at Publisher · View at Google Scholar
  36. SAS Institute, Statistical Analysis Software. Version 7, SAS Institute, Cary, NC, USA, 1996.
  37. M. Rejmánek and D. M. Richardson, “What attributes make some plant species more invasive?” Ecology, vol. 77, no. 6, pp. 1655–1661, 1996. View at Google Scholar
  38. R. N. Mack, “Predicting the identity and fate of plant invaders: emergent and emerging approaches,” Biological Conservation, vol. 78, no. 1-2, pp. 107–121, 1996. View at Publisher · View at Google Scholar
  39. E. Grotkopp and M. Rejmánek, “High seedling relative growth rate and specific leaf area are traits of invasive species: phylogenetically independent contrasts of woody angiosperms,” American Journal of Botany, vol. 94, no. 4, pp. 526–532, 2007. View at Publisher · View at Google Scholar
  40. M. B. Mazzola, K. G. Allcock, J. C. Chambers et al., “Effects of nitrogen availability and cheatgrass competition on the establishment of Vavilov Siberian wheatgrass,” Rangeland Ecology and Management, vol. 61, no. 5, pp. 475–484, 2008. View at Publisher · View at Google Scholar
  41. P. R. Premi and A. H. Cornfield, “Effects of copper, zinc, and chromium on immobilization and subsequent re-mobilization of nitrogen during incubation of soil treated with sucrose,” Geoderma, vol. 3, no. 3, pp. 233–237, 1970. View at Google Scholar
  42. S. Jonasson, A. Michelsen, I. K. Schmidt, E. V. Nielsen, and T. V. Callaghan, “Microbial biomass C, N and P in two arctic soils and responses to addition of NPK fertilizer and sugar: implications for plant nutrient uptake,” Oecologia, vol. 106, no. 4, pp. 507–515, 1996. View at Google Scholar
  43. G. M. Shaban, “Further studies on Egyptian soil fungi: succession of sugar and osmophilic fungi in soil amended with five organic substrates,” Mycopathologia, vol. 136, no. 1, pp. 33–40, 1996. View at Google Scholar
  44. A. V. Sturz and B. R. Christie, “Beneficial microbial allelopathies in the root zone: the management of soil quality and plant disease with rhizobacteria,” Soil and Tillage Research, vol. 72, no. 2, pp. 107–123, 2003. View at Publisher · View at Google Scholar
  45. J. W. Paul, E. G. Beauchamp, and J. T. Trevors, “Acetate, propionate, butyrate, glucose, and sucrose as carbon sources for denitrifying bacteria in soil,” Canadian Journal of Microbiology, vol. 35, pp. 754–759, 1989. View at Google Scholar
  46. D. N. Rao and D. S. Mikkelsen, “Effect of acetic, propionic, and butyric acids on young rice seedlings growth,” Agronomy Journal, vol. 69, pp. 923–928, 1977. View at Google Scholar
  47. H. Marschner, Mineral Nutrition of Higher Plants, Academic Press, New York, NY, USA, 1995.
  48. J. G. Ehrenfeld, “Effects of exotic plant invasions on soil nutrient cycling processes,” Ecosystems, vol. 6, no. 6, pp. 503–523, 2003. View at Publisher · View at Google Scholar
  49. S. O. Link, H. Bolton Jr., M. E. Thiede, and W. H. Rickard, “Responses of downy brome to nitrogen and water,” Journal of Range Management, vol. 48, pp. 290–297, 1995. View at Google Scholar
  50. O. Vaartaja, “Responses of Pythium ultimum and other fungi to a soil extract containing an inhibitor with low molecular weight,” Phytopathology, vol. 67, pp. 67–71, 1977. View at Google Scholar