Introduction
The high fecundity of Palmer amaranth (Amaranthus palmeri S. Watson) (Korres Reference Korres2018; Korres and Norsworthy Reference Korres and Norsworthy2017) and waterhemp [Amaranthus tuberculatus (Moq.) J. D. Sauer] (Hartzler et al. Reference Hartzler, Battles and Nordby2004; Heneghan and Johnson Reference Heneghan and Johnson2017) and the relatively high frequency of evolving herbicide resistance (Heap Reference Heap2017; Jhala et al. Reference Jhala, Sandell, Rana, Kruger and Knezevic2014; Molin et al. Reference Molin, Nandula, Wright and Bond2016; Vencill et al. Reference Vencill, Grey, Culpepper, Gaines and Westra2008) are major reasons why these species have become two of the most problematic weeds in U.S. cropping systems (Riar et al. Reference Riar, Norworthy, Steckel, Stephenson, Eubank and Scott2013; Webster and Nichols Reference Webster and Nichols2012). The excessive proliferation of these species can rapidly enrich the soil seedbank, the persistence of which is the driving force for future weed infestations in agricultural production systems. Seed persistence in soil seedbanks counteracts the effects of unfavorable environmental conditions for seed germination over long periods (Gutterman Reference Gutterman1994; Holmgren et al. Reference Holmgren, Stapp, Dickman, Gracia, Graham, Gutierrez, Hice, Jaksic, Kelt, Letnic, Lima, Lopez, Meserve, Milstead, Polis, Previtali, Richter, Sabate and Squeo2006) and increases the possibility that viable seeds are available when conditions for seed germination and seedling recruitment are optimal (Holmgren et al. Reference Holmgren, Stapp, Dickman, Gracia, Graham, Gutierrez, Hice, Jaksic, Kelt, Letnic, Lima, Lopez, Meserve, Milstead, Polis, Previtali, Richter, Sabate and Squeo2006).
Weed species that form persistent seedbanks are a concern for future weed management. The persistence of viable seeds in the soil seedbank depends on a wide range of interacting biotic and abiotic factors. These include germination cues, seed dormancy, seed size (Honda Reference Honda2008; Hulme Reference Hulme1998; Ooi et al. 2007; Thompson et al. Reference Thompson, Green and Jewels1994), physiological age, predation, and microbial decay, along with environmental conditions, burial depth, and burial duration (Davis et al. Reference Davis, Renner and Gross2005; Liebman et al. Reference Liebman, Mohler and Staver2001). High mortality occurs at the seed stage owing to high seed losses and fatal germination (i.e., the condition wherein seeds germinate but fail to emerge) (Cavers Reference Cavers1983; Forcella Reference Forcella2003; Forcella et al. Reference Forcella, Wilson, Renner, Dekker, Harvey, Alm, Buhler and Cardina1992). Consequently, reducing the number of germinable seeds will decrease the number of individuals that will be subjected to weed management operations and the number of escapees that could replenish the soil seedbank. Longevity of seeds in the soil is the most determinant factor for the success of this approach.
The first crucial phase in the formation of a persistent soil seedbank is burial (Fenner and Thompson Reference Fenner and Thompson2005). Whether buried seeds contribute to soil seedbank persistence and consequently to weed population regeneration depends mainly on the depth from which the seeds are able to germinate (Baker Reference Baker1989). The persistence and viability of some weed species after long burial periods is well documented (Conn et al. Reference Conn, Beattie and Blanchard2006; Telewski and Zeevaart Reference Telewski and Zeevaart2002). However, the majority of weed species lose seed viability at relatively short periods after burial (Burnside et al. Reference Burnside, Wilson, Weisberg and Hubbard1996; Conn et al. Reference Conn, Beattie and Blanchard2006; Egley and Chandler Reference Egley and Chandler1983; Lutman et al. Reference Lutman, Cussans, Wright, Wilson, Wright and Lawson2002), particularly small-sized seeds such as A. palmeri (Jha et al. Reference Jha, Norsworthy and Garcia2014; Sosnoskie et al. Reference Sosnoskie, Webster and Culpepper2013), which are more likely to become buried (Peart Reference Peart1984; Thompson et al. Reference Thompson, Green and Jewels1994). Omami et al. (Reference Omami, Haigh, Medd and Nicol1999) found changes in redroot pigweed (Amaranthus retroflexus L.) viability for seeds placed on the soil surface compared with seeds buried at various depths up to 10 cm. He reported that the decline in viability was most rapid for the seeds on the soil surface compared with buried seeds. Schweizer and Zimdahl (Reference Schweizer and Zimdahl1984) discussed the persistence of Amaranthus species seedbank due to longevity of seeds, which, based on the literature, seems to vary considerably from a 12-mo period (Horng and Leu 1974; Omami et al. Reference Omami, Haigh, Medd and Nicol1999) up to 4 (Jha et al., Reference Jha, Norsworthy and Garcia2014; Steckel et al. Reference Steckel, Sprague, Stoller, Wax and Simmons2007), 10 (Burnside et al. Reference Burnside, Fenster, Evetts and Mumm1981; Toole and Brown Reference Toole and Brown1946), or even 40 yr (Kivilaan and Bandurski Reference Kivilaan and Bandurski1981; Quick Reference Quick1961).
Recent research has sought to address the influence of climate in relation to plant biological characteristics on the establishment and persistence of plant populations (Scott et al. Reference Scott, Webber, Murphy, Ota, Kriticos and Loechel2014). As stated by Ooi (Reference Ooi2012), expanding our knowledge of the response and adaptability of seedbanks to environmental and climatic factors will provide the basis for accurate predictions of species occurrence and future distribution, especially in ecosystems that are exposed to temporarily irregular disturbances.
As mentioned previously, the persistence of viable seeds in the seedbank is affected by a wide range of interacting biotic and abiotic factors that in turn depend on the position of seeds in the soil profile (Omami et al. Reference Omami, Haigh, Medd and Nicol1999) and geographic location (Warr et al. Reference Warr, Thompson and Martin Kent1993). Knowledge of the effects of burial depth and burial duration on long-term seed viability and, subsequently, seedbank persistence of A. palmeri and A. tuberculatus populations originating from different locations and dispersed among diverse regions with different soil and climatic conditions can be used for the development of efficient weed management approaches. This is of particular interest given the high fecundity of both species and their high seedbank replenishment potential.
The aim of this study, therefore, was to assess A. palmeri and A. tuberculatus seed persistence at two soil burial depths over a 3-yr period at various locations by testing the following hypotheses: (1) Was seed viability of A. palmeri and A. tuberculatus affected when seeds were exposed to diverse soil surface and subsurface environments at different experimentation sites? (2) Was seed viability of A. palmeri and A. tuberculatus, hence seedbank persistence of these species, reduced as burial depth and burial duration increased?
Materials and Methods
Seed Material and Seedbank Establishment
Seeds of A. palmeri and A. tuberculatus ecotypes, originating from five different locations (i.e., A. palmeri from Arkansas, Indiana, Missouri, Nebraska, and Tennessee; A. tuberculatus from Indiana, Missouri, Nebraska, Ohio, and Wisconsin), were collected as they matured between mid-September to late October 2013 and sent to the University of Arkansas, Fayetteville, for further processing. Approximately 1 mo after the plant material was collected, a cleaned seed sample from each seed lot was sent to seven experimental sites (i.e., Arkansas, Illinois, Indiana, Mississippi, Missouri, Tennessee, and Wisconsin) for the establishment of the seed burial trials (Figure 1).
Experimental sites across Midsouth United States, where Amaranthus palmeri and Amaranthus tuberculatus seed material was exposed to burial trials for a period of 1 to 3 yr before viability test evaluation. Numbers in parentheses represent the latitude and longitude of the experimental sites.
At each site, seeds of each species under investigation were buried using polyethylene mesh bags (64 cm2), with 500-micron pore openings (Elko Filtering, Miami, FL). More specifically, 100 seeds from each seed lot were counted and thoroughly mixed with approximately 20 g of soil collected from the burial site and known to be free of both weeds. Soil placed in the bags was sieved though a 1.4-mm (14 mesh) screen to ensure that no alien seeds would be enclosed in the polyethylene bag. The use of the polyethylene bags, particularly for weeds with small-sized seeds such as A. palmeri and A. tuberculatus, ensures that seeds could be retrieved on any sampling occasion. Wijayratne and Pyke (Reference Wijayratne and Pyke2012) adopted the same approach when investigating the persistence of the small-sized seeds of big sagebrush (Artemisia tridentata Nutt.).
Soil was excavated at each experimental site to a 15-cm depth, and polyvinyl chloride (PVC) plastic cylindrical pipe cages (60-cm diameter by 17.5-cm height with openings at both ends; Figure 2) were placed in the opening and filled with excavated soil after installation of the polyethylene bags within the cage. One polyethylene bag containing seeds from one location of origin and one species (one ecotype) was placed in each cage at the 15-cm depth. Polyethylene bags were also placed at the soil surface (0 cm) after the cage was filled with excavated soil, for a total of 10 polyethylene bags. The remaining 2.5 cm of the rim of the cage remained above the soil surface to prevent off-site movement of seed-containing bags but also to ensure that potential stagnant water could percolate through the soil profile. The cages were covered with wire mesh to prevent possible damage of seed bags by rodents and birds. Three replicates were used for this experimental setup for each of A. palmeri and A. tuberculatus species. Eighteen cages (nine for each species) were used in the study in each experimental location (Figure 2).
Experimental layout in which the randomized arrangement of main plots (i.e., retrieval year), subplots (colored seed bags representing the site by ecotype treatments), and sub-subplot (i.e., burial depth treatment) are depicted along with details for seedbank establishment (dimensions and burial depth of PVC cage).
Seed Germination
Germination tests on A. palmeri and A. tuberculatus seed samples before burial (December 2013) and after the completion of the experiment (December 2017) were conducted as described by Jha et al. (Reference Jha, Norsworthy and Garcia2014), with four replications for each combination of species and ecotype. For the duration of the experiment, seed samples were stored at 4 C with approximately 25% to 30% relative humidity.
For the germination evaluations, a seed lot of 100 seeds per species from each ecotype were placed in separate 9-cm-diameter plastic petri dishes (Fisher Scientific, Suwanee, GA, USA) lined with two layers of Whatman filter paper (Whatman’s No. 1, Fisher Scientific), and moistened with 5 ml of 1% (v/v) captan fungicide (Captan 4-L, Drexel Chemical, Memphis, TN, USA) solution in deionized water. These were incubated for 18 d with a 14-h photoperiod at 30 C, which is the optimum temperature for Amaranthaceae germination (Steckel et al. Reference Steckel, Sprague, Stoller and Wax2004). Deionized water was added when necessary to maintain adequate moisture for the incubated seeds. Seed germination was assessed every 6 d, with germination determined by radicle protrusion of at least 1 mm. Nongerminated seeds were checked for viability using both a tetrazolium test, as described below, and a seed crush test (Borza et al. Reference Borza, Westerman and Liebman2007; Sawna and Mohler Reference Sawna and Mohler2002). The viability of the untreated seed material from each location was evaluated separately; however, germination and viability test results were combined to estimate viability of each seed lot.
Seed Retrieval and Viability (Tetrazolium) Test
Each November, the bags pertaining to the retrieval timing at both depths were extracted by carefully unearthing the PVC cages. The retrieved seed bags from all sites were sent to Fayetteville, AR, where seeds were carefully retrieved and subjected to the tetrazolium test for seed viability evaluation. Soil that had been earlier added to the bags was gently rinsed with tap water, and the remaining content of the bag was placed in a 9-cm-diameter petri dish from which the seeds were retrieved using a pair of forceps (Becton, Dickinson, Franklin Lakes, NJ, USA) and visually inspected using a dissection Accu-Scope 3055 LED Stereo microscope (Accu-Scope, Commack, NY, USA). All seeds were counted and classified as damaged or intact.
Damaged seeds (%) were estimated based on Equation 1:
$${\rm DS{\,\equals\,}100}{\minus}{\rm IS}_{{t_{{_{i} }} }} ,\,i{\,\equals\,}1,2,\,{\rm or}\,3$$
where DS is damaged seeds + seed losses, IS is intact seeds found in the polyethylene seed bag at retrieval year t i , 100 is the total number of seeds placed in the polyethylene seed bag at the beginning of the experiment, and t i is retrieval year. Damaged seeds included broken, shrunk, or malformed seeds (Figure 3) and those lost due to deterioration and futile germination. Any other debris was also discarded.
Amaranthus palmeri seeds as they appeared under a dissection microscope (A) before the seed retrieval and cleaning processes and (B) after the cleaning process. The same criteria were used for A. tuberculatus seeds.
To facilitate tetrazolium straining, the undamaged seeds were initially placed in petri dishes between two Whatman filter papers that were moistened with 2.5 ml of deionized water for 24 h at room temperature. Immediately after this period, 2.5 ml of 1% w/w solution of 2, 3, 5-triphenyltetrazolium chloride was added to the petri dish to ensure that the seeds were well imbibed into the solution. Seeds remained at room temperature for a 24-h staining period (Forcella et al. Reference Forcella, Webster and Cardina2003). Seeds were then removed from the petri dish and gently crushed and classified as viable if the entire embryo was stained (Association of Official Seed Analysts 1970; Forcella et al. Reference Forcella, Webster and Cardina2003; International Seed Testing Association 1985; Price et al. Reference Price, Wright, Gross and Whalley2010).
The percentage of viable seeds (VS) after tetrazolium staining was calculated as the total number of viable seeds, which was the sum of germinated seeds (G) plus those that tested positive with tetrazolium (T) divided by the total number of seeds placed in the polyethylene seed bag (N) and multiplied by 100 (Equation 2) (Borza et al. Reference Borza, Westerman and Liebman2007).
$${\rm VS}{\,\equals\,}{{G{\rm }{\plus}{\rm }T} \over N}{\times}100$$
Damaged seeds were expressed as a percentage of the total seeds found in the polyethylene mesh bags at each retrieval time.
Soil Temperature and Volumetric Water Content
Minimum/maximum soil temperature and volumetric water content (i.e., soil moisture content) were recorded every 15 min using Onset HOBO U12 (Onset Computer, Bourne, MA, USA) data loggers with a soil-temperature probe (TMC6-HD, Onset Computer) and a soil-moisture probe (Onset S-SMD-M005 10HS, Onset Computer) placed at the soil surface and 15 cm below the soil surface throughout the entire experimental period. Data from the data loggers were downloaded to a laptop unit every 6 mo. Logger batteries were checked and were replaced, when necessary, every year.
Experimental Design and Data Analysis
The experiment was conducted as a split-split-plot design with three replications, where year of retrieval was the main plot factor, site by location of origin (ecotype) were subplot factors, and burial depth was the sub-subplot factor. The main plot treatments were randomly assigned, and they were permanent throughout the period of the study. The plot area was 1-m wide by 3-m long, and the subplot was 1 m2, although the experiment was limited to a PVC cage, and the sub-subplot was limited within the PVC cage (i.e., 60-cm diameter) (Figure 2).
Seed viability, expressed as a percentage viability of the initial 100-seed population placed in the polyethylene mesh bags between sites by origin locations, years, and burial depths, was analyzed as fixed effects by ANOVA using JMP v. 13.1.0 Pro software (SAS Institute, Cary, NC, USA), whereas replication was set as a random effect. Species were analyzed separately due to different collection origins. Seed damage was expressed as a percentage of the remaining seed population at each retrieval time and was analyzed using the same methods as those used for seed viability data.
Results and Discussion
Viability of Initially Harvested and Stored Seeds
The viability of the seeds from each location of origin was evaluated at the beginning and at the end of the experimental period using germination and tetrazolium tests. Both results were averaged and expressed as percentage viability. The percent viability ranged from 88.5% to 92.5% in 2013 and 89.2% to 94.5% in 2017 for A. palmeri and 88.5% to 94.5% in 2013 and 90.2% to 94.5% in 2017 for A. tuberculatus (Table 1). Barton (Reference Barton1961) reported 25% germination of A. retroflexus seed when stored on moist glass wool at constant temperatures over a period of 8 yr, but 100% viability and germination for the remaining seeds when these were exposed to suitable temperature and relative humidity environments.
Percentage of Amaranthus palmeri and Amaranthus tuberculatus viable seeds before (2013) and at the end of the experimental period (2017) of stored seed lots.
a Germinated and nongerminated but viable seeds were summed as viable seeds for both species.
Effects of Site and Seed Origin (Ecotype) on Seed Damage and Seed Viability
Significant differences (α=0.0001) for seed damage and viability were recorded for both species due to burial site. More specifically, higher seed damage averaged across ecotype, burial treatment, and retrieval year was recorded for the seed that originated from Illinois (51.3% and 51.8%) followed by Tennessee (40.5% and 45.1%), and Missouri (39.2% and 42%) for A. palmeri and A. tuberculatus, respectively. Pakeman et al. (Reference Pakeman, Small and Torvell2012) reported that increases in soil moisture resulted in increases of the rate of seed mortality. This might be attributed to the activity of fungal pathogens during moist or flooded conditions (Fogliatto et al. Reference Fogliatto, Vidotto and Ferrero2010; Liebman et al. Reference Liebman, Miller, Williams, Westerman, Dixon, Heggenstaller, Davis, Menalled and Sundberg2014). The average volumetric water content values for Illinois and Tennessee were recorded at 0.39 and 0.38, respectively, and were the highest levels among all sites, whereas that of Missouri was at a moderate level equal to 0.22 (Figure 4).
Monthly soil temperature (averaged over a 15-min concurrent recording period on a daily basis for the entire experimental period) at the top and at 15 cm below the soil surface (left y-axis) and monthly soil volumetric water content at 15 cm below soil surface (right y-axis) for each of the seven sites where the seed material of Amaranthus palmeri and Amaranthus tuberculatus was exposed to burial conditions during 2014–2016. Data presented for Missouri include only two experimental years (2015 and 2016).
Volumetric water content at field capacity varies among soils, with values ranging from 0.1 or less for sandy soils to 0.4 for clay soils (Sinclair and Bennet Reference Sinclair and Bennet1998). The Indiana and Mississippi sites exhibited high viability, averaged across burial treatments, years, and ecotypes, for both species (i.e., 33.8% and 19.5% for A. palmeri and 33.4% and 27.8% for A. tuberculatus, respectively). Both the Indiana and Mississippi locations, despite their differences in soil temperature, exhibited moderate average volumetric water content, compared with values recorded for Illinois or Tennessee, at 0.32 and 0.29, respectively (Figure 4).
Despite the similarities of soil texture between the experimental sites (Table 2), the moderately higher percentage of sand content at Indiana and Arkansas followed by Tennessee and Mississippi is noticeable. Nevertheless, further research is required to clarify possible relationships among soil type structure, volumetric water content, and seed damage or viability.
Soil series, texture class, and related particle percentages along with organic matter (OM) content and pH for each of the experimental sites where seeds of Amaranthus palmeri and Amaranthus tuberculatus were exposed to burial treatments.
Annual mean soil temperature at soil surface and 15 cm below the soil surface was recorded at 12.6 and 13.9 C for the Indiana site and at 17.8 and 18.2 C for the Mississippi site, respectively. Webb et al. (Reference Webb, Smith and Schulz-Schaeffer1987) reported that amaranth seedling emergence increased as temperature increased from 15.3 to 21.3 C under controlled environmental conditions. He also mentioned that these results corroborate earlier research under field conditions when mean spring soil temperatures were considered.
Larcher (Reference Larcher1980) reported that the movement of water through the soil profile and into plant tissue are soil-temperature dependent; water can be extracted more readily from warm than cold soils. The relatively low average soil temperatures (13.5 C) in combination with the low average soil volumetric water content recorded at Missouri (equal to 0.22) possibly resulted in low seed viability for both A. palmeri and A. tuberculatus (Figure 4). High soil moisture levels deplete soil oxygen, causing hypoxic conditions (Wesseling and van Wijk Reference Wesseling and van Wijk1957). Orthodox seeds, such as these of the Amaranthaceae family (Hong et al. Reference Hong, Linington and Ellis1996), maintain their longevity under aerobic conditions and permissible moisture levels; otherwise, seed viability will show the maximum rate of deterioration at a given temperature (Roberts and Ellis Reference Roberts and Ellis1989).
The effects of site by seed origin (ecotype) averaged over years and burial depth on seed viability were found to be different (α=0.001) for both species (Figure 5; Supplementary Tables S1 and S2). Independently, the origin of the seed, hence the conditions of maternal environment under which the seeds were produced, influences the ability of these species to form a persistent seedbank, even though persistence varies by site (Figure 5; Supplementary Tables S1 and S2). This facilitates the occurrence and distribution of these species, particularly A. palmeri, over a wide range of habitats (Korres et al. Reference Korres, Norsworthy, Bagavathiannan and Mauromoustakos2015) or soil characteristics (Korres et al. Reference Korres, Norsworthy, Brye, Skinner and Mauromoustakos2017). Nevertheless, Penfield and MacGregor (Reference Penfield and MacGregor2017) reported that seed-production environment effects are multifaceted and involve a complex and overlapping gene network that acts independently on fruit, seed coat, or zygotic tissues, which can be analyzed through careful physiological, molecular, and genetic approaches.
Interaction of experimental site by ecotype on seed viability for Amaranthus palmeri and Amaranthus tuberculatus averaged across 2014–2016. Vertical bars represent±standard error of the mean. Supplemental information is also provided in Supplementary Tables S1 and S2, where the actual values averaged across three replications per treatment and five locations of seed material origins are shown.
Seed Burial Effects
Burial depth affected (α=0.001) seed damage plus loss for both species. Seeds placed on the soil surface had increased damage and loss compared with seeds buried at 15 cm, independent of the experimental site. Increased damage and loss of unburied seeds at all sites within the same year ranged from 3% to 42% for A. palmeri and 10% to 62% for A. tuberculatus (Figure 6; Supplementary Tables S1 and S2). The rate of unburied seed damage/loss versus that of buried seeds, between consecutive years, was greater for the unburied seeds, particularly for 2014 and 2015 (Figure 6; Supplementary Tables S1 and S2), for both species. As reported by Hulme (Reference Hulme1998), seed burial protects seeds from insect predation; however, seeds are susceptible to fungal or bacterial pathogen infection (Blaney and Kotanen Reference Blaney and Kotanen2001; Leishman et al. Reference Leishman, Masters, Clarke and Brown2000). In addition, burial of seeds can amend unfavorable environmental effects, reducing seed weathering and increasing seed longevity (Facelli et al. Reference Facelli, Chesson and Barnes2005; Wijayratne and Pyke Reference Wijayratne and Pyke2012). Crist and Friese (Reference Crist and Friese1993) reported that seed decomposition and fungal pathogens were the major factors for the greatest decline of seeds deposited on soil surface compared with buried seeds. Nevertheless, susceptibility of weed seeds to decay by soil microorganisms is species dependent (Chee-Sanford et al. Reference Chee-Sanford, Williams, Davis and Sims2006), particularly in regard to the soil microbial community. The manipulation of soil fertility by the incorporation of organic amendments into the soil and/or the choice of cropping system that can influence the composition of fungal and bacterial communities (Davis Reference Davis2007; Davis et al. Reference Davis, Anderson, Hallett and Renner2006; Ullrich et al. Reference Ullrich, Buyer, Cavigelli, Seidel and Teasdale2011) might also affect seedbank longevity and persistence (De Cauwer et al. Reference De Cauwer, D’Hose, Cougnon, Leroy, Bulcke and Reheul2011).
Interaction of experimental site by burial depth on percentage seed damage and loss averaged across 2014–2016 for Amaranthus palmeri and Amaranthus tuberculatus. Damaged seeds include broken, shrunk, or malformed seeds and those lost due to deterioration or futile germination, which were impossible to count. Vertical bars represent±standard error of the mean. Supplemental information is also provided in Supplementary Tables S1 and S2, where the actual values averaged across three replications per treatment and five locations of seed material origins are shown.
Seeds that were not placed in the field but remained under storage conditions had an average viability of 94.8% and 91.1% (±1.3 SE) for A. palmeri and 93.5% and 91.4% (±1.3 SE) and A. tuberculatus for 2013 and 2017, respectively (Table 1). On the contrary, viability of intact seeds rapidly declined the first 12 mo by 80% and 85% for buried and unburied A. palmeri seeds, respectively (Figure 7). Likewise, the percentage loss of viability for buried and unburied A. tuberculatus seeds for the first 12 mo was 78.2% and 84.6%, respectively. Loss of seed viability continued to decrease for both species between 12 and 24 mo burial, reaching the lowest level, at which burial depth had no influence, by the end of the 36-mo experimental period (Figure 7).
Percentage seed viability as affected by burial depth and retrieval time (in months) for Amaranthus palmeri and Amaranthus tuberculatus. Vertical bars represent±standard error of the mean (i.e., 0.612 and 0.649 for A. palmeri and A. tuberculatus, respectively).
The rate at which A. palmeri and A. tuberculatus seeds lost viability over time depended on whether seeds were placed on the soil surface or buried, and it was found to vary among sites. A clear trend in reduction of seed viability was observed for Arkansas, Illinois, Indiana, Missouri, and Tennessee ecotypes compared with Mississippi and Wisconsin ecotypes in the case of A. palmeri (Figure 8). Viability of intact A. palmeri seeds on the soil surface was lower for the entire duration of the study but with some exceptions, as in the case of A. tuberculatus from the Indiana experimental site (Figure 8). Seed burial seemed to act as a long-term conservation mechanism for seedbank persistence in most sites for both species. Amaranthus palmeri seed viability was reduced in Arkansas between 2014 and 2016 for unburied seeds (90.3%) compared with buried seeds (79.4%). Similarly, seed viability declined by 88.7% and 68.4% in Illinois, by 82.4% and 69.2% in Indiana, by 63.1% and 62.2% in Mississippi, and by 60.6% and 43.8% in Wisconsin for unburied and buried seeds, respectively. Conversely, viability was reduced at a slower rate for unburied seeds than for buried seeds in Missouri and Tennessee. Similar trends were recorded for A. tuberculatus (Figure 8).
Effects of experimental site by burial depth by year on percentage seed viability for Amaranthus palmeri and Amaranthus tuberculatus. Vertical bars represent±standard error of the mean.
The effects of burial depth and burial duration on deterioration of seed viability and seedbank longevity have been demonstrated for a range of weed species, such as wild oat (Avena fatua L.) (Miller and Nalewaja Reference Miller and Nalewaja1990), kochia [Bassia scoparia (L.) A. J. Scott] (Zorner et al. Reference Zorner, Zimdahl and Schweizer1984), ripgut brome (Bromus diandrus Roth) (Gleichsner and Appleby Reference Gleichsner and Appleby1989), weedy rice (Oryza sp.) (Chauhan Reference Chauhan2012), giant ragweed (Ambrosia trifida L.) (Harrison et al. Reference Harrison, Regnier, Schmoll and Harrison2007), and A. palmeri (Sosnoskie et al. Reference Sosnoskie, Webster and Culpepper2013). All of these studies reported findings similar to the work presented here and highlighted the importance of burial duration and depth on seed longevity, seed viability, and seedbank persistence; the deeper the seed burial (up to 30 cm), the greater the seedbank persistence (up to 36 mo burial duration).
As mentioned previously, the first important phase for the development of a persistent soil seedbank is burial (Fenner and Thompson Reference Fenner and Thompson2005). Small seeds are more likely to become buried, thereby reinforcing the selective advantage of a small seed size, as is found in A. palmeri and A. tuberculatus, two very prolific weed species. The importance of tillage practices was mentioned as a primary tool for the depletion of seedbank persistence (Clements et al. Reference Clements, Benoit, Murphy and Swanton1996; Cousens and Moss Reference Cousens and Moss1990). Various studies (Blackshaw et al. Reference Blackshaw, Larney, Lindwall and Kozub1994; Ominski and Entz Reference Ominski and Entz2001) reported that conservation or zero-tillage systems resulted in reductions of weed populations and seedbank depletion, an approach that could be proven to be quite suitable for A. palmeri and A. tuberculatus. Accumulation of seeds on soil surface in reduced-tillage cropping systems could increase seed mortality due to increased seed predation (Hossain and Begum Reference Hossain and Begum2015). Lack of soil disturbance via tillage could also encourage higher predator populations, as it enhances the number, diversity, and/or activity of seed-consuming habitat (Blubaugh and Kaplan Reference Blubaugh and Kaplan2015). In addition, the removal of weed before seed-set or harvesting weed seed could serve as a prevention method in reducing soil seedbank inputs and depleting weed seedbanks (Walsh et al. Reference Walsh, Harrington and Powles2012, Reference Walsh, Newman and Powles2013), including those of Amaranthaceae weed species (Norsworthy et al. Reference Norsworthy, Korres, Walsh and Powles2016). The results presented here indicate that the greatest influence of seed viability was burial conditions, time, and site-specific soil conditions, more so than geographical location. Hence, management of these weed species should focus on reducing seed shattering, removing the seed from the soil surface where germination may occur for prolonged periods, enhancing seed predation, or adjusting tillage systems.
Supplementary Materials
To view supplementary material for this article, please visit https://doi.org/10.1017/wsc.2018.27
Acknowledgments
Financial support from the United Soybean Board for this research is greatly appreciated. Joe Beeler, David Kincer, Joseph L. Matthews, Shaun Billman, Devin Hammer, Nathan Drewitz, and John Gaska proved invaluable assistance for the completion of this project.
No conflicts of interest have been declared.
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