Exploring the residence time of allelochemicals released by plants into different soils, episodic exposure of plants to allelochemicals, and the effects of allelochemicals in the field has the potential to improve our understanding of interactions among plants.
We conducted experiments in India and the USA to understand the dynamics of soil concentrations and phytotoxicity of (±)-catechin, an allelopathic compound exuded from the roots of Centaurea maculosa, to other plants in vitro and in soil. Experiments with single and pulsed applications into soil were conducted in the field. Experimental application of (±)-catechin to soils always resulted in concentrations that were far lower than the amounts added but within the range of reported natural soil concentrations. Pulses replenished (±)-catechin levels in soils, but consistently at concentrations much lower than were applied, and even pulsed concentrations declined rapidly. Different natural soils varied substantially in the retention of (±)-catechin after application but consistent rapid decreases in concentrations over time suggested that applied experimental concentrations may overestimate concentrations necessary for phytotoxicity by over an order of magnitude. (±)-Catechin was not phytotoxic to Bambusa arundinacea in natural Indian soil in a single pulse, but soil concentrations at the time of planting seeds were either undetectable or very low. However, a single dose of (±)-catechin suppressed the growth of bamboo in sand, in soil mixed with organic matter, and Koeleria macrantha in soils from Montana and Romania, and in field applications at 40 µg l−1. Multiple pulses of (±)-catechin were inhibitory at very low concentrations in Indian soil.
Our results demonstrate that (±)-catechin is highly dynamic in natural soils, but is phytotoxic well below natural concentrations measured in some soils and applied at low concentrations in the field. However, there is substantial conditionality in the effects of the allelochemical.
Citation: Inderjit, Pollock JL, Callaway RM, Holben W (2008) Phytotoxic Effects of (±)-Catechin In vitro, in Soil, and in the Field. PLoS ONE 3(7): e2536. https://doi.org/10.1371/journal.pone.0002536
Editor: Michael Somers, University of Pretoria, South Africa
Received: February 24, 2008; Accepted: May 19, 2008; Published: July 2, 2008
Copyright: © 2008 Inderjit et al. This is an open-access article distributed under the terms of the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original author and source are credited.
Funding: This work was supported by the University of Delhi, India; Ministry of Environment and Forests, India; Research Office at The University of Montana, the Aldo Leopold Wilderness Center, the USFS Fire Sciences Laboratory and Rocky Mountain Research Station, the USDA, DoD SERDP, the National Science Foundation, and the Civilian Research and Development Foundation. The funders had no role in study design, data collection and analysis, decision to publish or preparation of the manuscript.
Competing interests: The authors have declared that no competing interests exist.
Allelopathic effects have been attributed to a number of exotic invasive plants  and recent research has also suggested the possibility that some invaders may possess novel chemicals that are more phytotoxic to naïve and non-adapted native plants, soil microbes, or herbivores in the invaded range than adapted species in the invader's native range –. Such biogeographical differences in the effects of phytotoxic, antimicrobial, or defense biochemistry have been proposed as a mechanism for invasion - the “Novel Weapons Hypothesis” –. In this context, the allelopathic effects of the North American invasive weed, Centaurea maculosa Lam. [spotted knapweed, recently suggested to be C. stoebe L. (USDA, NRCS 2007)], have been studied extensively.
Phytotoxic effects have been reported from C. maculosa leaves  and roots  and potentially biologically-active compounds isolated from species in the Centaurea genus include aromatic amines, chromenes, phenols, nonterpenoid lactones, lignins, and triterpenes , . Also, phytotoxic effects of (±)-catechin, a phenolic compound exuded from the roots of C. maculosa (or the separated forms of (−) or (+) catechin), have been demonstrated in vitro, in sand culture, in controlled experiments with field soils, and in the field , – (J. Pollock and W. Holben, unpublished results). (±)-Catechin has also been implicated in the Novel Weapons Hypothesis  (W. He & R.M. Callaway, unpublished data).
However, seemingly similar experiments have not always shown (±)-catechin to have inhibitory effects for all species , . Also, different soil types have been reported to eliminate phytotoxicity of (+)-catechin (one isomer of the (±) combination ), and inhibitory effects vary substantially among target plant species , , . Furthermore, field application of (±)-catechin to soils at the same site and to the same plant species show substantial variation between years (6,22). Even within the same growing season, application of (±)-catechin dramatically reduced the growth of Geum triflorum Pursh in open grassland , but the same concentration had no detectable effect on G. triflorum in soils under Pseudotsuga menzeisii tree canopies several meters away (G.C. Thelen & R.M. Callaway, unpublished results).
Most importantly, whether or not natural soil concentrations of (±)-catechin reach phytotoxic concentrations is questionable. Recent measurements show that concentrations are usually far lower than initially reported, and vary much more spatially and temporally in C. maculosa rhizospheres than earlier reported –. Recent extensive sampling of soil catechin concentrations recorded a mean of 650±450 µg g−1 (1 SD), with 20 out of 20 rhizospheres containing catechin) at one site and at one time in the growing season, but at the same site over six other sampling periods no (±)-catechin was detected, but using an approach with a detection limit of 25 µg g−1  This raises the possibility that (±)-catechin may be released in pulses. At 10 other sites that were sampled only once, but at other times, no (±)-catechin was detected in C. maculosa rhizospheres . Other sampling efforts have detected (±)-catechin in soils more frequently in C. maculosa rhizospheres, but at far lower levels, ranging from 0–1 µg g−1 . These results also suggest that (±)-catechin may be more abundant at some times during the growing season than others. It is important to note that bulk soil concentrations such as these suggest target concentrations for soil experiments, but are not relevant for estimating the phytotoxicity of experimental solutions. This is in part because most soil sampling and analytical techniques result in an “averaging” of the measured concentration of the chemical in bulk soil, not in the soil solution, and the actual spatial distribution of the chemical is likely to be concentrated at the rhizoplane of the exuding roots. Experimental concentrations for (±)-catechin solutions may also be estimated by the concentration of (±)-catechin achieved by root exudation from C. maculosa into solution. For seedlings this has been reported at 0–2.4 µg ml−1 , 5–35 µg ml−1 –, 0–113 µg ml−1  and 83–185 µg ml−1 . These concentrations should be considered rough estimates as in some of these cases the solution was designed to stabilize this highly dynamic chemical, seedlings were not exposed to natural light or natural soils, and seedling exudation may not be comparable to adult exudation.
Variation in the environmental concentrations of a putative allelopathic chemical, and in the results of experimental tests for its toxicity, could be due to many other reasons: use of different experimental chemical concentrations, subtle differences in the age or nature of the chemical applied, natural instability of the chemical in vitro or in situ, the age, size, or health of the target plants, seasonal timing of experimental application or soil collection, soil temperature or moisture, or different analytical or methodological techniques. Furthermore, most plants do not continuously biosynthesize secondary metabolites throughout their life cycle and allelopathic compounds have been shown to be dynamic in soils ,  and in their production . The extreme variation reported for soil (±)-catechin concentrations is probably also affected by oxidation of the molecule, which results in changes in its absorption spectrum  and the exudate's chelating effects on metals to potentially release insoluable phosphates . These factors almost certainly cause experimental concentrations in solutions and substrates to be far lower than those initially applied –, resulting in substantial mismatches between applied experimental and in situ concentrations. Furthermore, although single dose experiments are a crucial step towards understanding the effects of putative allelochemicals in natural settings and may mimic pulsed releases, applying single doses of a biochemical to soil is likely to underestimate the concentration of the chemicals released as exudates over long periods of time.
The possibility of pulsed deliveries of root exudates  raises other questions about experimental protocol. The concentrations of biologically active chemicals that can be detected and measured in soil may vary periodically as plants sporadically vary in the exudation of chemicals (32]. Temporal fluxes in the concentration of allelopathic chemicals have been measured in soils , temporal dynamics have been measured in production , and temporal effects have been modeled , but to our knowledge no studies have attempted to mimic such dynamics in experimental applications.
We focus on three aspects of the effects of (±)-catechin that require better resolution: 1) matching exuded concentrations and measured concentrations in soils to phytotoxicity, 2) determining the potential for low concentrations of (±)-catechin in soil to be phytotoxic, and 3) measuring the fate and effect of pulsed, or dynamic, experimental deliveries. We tackled these issues by conducting Petri dish assays using lower concentrations than tested in the past, making repeated measurements of (±)-catechin in soil after experimental applications, and testing the phytotoxicity of (±)-catechin in different soils, different application concentrations, in pulsed applications, and in the field.
Materials and Methods
In vitro phytotoxicity tests
We first tested the potential of low in vitro concentrations of (±)-catechin to be phytotoxic to our two focal test species, Bambusa arundinacea (bamboo), which is native to India and Koeleria macrantha (Ledeb.) J.A. Schultes, a species native to North America. We chose Bambusa because it is highly abundant in subtropical India and appears to be a dominant competitor in its native range. We chose Koeleria through a random draw from the names of 6 dominant native Montana grass species placed in a hat. Bambusa is from a region in which C. maculosa does not occur. Koeleria occurs in invaded grasslands and we used field collected seeds from areas with low densities of C. maculosa. For each species, 10 seeds were placed on Whatman # 1 filter paper in each of 15 9-cm diameter Petri dishes. For each species, in 5 of these Petri dishes the filter papers were initially wetted with 10 ml of a catechin solution (50 mg of (±)-catechin dissolved in 10 ml of 100% methanol and then diluted in 990 ml HPLC-pure water for a final 50 µg ml−1). In 5 other Petri dishes for each species 10 ml of a 25 µg ml−1 solution was applied. In another 5 Petri dishes for each species only the water/methanol (99∶1 v/v) solution was applied. Several similar studies have demonstrated (±)-catechin phytotoxicity for many different species at higher concentrations than we used , , but we chose these lower concentrations because they were similar to that reported in a recent seedling exudation experiment (Ridenour et al., in press ) and between the concentrations reported by Bais et al. , Weir et al. – and Blair et al. . Petri dishes were sealed with Parafilm, kept at 21–23°C and exposed to a 12∶12 hour day∶night schedule. Root length was measured 12 days after the application of the treatments to the seeds, and treatments were compared for each species using ANOVA and post ANOVA Tukey tests (n = 5).
The potential for (±)-catechin to be phytotoxic at natural soil conditions has been the most controversial aspect of C. maculosa allelopathy, and as discussed above the most difficult to test. Recent extensive measurements show clearly that earlier studies dramatically overestimated natural soil concentrations , , pure (±)-catechin diminishes very rapidly in soils immediately after application , and (±)-catechin appears to occur in C. maculosa rhizospheres in the field in episodic pulses . This creates experimental problems. Applied amounts dramatically overestimate the longer term resident concentrations in soils that target plants experience, but applying the concentrations necessary to achieve low soil concentrations during the course of a multi-day experiment requires exposing target plants to pulses of very high concentrations at the time of application. Such pulses may be experienced in nature, but it is difficult to estimate how often they occur, or the concentrations experienced by the root surfaces of neighboring plants. We approached this problem by combining different experimental approaches including planting seeds well after (±)-catechin application, measuring bulk concentrations in our experimental soils, and conducting experiments in which seeds and seedlings either experienced pulses or did not.
The first two experiments (single pulse and multiple pulses, Indian soil) were conducted in parallel at the University of Delhi and The University of Montana with Indian soil and Bambusa arundinacea (bamboo). India does not have a history of C. maculosa invasion. We therefore assume that soil communities in Indian soil and native Indian plants (e.g. Bambusa) have not experienced (±)-catechin exuded from C. maculosa roots. The effects of (±)-catechin on Bambusa were measured at the University of Delhi. Because the equipment to measure (±)-catechin does not exist at the University of Delhi, soil collected at the same place and time was sent to The University of Montana to explore the relationship between applied (±)-catechin concentrations and extant concentrations in the soil using the same protocol, replication, pots, and experimental conditions in which phytotoxicity was tested. We also explored (±)-catechin dynamics and phytotoxicity in soils from Montana and Romania, and our general intent was simply to ascertain generality, or conditionality, using many different soils.
Blair et al.  used an approach to measure (±)-catechin in soil that was sensitive to low concentrations and often found (±)-catechin in C. maculosa rhizospheres, but never more than 1 µg g−1 soil. Perry et al. , used an approach with a higher detection limit of 25 µg g−1 soil and found detectable levels of (±)-catechin far less frequently, but reported a pulse at a repeatedly measured site averaging 650±450 µg g−1 (1 SD). Previous studies reported higher and more consistent soil concentrations of (±)-catechin, but as discussed in , we do not consider those measurements to be accurate. In experiments we targeted resident soil concentrations at 0–50 µg g−1.
To measure (±)-catechin, 1 g soil was collected in sterile Eppendorf tubes, amended with 1 ml of 100% methanol, briefly mixed by vigorous vortexing, pelleted by centrifugation for 10 min at 13000 rpm, and the supernatant was placed into vials for HPLC analysis . In brief, catechin concentrations were measured by high-pressure liquid chromatography (HPLC) using 15 µL injection volumes with UV detection at 280 nm on a HP series 1100 with a HP ODS Hypersil C18 column (5 µm, 125×4 mm) using a methanol (25% v/v) -phosphoric acid (15 mM) mobile phase at a flow rate of 1 ml/min. This method employs an isocratic elution, which potentially eliminates variability among peak areas that occurs when employing an increasing gradient elution as in other methods , . Also, this technique's limit of detection ranged from 5 µg ml−1 to 3000 µg ml−1 of (±)-catechin for standard solutions dissolved in 100% methanol immediately after preparation, and is therefore an effective methodological approach. Thus, differences measured in applied concentrations of (±)-catechin and concentrations of (±)-catechin in soils are most likely due to transformation of the pure form through chelation, sorption, oxidation, microbial processes, or other unknown soil effects.
Single pulse, Indian soil
In India we collected soil from under native vegetation (sandy loam; pH, 7.7; organic matter, 0.95%) of Delhi, India (Lat., 28.38 N; Long., 77.12 E). This soil has no history of exposure to any Centaurea species. For each of 6 replicates per treatment, 150 g soil was added to a 190 cm3 pot (n = 6 for each treatment) which then was treated with 40 ml of 0 µg, 500 µg, 1000 µg or 1500 µg ml−1 (±)-catechin dissolved in 100% methanol, then diluted to 5% methanol in HPLC-grade water (v/v) designed to apply concentrations of 0 µg, 133 µg, 266 µg and 400 µg (±)-catechin g−1 soil.
Multiple pulses, Indian soil
We dissolved (±)-catechin in 100% methanol and then further diluted it into HPLC-pure water (5∶95 v/v) to obtain final concentrations of 0, 500, 1000 and 1500 µg ml−1. Ten replicates of 50 g soil (the same as in the first experiment) in 50 ml vials were initially treated with 15 ml (day 1) of (±)-catechin (at the 0, 500, 1000 and 1500 µg ml−1 concentrations), and then soils were irrigated three times (days 3, 7, 10) with 5 ml of the appropriate concentration, and one time with 4 ml (day 14) of the solutions. This established treatments in which all replicated vials received 34 ml of solution, and in which a total of 0, 340, 680, or 1020 µg g−1 of (±)-catechin was added to the soil. This application rate saturated the soils with the solutions, but did not leave solution standing on top of the soils. The tubes were incubated under alternating 12-hr light and 12-hr dark period at 22–24°C for 17 days. To determine the stability and maximum accumulated in situ soil concentrations achieved by these applications, we sampled immediately after application, on days 3 and 7, both before and after the day 10 and day 14 applications, and again on day 17. To measure (±)-catechin, a 1 g soil sample was collected from each tube for each measurement and processed for HPLC analysis as outlined above.
Single pulses, North American and European soils
To establish soil concentrations for other experiments we also tested the stability of (±)-catechin in soils where C. maculosa currently occurs, and measured variation in the retention of a single experimentally applied pulse of the compound among soils from different sites. We collected soils from grasslands in which C. maculosa was present, but from the rhizospheres of the most abundant native grasses. Soil samples were collected from 5 sites in Romania, where C. maculosa is native, and 5 sites in Montana where C. maculosa is an aggressive exotic invader. The locations of the Romanian sites were at 47.13 N/26.29 E, 46.5 W, 26.56 E, 47.09 N/27.35 E, 47.10 N/22.52 W, 45.51 N/27.26 E and the locations of the Montana sites were at 46.35 N/112.04 W, 46.51 N/113.59 W, 46.60 N/113.57 W, 46.10 N/113.46 W and 48.52 N/115.03 W.
For each of these 10 sites, we placed 50 g soil into five 50 ml vials and treated them with a single dose of (±)-catechin added in 10 ml of HPLC-grade water. We dissolved (±)-catechin into water by gradually warming the solution to ≈80°C and gently stirring. This new approach is promising as methanol-water solutions do not keep (±)-catechin in solution as long as warmed water (J. Pollock, personal observation) and methanol may have unknown effects on plants. This solution was concentrated at 2,500 µg ml−1 and achieved an initial calculated soil concentration of 500 µg g−1. We began with this high concentration because it is close to the mean concentration of the pulse measured by Perry et al.  and because preliminary experiments indicated that a pulse of this magnitude would be necessary to achieve even trace amounts after several days. Tubes in this experiment were incubated in the dark because sunlight appears to increase the oxidation rate of (±)-catechin (J. Pollock, personal observation). Soil concentrations of (±)-catechin were measured immediately after application and after 1, 3 and 10 days of incubation with the methodology described above. We tested the effects of region (fixed), site (random and nested within region) using a separate ANOVA for each time (fixed) on catechin concentration. We performed these tests using the PROC GLM module within SAS using Type III sum of squares (version 9.1).
Using a subset of these soils (two sites) we also extracted (±)-catechin from the same soils using the methanol solution used by Perry et al.  and the phosphoric acid (0.1% final concentration) solution used by Blair et al.  to test for the possibility that the methanol extraction methodology was failing to extract large portions of (±)-catechin from the soils. Standards of (±)-catechin were also made following Blair et al.  for this test.
Phytotoxicity experiments in soils
Single pulses, Indian soil.
The first experiment conducted with Indian soil and Bambusa was designed to test the effect of single pulses of (±)-catechin, applied at relatively high doses. For each of 6 replicates per treatment, 150 g soil was added to a 190 cm3 pot, and different treatments received 40 ml of 0 µg, 500 µg, 1000 µg or 1500 µg ml−1 (±)-catechin dissolved in 100% methanol, then diluted to 5% methanol in HPLC-grade water (v/v), which was designed to establish treatment concentrations of 0 µg, 133 µg, 266 µg and 400 µg catechin g−1 soil. However, as described in the results these one-time applications resulted in relevant soil treatments for this experiment of undetectable soil concentrations in the control, the 133 µg, and the 266 µg treatments and 60±20 µg g−1 in the 400 µg treatment within an hour after addition. Two days later, equivalent to prior to planting Bambusa seeds, the 60 µg g−1 concentration decreased to a mean concentration of 4.3±2.4 µg g−1 (also see the multiple pulse experiment below). Over the course of the experiment 25 ml of HPLC-grade water was added to each pot to maintain soil moisture. In each of these pots 6 Bambusa seeds were planted and seedling mass was measured 14 days later. Untransformed seedling mass was tested with a single ANOVA using “treatment” and “pot” as fixed factors and to differentiate among specific treatments a post-ANOVA Tukey test was conducted (significance limit at P<0.01; SPSS 15.0 .
When these experiments had ended, the soil treated with (±)-catechin (0, 133, 266 or 400 µg g−1 soil) was analyzed for pH, electrical conductivity (EC), organic carbon (OC), exchangeable phosphate-P, total organic nitrogen (N) and total phenolics after air-drying for 24 hours. Five g of soil was soaked with 25 ml water followed by filtration. One aliquot of the soil filtrate was used to measure pH and EC using a pH and conductivity meter (Metrex, 231-R), while a second part of the filtrate was used to determine total phenolics using Folin and Ciocalteu's phenol reagent . (±)-Catechin is a flavonoid and likely to undergo rapid microbial degradation to yield phenolic acids . Thus, the levels of total phenolics in (±)-catechin-treated soil allowed us to examine whether or not direct degradation products of (±)-catechin, other than oxidized or chelated forms, increase with increasing treatment levels. Soil organic carbon was determined using a chromate titration method  (Piper 1966). To determine phosphate-P, 5 g soil was soaked with 2.5% acetic acid, shaken for 30 min followed by filtration. Exchangeable phosphate-P was determined using the molybdenum blue method (Allen 1989). To determine total organic N, 1 g soil was digested using the Kjeldahl method, and N concentration was determined using indophenol method . All analyses were done using six replicates of soil.
Multiple pulses, Indian soil.
A second experiment was conducted with Indian soil and Bambusa, designed to test the concentrations achieved by pulsing deliveries and adding larger total quantities of (±)-catechin into the soil over time. In this case, we added 50 g soil to each of twenty-four 85 ml vials and replicates of 6 were repeatedly treated with catechin (as described above) at either 500, 1000 or 1500 µg ml−1. An initial application of 15 ml of (±)-catechin at these concentrations was added and then 6 Bambusa seeds were sown 2–5 mm below the surface of the treated soil. Plants were then irrigated 3 more times with 5 ml and one time with 4 ml of each concentration of (±)-catechin over a 14 day period, after which shoot height and mass were measured. Soil treated with a total of 34 ml of 0 µg, 500 µg, 1000 µg or 1500 µg ml−1 (±)-catechin in solution was equivalent to adding 0 µg (control), 340 µg, 680 µg and 1020 µg catechin g−1 soil, but, as described below the measured mean soil concentrations for the course of the experiment achieved were 0, 1.4±1.4 µg (1SE), 14.5±5.8 µg, and 36.1±10.2 µg g−1. (±)-Catechin was not applied directly in contact with the seedlings but to the soil surrounding them, but it is important to note that in order to achieve low soil concentrations, target seedlings were briefly exposed to high concentrations of (±)-catechin during the last three applications. As a control, 6 pots received methanol and distilled water instead of the (±)-catechin solution. Untransformed seedling mass was tested with a single ANOVA using “treatment” and “pot” as fixed factors and to differentiate among specific treatments a post-ANOVA Tukey test was conducted (significance limit at P<0.01; SPSS 15.0 ).
Single pulses, other Indian soils.
Based on prior reports  we reasoned that soil organic matter and other factors could affect the phytotoxicity of (±)-catechin. For this reason, and simply to test the effects of the root exudate in a variety of conditions, a third set of phytotoxicity experiments was conducted to test the effects of low concentrations of (±)-catechin in other soil types. We experimented with the natural sandy loam soil collected in India but enriched with organic material, and natural river sand with virtually no organic matter. In the first experiment, compost (native tree litter was composted for 1 year) was added to the original Indian soil to obtain an organic matter content of 1.5% and the mixture was treated with 0, 133, 266 or 400 µg (±)-catechin g−1 soil. (±)-Catechin solutions were prepared as described above. In another treatment, 50 g of river sand was amended with the same doses of (±)-catechin. Controls were watered with the methanol-distilled water solution. For controls and treatments, seeds were planted two days after treatments were applied to the soils. For each treatment 6 pots were each planted with 6 bamboo seeds. Growth conditions for these treatments were well lit and had an average day/night temperature of 35/25°C, respectively. After 14 days, shoot height and shoot dry weight were measured. We did not measure (±)-catechin concentrations for this experiment, but all applied concentrations were well below the pulse measured by Perry et al.  and measurements reported here for 11 different soil collections indicate that at the time of planting seeds soil concentrations of the compound were far lower than that applied. Statistics were conducted as described for the first two phytotoxicity experiments.
Single pulses, North American and European soils.
We conducted a fourth phytotoxicity experiment by planting Koeleria macrantha seeds into 9 of the 10 soils from Montana and Romania (insufficient soil remained from one of the Romanian sites). The purpose of this experiment was to test for the possibility, suggested in the experiment with the Indian soil, that very low concentrations of (±)-catechin, or (±)-catechin derivatives not evident in measurements of pure (±)-catechin, might also be phytotoxic. This experiment also avoided the problem inherent to the multiple pulse experiment of brief exposure to high concentrations of (±)-catechin at the time of addition. We planted Koeleria in the remaining 42 g (8 of the 50 g had been analyzed for (±)-catechin) of soil at the end of the single pulse, North American and European soils, experiment described above. This exposed seeds and germinating seedlings to concentrations below the detectable limit of 5 µg g−1 for soil from 7 sites, 10±5 µg g−1 for one site and 41±33 µg g−1 for one site. In each of the 5 replicate pots per site we planted 10 seeds of Koeleria (total treatment n = 45 pots, each with 10 seeds). For each of the 9 sites, we also put 42 g of soil that had not been exposed to (±)-catechin into pots (control n = 3 per site; total n = 27 pots) which were also planted with Koeleria. All pots were watered by misting twice per day with tap water for 10 days, after which no new seed emergence was observed. During this period survival of seedlings was recorded and after 10 days pots were no longer watered. Seedling survival was measured for another 11 days after watering ceased. We subjected the seedlings to drought because most in vitro experiments for most plant species have shown that the strongest effect of (±)-catechin is on root elongation; not shoot elongation . We hypothesized that inhibition of root growth might expose seedlings to greater suppression by drought, a factor not yet tested in the context of (±)-catechin phytotoxicity. Survival was compared among treatments using the Kaplan-Meier test followed by log rank (Mantel-Cox), Breslow, and Tarone-Ware comparisons (SPSS 15.0, 2006). We also measured the maximum height attained by seedlings in these treatments and tested the effects of region (fixed), site (random and nested within region) in separate ANOVAs using the PROC GLM module within SAS using Type III sum of squares (version 9.1).
Single pulse, in situ soils.
We conducted a fifth experiment in which we applied (±)-catechin to seedlings in the field at a concentration roughly similar to what accumulates in experimental solutions containing C. maculosa seedlings (see above). We created a solution of 40 µg (±)-catechin ml−1 water by dissolving it in warm water as described above. Three ml of this solution was injected into the rhizospheres of 15 small Koeleria macrantha plants at each of 7 sites in western Montana (46°51′37.22″ N, 113°58′41.24″ W; 46°50′59.75″ N, 113°58′51.82″ W; 46°52′03.83″ N, 113°58′16.45″ W; 46°53′14.42″ N, 113°59′04.80″ W; 46°29′35.83″ N, 114°05′25.25″ W; 46°53′39.74″ N, 113°56′02.84″ W; 46°56′10.91″ N, 113°57′42.20″ W). The 3 ml solution wetted ≈5 g of soil resulting in an estimated initial bulk concentration of ≈24 µg g−1. As shown in the results this likely decreased rapidly. Fifteen other plants at each site were treated with 3 ml of water and used as controls. These solutions were injected into soils using a micropipette on 7–8 April 2007, and at this time the number of leaves was counted. On 28–29 April 2007 the number of leaves was counted again, and the change in leaf number was recorded. Change in leaf number was analyzed with ANOVA with treatment as a fixed factor and site as a random factor ((SPSS 15.0, 2006).
In vitro phytotoxicity tests
(±)-Catechin significantly inhibited the root growth of Bambusa and Koeleria seedlings at 50 µg ml−1 but not at 25 µg ml−1 (Fig. 1; ANOVA for Bambusa, Ftreatment = 6.55; df = 2,15; P = 0.012. ANOVA for Koeleria, Ftreatment = 4.97; df = 2,15; P = 0.027). We noted that the (±)-catechin solutions in the Petri dishes appeared to be oxidized (having a red-rust or brown color), indicating that the seedlings in this experiment may have been exposed to concentrations of non-oxidized (±)-catechin that were lower, during most of the duration of the experiment, than the solutions prepared and applied at the onset of the experiment.
Single pulses, Indian soil.
In the first experiment, single pulse applications of 0 (control) µg, 133 µg, 266 µg and 400 µg g−1 of (±)-catechin resulted in soil levels that were not detectable one hour later in the control or the two lowest application rates, and 60±20 (1SE) µg g−1 in the highest application rate. Two days later the latter had declined to a mean concentration of 4.3±2.4 µg g−1.
Multiple pulses, Indian soil.
The detected concentrations of (±)-catechin added in repeated pulses to the sandy loam soils from India were also far lower than the applied amounts of (±)-catechin added to the soil (Fig. 2). No (±)-catechin was observed in control soils, and the treatment calculated to add a total of 340 µg (±)-catechin g−1 of soil also resulted in zero (±)-catechin detected at all times but one, in which we detected 11.4±4.5 µg g−1 immediately after application at day 7. The 680 µg g−1 soil (±)-catechin application resulted in a mean of 14.5±5.8 and a maximum of 47.8±20.2 µg g−1 immediately after application on day 7. The 1020 µg (±)-catechin application g−1 of soil produced a maximum of 77.3±30.9 µg g−1 in the soil immediately after application on day 7 and an average across all measurements of 36.1±10.2 µg g−1 (±)-catechin in the soil. High soil (±)-catechin concentrations were always associated with measurements taken as soon as possible after application; whereas when measured 3–4 days after application of (±)-catechin, the highest concentration detected was 10 µg g−1. Most other measurements at these times were zero. In general, low readings of (±)-catechin corresponded to the development of red-brown coloration of the soil, suggesting that at least a component of the (±)-catechin loss was due to oxidation.
Values on x-axis denote the days on which sampling was conducted. In detail, “10” and “14” denote sampling prior to the application of (±)-catechin pulses on those days, and “10.2” and “14.2” denote sampling two hours after application. The total (±)-catechin delivered to these soils over all pulses was 0, 340, 680, or 1020 µg g−1. The single error bar shown indicates the largest 1 SE.
Single pulses, North American and European soils.
Soil concentrations measured immediately after application of (±)-catechin in the 5 soils from Montana and the 5 soils from Romania were highly variable, ranging from almost zero for one Montana soil to mean concentrations that were ≈200 µg g−1 higher than the calculated application rate of 500 µg g−1 (Fig. 3). After 1 day, the mean (±)-catechin concentration for all 10 soils was 126±34 µg g−1 soil and the concentration decreased to a range of 0–41±33 µg g−1 among the 10 soils 10 days after application. In an ANOVA, the effect of continent (fixed) was not significant (F = 2.298; df = 1,8; P = 0.204); the effect of site (nested, random) was not significant (F = 1.224; df = 8,4; P = 0.424), but the effect of time (fixed) after application was highly significant ((F = 10.535; df = 4,160); P<0.001). The high concentrations early in the time series indicate that our extraction protocol was effective for these soils, and the high degree of variation within sites, and the very high initial spike in one soil, was likely due to the variation in clay and silt fractions in soil and uneven dispersion of the applied (±)-catechin or differences in soil chemistry. The phosphoric acid extraction protocol used by Blair et al. , with which they reported the highest recovery of experimentally applied (±)-catechin, coupled with our HPLC detection protocol, extracted even less (±)-catechin in the two soils for which we compared the methods. Also, standards made using methods described by Blair et al.  also demonstrated a decrease in sensitivity for (±)-catechin (data not shown). For soils from Breazu, Romania, the methanol extraction recovered 17.0±10.0 (1 SE) µg g−1 10 days after application, whereas the phosphoric acid and methanol extraction recovered 4.3±2.9 µg g−1. For soils from Nelson Gulch, Montana 7.4±7.2 µg g−1 (±)-catechin was recovered using the methanol extraction but no (±)-catechin was recovered using the phosphoric acid and methanol extraction.
Phytotoxicity experiments in soils
Single pulses, Indian soil.
In the first experiment, in which application rates of 0 (control), 133, 266 and 400 µg g−1 of (±)-catechin could not be detected in the control and two lowest application rates, and was measured at 4.3±2.4 µg g−1 at the time seeds were planted, we saw no effect of (±)-catechin on the shoot mass of Bambusa at any application rate (data not shown).
Multiple pulses, Indian soil.
In the second experiment, designed to test the effect of pulsing larger quantities of (±)-catechin into the soil, applications of total amounts of 0 (control), 340, 680 and 1020 µg g−1 of (±)-catechin achieved mean measured concentrations over the course of the experiment of 1.4±1.4 (1SE), 14.5±5.8, and 36.1±10.2 µg g−1, respectively, in soils (Fig. 3). However, even at these very low soil concentrations, significant phytotoxicity was observed for shoot mass of Bambusa at 1.4±1.4, 14.5±5.8, and 36.1±10.2 µg g−1 µg g−1 (Fig. 4). It is important to note; however, that seeds and seedlings were briefly exposed to higher concentrations of (±)-catechin each time a pulse was added.
The x axis shows total measured concentrations of (±)-catechin below the bars and the applied concentrations in parentheses. Bars show 1 SE and shared letters indicate no significant difference among means as determined by ANOVA with treatment and pot as fixed variables and post-ANOVA Tukey tests; P<0.05.
The pH of soil treated with 133 (7.99±0.10), 266 (7.65±0.01) or 400 (7.93±0.08) µg catechin g−1 soil was significantly higher when compared to untreated (7.23±0.03) soil. The applied concentrations of catechin, however, did not influence conductivity, organic carbon, available phosphorus, or total organic N (data not shown). Even though the detected concentrations of (±)-catechin were far lower than the applied amounts, a significant increase in total phenolics was observed when soil was treated with repeated pulses of (±)-catechin. However, total phenolic concentrations were much lower than would be expected from the total added amounts of (±)-catechin. In control soils total phenolics equaled 3.6±0.3 µg g−1; when 133 µg g−1 of (±)-catechin was added to the soil 16.2±0.6 µg g−1 total phenolics were recovered; when 266 µg g−1 of (±)-catechin was added to the soil 23.4±0.4 µg g−1 total phenolics were recovered; and when 400 µg g−1 of (±)-catechin was added to the soil 36.1±0.5 µg g−1 of total phenolics were recovered.
Single pulses, other Indian soils.
In the third experiment, in which (±)-catechin was applied to sand or to the Indian soil enriched with organic matter at 0, 133, 266 or 400 µg g−1, and seeds were planted two days later, we observed inhibition of shoot mass of Bambusa in both substrates at applied rates of 266 µg g−1 and higher (Fig. 5). We did not measure (±)-catechin concentrations in the sand or soil plus organic matter treatments but all applied concentrations were lower than the in situ soil pulse measured by Perry et al.  and results from all other substrates tested here suggest that the amounts of (±)-catechin in these soils at the time of planting was much lower than the applied dose.
Single pulses, North American and European soils.
In the fourth experiment with soils from Montana and Romania, when seeds were planted after (±)-catechin concentrations had been allowed to decline for 12 days (see Fig. 3), treatment of the soils with (±)-catechin corresponded with significantly lower seedling emergence, height, and survival (Figs. 6, 7). Planted 12 days after (±)-catechin application, and after soil concentrations had decreased to low or undetectable levels, seedling emergence of Koeleria was inhibited significantly in 5 of the 9 soils and seedling height was reduced in 3 of the 9 soils. Using an ANOVA model with untransformed data (the means for each pot), with continent and treatment as fixed variables and site as a random variable, only the effect of (±)-catechin treatment was significant for emergence (F = 64.12; df = 1,54; P = 0.004) and for height (F = 32.55; df = 1,40; P = 0.0011). Furthermore, the survival of Koeleria seedlings in the (±)-catechin treatment decreased much faster after being exposed to drought than seedlings in control soils (Fig. 7). Kaplan-Meier Survival Analysis demonstrated significantly lower survival among Koeleria seedlings exposed to drought in the (±)-catechin treatment than in the control (Log-rank Chi-square = 7.224; df = 1; P = 0.007; Breslow Chi-square = 3.297; df = 1; P = 0.069; Tarone-Ware Chi-square = 4.703; df = 1; P = 0.030).
(±)-Catechin had been added to the soil 12 days prior to sowing seeds, and the numbers below the bars show the concentration in the soil two days before adding seeds. Error bars show 1 SE and asterisks denote significant differences between treatments at a particular site as determined by separate t-tests. The analysis from the complete ANOVA model is presented in the results.
(±)-Catechin had been added to the soil 12 days prior to sowing seeds, and no (±)-catechin was applied during the time course shown here. Results from all nine sites are combined. The arrow on the graph denotes when watering was stopped, and afterwards seedlings were exposed to increasingly drier soils. Kaplan-Meier survival analysis and Chi-square analyses are presented in the results.
Single pulse, in situ soils.
The mean leaf growth of the control plants in the field experiment was 2.90±0.16 (1 SE) leaves per plant versus 2.45±0.15 for the plants treated with (±)-catechin (Figure 8). A subsample of soils collected immediately after application demonstrated no detectable (±)-catechin. Based on separate t-tests, there was no significant effect of (±)-catechin addition at any single site, but the overall treatment effect was significant (ANOVA, Ftreatment = 8.86; df = 1,196; P = 0.025, Fsite = 3.09; df = 6,196; P = 0.098).
Error bars show 1 SE. We tested the effects of (±)-catechin on growth across all sites (n = 15 in each treatment at each site) with a two way ANOVA, with (±)-catechin as a fixed factor and site as a random factor (SPSS 15.0, SPSS, Chicago). ANOVA, Ftreatment = 8.86; df = 1,196; P = 0.025, Fsite = 3.09; df = 6,196; P = 0.098).
Our results demonstrated phytotoxicity for (±)-catechin at low concentrations in Petri dishes and in soils. In some cases we measured toxicity when (±)-catechin concentrations were below the 5 µg g−1 detection limit of our protocol. We also measured phytotoxicity in Indian soils amended with organic matter, river sand, and in situ field experiments in Montana applying concentrations within the range produced in vitro by C. maculosa seedlings. Collectively, these results provide a significant step towards understanding the role of catechin in the natural environment and understanding allelopathy in general. A large number of other studies have demonstrated phytotoxicity of (±)-catechin in vitro and in sand cultures –, , –, , in experiments with field soils ,  and in field applications , , , and our results help to put toxicity into the context of natural soil concentrations (±)-catechin and amounts exuded by seedlings.
We do not know the reason for the disparity between our results for (±)-catechin phytotoxicity (and those cited above that show phytotoxicity) and experiments that have not , , , but there are several possibilities worth considering. First, the rate at which different forms of catechin oxidize could lead to substantial differences if the oxidized forms are not toxic or if other forms are more toxic. Our non-quantified observations suggest that oxidation of (±)-catechin appears to be affected by exposure to light, the presence of seeds in the solution, contaminants in containers, different sources of the water used for the solution, and time. We also found that (±)-catechin was more toxic in some soils than would be estimated from its effects in solutions in vitro. This raises the possibility that some chelated forms of (±)-catechin, perhaps with different metals, may be more phytotoxic than the pure form, and we are currently exploring this possibility. Regardless, because (±)-catechin oxidizes and chelates rapidly, applied concentrations are a poor benchmark for phytotoxicity, substantially overestimating the concentration of (±)-catechin required for phytotoxicity in vitro and in the field. Furthermore, soil texture modifies allelopathic expression  and organic matter may affect the biological effects of compounds by coating metal surfaces and preventing compounds from coming into contact with mineral ions, thus slowing the rate of oxidation  or chelation processes. Microbial mineralization or decomposition to non-toxic forms ,  may also affect the dynamics of allelochemicals in soils. For example, Acinetobacter calcoaceticus bacteria use catechins as carbon sources .
For a number of different soils and experimental conditions we demonstrated phytotoxicity of (±)-catechin at and soil concentrations approaching that detected in the field by Blair et al.  are far below the pulse reported by Perry et al. . Variation in the phytotoxicity of any allelochemical can be affected by differences in extraction methodology, analytical techniques, variation in the rates of chemical degradation, and the vagaries of experimental application procedures . Therefore it is not surprising that substantial variation has been found among experiments. However, it is important to note in this context that we found that known amounts of (±)-catechin experimentally added to soils were dramatically reduced to very low, or even undetectable levels (<5 µg g−1) but still produced phytotoxic effects in some soils, including our field tests. It is not clear if “pure” (±)-catechin itself is phytotoxic at such low levels, but in vitro experiments suggest this is not the case. We may not have detected all (±)-catechin in our test soils, but our repeated measurements of (±)-catechin dynamics in some soils and comparative extraction protocols demonstrate that we were unlikely to have missed large amounts. On the other hand there might have been phytotoxic effects of chelated forms of catechin or other degradation products as well as (±)-catechin itself. The total phenolic content of soils amended with 0, 340, 680 0r 1020 µg catechin/Indian soil was 3.6±0.6, 16.2±1.62, 23.3±0.8 and 36.1±0.9 µg/g soil, respectively. Research by Furubayashi et al.  indicates that the degradation products, tested in one soil type, of the+form of catechin are much less toxic than the pure form in vitro, but they used lettuce as a target species, which is unusually resistant to (±)-catechin, relative to many native North American species .
Our results also demonstrate the potential for drought to interact with the effects of (±)-catechin (see ). Such allelopathy-by-environment interactions are commonly overlooked, but have the potential to cause substantial variation in allelopathic experiments. In summary, our results clearly demonstrate that (±)-catechin has the potential to play an important ecological role in the invasion of Centaurea maculosa in North America and support the Novel Weapons Hypothesis.
Inderjit acknowledges S. Kaushik, S. Mangla and R. Kaur for their help in the laboratory. We thank B. K. Ehlers and anonymous reviewers for their constructive comments on the previous version of the manuscript.
Conceived and designed the experiments: I JP RC WH. Performed the experiments: I JP RC. Analyzed the data: I JP RC WH. Contributed reagents/materials/analysis tools: I WH. Wrote the paper: I JP RC WH.
- 1. Hierro JL, Callaway RM (2003) Allelopathy and exotic plant invasion. Plant Soil 256: 25–39.
- 2. Callaway RM, Aschehoug ET (2000) Invasive plant versus their new and old neighbors: a mechanism for exotic invasion. Science 290: 521–523.
- 3. Mallik AU, Pellissier F (2000) Effects of Vaccinium myrtillus on spruce regeneration: testing the notion of coevolutionary significance of allelopathy. J Chem Ecol 26: 2197–2209.
- 4. Vivanco JM, Bais HP, Stermitz FR, Thelen GC, Callaway RM (2004) Biogeographical variation in community response to root allelochemistry: novel weapons and exotic invasion. Ecol Lett 7: 285–292.
- 5. Cappuccino N, Arnason JT (2006) Novel chemistry of invasive exotic plants. Biol Lett 2: 189–193.
- 6. Thorpe A (2006) Biochemical effects of Centaurea maculosa on soil nutrient cycles and plant communities. PhD Dissertation. University of Montana, Missoula.
- 7. Callaway RM, Cipollini D, Barto K, Thelen GC, Hallett SG, et al. (2008) Novel weapons: invasive plant root exudates suppress fungal mutualisms in America but not in its native Europe. Ecology 89: 1043–1055.
- 8. Stinson KA, Campbell SA, Powell JR, Wolfe BE, Callaway RM, et al. (2006) Invasive plant suppresses the growth of native tree seedlings by disrupting belowground mutualisms. PLoS Biology 4: e 140. DOI: 10. 1371/Journal. pbio. 0040140.
- 9. Callaway RM, Ridenour WM (2004) Novel weapons: invasive success and the evolution of increased competitive ability. Front Ecol Environ 2: 436–443.
- 10. Callaway RM, Hierro JL, Thorpe AS (2005) Evolutionary trajectories in plant and soil microbial communities: Centaurea invasions and the geographic mosaic of coevolution. In: Sax DF, Gaines SD, Stachowicz JJ, editors. Exotic species invasions: insights into ecology, evolution and biogeography. Sunderland, MA: Sinauer. pp. 341–363.
- 11. Rabotnov TA (1982) Importance of the evolutionary approach to the study of allelopathy. Ékologia No. 3, May–June: 5–8. Translated from Russian.
- 12. Kelsey RG, Locken LJ (1987) Phytotoxic properties of cnicin, a sesquiterpene lactone from Centaurea maculosa (spotted knapweed). J Chem Ecol 13: 19–33.
- 13. Ridenour WM, Callaway RM (2001) The relative importance of allelopathy in interference: the effects of an invasive weed on a native bunchgrass. Oecologia 126: 444–450.
- 14. Marco JA, Sanz JF, Sancenon SA, Fustaiyan A, Saberi M (1992) Sesquiterpene lactones and lignans from Centaurea species. Phytochemistry 31: 3527–3530.
- 15. Huneck S, Jakupovic J, Schuster A (1986) Weitere inhaltsstoffe aus Centaurea stoebe (Further compounds from Centaurea stoebe). Planta Med 5: 343–532.
- 16. Buta JG, Lusby WR (1986) Catechins as germination and growth inhibitors in lespedeza seeds. Phytochemistry 25: 93–95.
- 17. Bais HP, Walker TS, Stermitz FR, Hufbauer R, Vivanco JM (2002) Enantiomeric-dependant phytotoxic and antimicrobial activity of (±)-catechin: a rhizosecreted racemic mixture from spotted knapweed. Plant Physiol 128: 1173–1179.
- 18. Bais HP, Vepachedu R, Gilroy S, Callaway RM, Vivanco JM (2003) Allelopathy and exotic plant invasion: from molecules and genes to species interactions. Science 301: 1377–1380.
- 19. Weir TL, Bais HP, Vivanco JM (2003) Intraspecific and interspecific interactions mediated by a phytotoxin, (-)-catechin, secreted by the roots of Centaurea maculosa (spotted knapweed). J Chem Ecol 29: 2379–2394.
- 20. Weir TL, Bais HP, Stull VJ, Callaway RM, Thelen GC, et al. (2006) Oxalate contributes to the resistance of Gaillardia grandiflora and Lupinus sericeus to a phytotoxin produced by Centaurea maculosa. Planta 223: 785–795.
- 21. Iqbal Z, Hiradate S, Noda A, Isojima S, Fujii Y (2003) Allelopathic activity of buckwheat: isolation and characterization of phenolics. Weed Sci 51: 657–662.
- 22. Perry LG, Johnson C, Alford ÉR, Vivanco JM, Paschke MW (2005a) Screening of grassland plants for restoration after spotted knapweed invasion. Restor Ecol 13: 725–735.
- 23. Thelen GC, Vivanco JM, Newingham B, Good W, Bais HP, et al. (2005) Insect herbivory stimulates allelopathic exudation by an invasive plant and the suppression of natives. Ecol Lett 8: 209–217.
- 24. D'Abrosca B, Dellagreca M, Fiorention A, Isidori M, Monaco P, et al. (2006) Chemical constituents of the aquatic plant Schoenoplectus lacustris: evaluation of phytotoxic effects on the green alga Selenatrum capricornutum. J Chem Ecol 32: 81–96.
- 25. Furubayashi A, Hiradate S, Fujii Y (2007) Role of catechol structure in the adsorption and transformation reactions of L-Dopa in soils. J Chem Ecol 33: 239–250.
- 26. Simões KJ, Du FS, Kretzshmar CD, Broeckling , Stermiz FS, et al. (2008) Phytotoxic catechin leached by seeds of the tropical weed Sesbania virgata. J Chem Ecol 34: 681–687.
- 27. Inderjit , Seastedt TR, Callaway RM, Pollock JL, Kaur J (2008) Allelopathy and plant invasions: traditional, congeneric, and biogeographical approaches. Biol Inv. DOI 10.1007/s10530-008-9239-9.
- 28. Blair AC, Hanson BD, Brunk GR, Marrs RA, Westra P, et al. (2005) New techniques and findings in the study of a candidate allelochemical implicated in invasion success. Ecol Lett 8: 1039–1047.
- 29. Blair AC, Nissen SJ, Brunk GR, Hufbauer RA (2006) A lack of evidence for an ecological role of the putative allelochemical (±)-catechin in spotted knapweed invasion success. J Chem Ecol 32: 2327–2331.
- 30. Perry LG, Thelen GC, Ridenour WM, Callaway RM, Paschke MW, et al. (2007) Concentrations of the allelochemical (+/−)-catechin in Centaurea maculosa soils. J Chem Ecol 33: 2337–2344.
- 31. Ridenour WM, Vivanco JM, Feng Y, Horiuchi , Callaway RMNo evidence for tradeoffs: Centaurea plants from America are better competitors and defenders than plants from the native range. Ecology. In press.
- 32. Weidenhamer JD (2005) Biomimetic measurement of allelochemical dynamics in the rhizosphere. J Chem Ecol 31: 221–236.
- 33. Alford ÉR, Perry LG, Qinc B, Vivanco JM, Paschke MW (2007) A putative allelopathic agent of Russian knapweed occurs in invaded soils. Soil Biol Biochem 39: 1812–1815.
- 34. Huang Z, Haig T, Wu H, An M, Pratley J (2003) Correlation between phytotoxicity on annual ryegrass (Lolium rigidum) and production dynamics of allelochemicals within root exudates of an allelopathic wheat. J Chem Ecol 29: 2263–2279.
- 35. Thorpe AS, Archer V, Deluca TH (2006) The invasive forb, Centaurea maculosa, increases phosphorus availability in Montana grasslands. Appl Soil Ecol 32: 118–122.
- 36. Appel HM (1993) Phenolics in ecological interactions: the importance of oxidation. J Chem Ecol 19: 1521–1552.
- 37. Inderjit (2001) Soils: environmental effect on allelochemical activity. Agron J 93: 79–84.
- 38. Inderjit (2005) Soil microorganisms: an important determinant of allelopathic activity. Plant Soil 53: 97–104.
- 39. An M, Johnson IR, Lovett JV (2002) Mathematical modelling of residue allelopathy: the effects of intrinsic and extrinsic factors. Plant Soil 246: 11–22.
- 40. Rudrappa T, Bonsall J, Gallagher JL, Seliskar DM, Bais HP (2007) Root-secreted allelochemical in the noxious weed Phragmites australis deploys a reactive oxygenspecies response and microtubule assembly disruption to execute rhizotoxicity. J Chem Ecol 33: 1898–1918.
- 41. Paveto C, Güida MC, Esteva MI, Martino V, Coussio J, et al. (2004) Anti-Trypanosoma cruzi activity of green tea (Camellia sinensis) catechins. Antimicrob Agents Chemother 48: 69–74.
- 42. Perry LG, Thelen GC, Ridenour WM, Weir TL, Callaway RM, et al. (2005b) Dual role for an allelochemical: (±)-catechin from Centaurea maculosa root exudates regulates conspecific seedling establishment. J Ecol 93: 1126–1135.
- 43. SPSS Inc. (2006) SPSS Base 15.0 for Windows User's Guide. Chicago, IL: SPSS Inc.
- 44. Swain T, Hillis WE (1959) The phenolic constituents of Prunus domestica L. - the quantitative analysis of phenolic constituents. J Sci Food Agric 10: 63–68.
- 45. Arunachalam M, Mohan N, Mahadevan A (2003) Cloning of Acinetobactor calcoaceticus chromosomal region involved in catechin degradation. Microbiol Res 158: 37–46.
- 46. Piper CS (1966) Soil and plant analysis. Bombay, India: Hans Publishers.
- 47. Allen SE (1989) Chemical analysis of ecological materials. London: Blackwell.
- 48. Inderjit , Dakshini KMM (1994) Allelopathic effects of Pluchea lanceolata (Asteraceae) on characteristics of four soils and growth of mustard and tomato. Am J Bot 81: 799–804.
- 49. Djurišić AB, Lau TW, Lam LSM, Chan WK (2004) Influence of atmospheric exposure of tris (8-hydroxyquinoline) aluminum (Alq3): a photoluminescence and absorption study. Appl Physiol 78: 375–380.
- 50. Inderjit , Callaway RM, Vivanco JM (2006) Plant biochemistry helps to understand invasion ecology. Trends Plant Sci 11: 574–580.
- 51. Pedrol N, Gonzales L, Reigosa MJ (2006) Allelopathy and biotic stress. In: Regiosa MJ, Pedrol N, Gonzales L, editors. Allelopathy: a physiological process with ecological implications. Netherlands: Springer. pp. 171–209.