Natural Resources
Conservation Service
Ecological site R108XC515IA
Ponded Upland Depression Sedge Meadow
Last updated: 11/04/2024
Accessed: 08/23/2026
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Provisional. A provisional ecological site description has undergone quality control and quality assurance review. It contains a working state and transition model and enough information to identify the ecological site.
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Figure 1. Mapped extent
Areas shown in blue indicate the maximum mapped extent of this ecological site. Other ecological sites likely occur within the highlighted areas. It is also possible for this ecological site to occur outside of highlighted areas if detailed soil survey has not been completed or recently updated.
MLRA notes
Major Land Resource Area (MLRA): 108X–Illinois and Iowa Deep Loess and Drift
The Illinois and Iowa Deep Loess and Drift, West-Central Part (MLRA 108C) encompasses the eastern portion of the Southern Iowa Drift Plain and the Lake Calvin Basin of the Mississippi Alluvial Plain landforms (Prior 1991). It lies entirely in one state (Iowa), containing approximately 9,805 square miles (Figure 1). The elevation ranges from approximately 1,110 feet above sea level (ASL) on the highest ridges to about 505 feet ASL in the lowest valleys. Local elevation difference is mainly 10 to 20 feet. However, some valley floors can range from 80 to 200 feet, while some upland flats and valley floors only range between 3 and 6 feet. The MLRA is underlain by Pre-Illinoian glacial till, deposited more than 500,000 years ago and since undergone extensive erosion and dissection. In the northern half of the area the till thickness ranges from 150 to 350 feet and grades to less than 150 feet thick in the southern half. The till is covered by a mantle of Peoria Loess on the hillslopes and Holocene alluvium in the drainageways. Paleozoic bedrock, comprised of limestone, shale, and mudstones, lies beneath the glacial material (USDA-NRCS 2006).
The vegetation in the MLRA has undergone drastic changes over time. Spruce forests dominated the landscape 30,000 to 21,500 years ago. As the last glacial maximum peaked 21,500 to 16,000 years ago, they were replaced with open tundras and parklands. The end of the Pleistocene Epoch saw a warming climate that initially prompted the return of spruce forests, but as the warming continued, spruce trees were replaced by deciduous trees (Baker et al. 1990). Not until approximately 9,000 years ago did the vegetation transition to prairies as climatic conditions continued to warm and subsequently dry. Between 4,000 and 3,000 years ago, oak savannas began intermingling within the prairie landscape, while the more wooded and forested areas maintained a foothold in sheltered areas. This prairie-forest transition ecosystem formed the dominant landscapes until the arrival of European settlers (Baker et al. 1992).Classification relationships
USFS Subregions: Central Dissected Till Plains (251C) Section, Central Dissected Till and Loess Plain (251Cc), Mississippi River and Illinois Alluvial Plains (51Cf), Southeast Iowa Rolling Loess Hills (251Ch) Subsections (Cleland et al. 2007)
U.S. EPA Level IV Ecoregion: Rolling Loess Prairies (47f), Upper Mississippi Alluvial Plain (72d) (USEPA 2013)
National Vegetation Classification – Ecological Systems: North-Central Interior Wet Meadow-Shrub Swamp (CES202.701) (NatureServe 2015)
National Vegetation Classification – Plant Associations: Carex lacustris Wet Meadow (CEGL002256) (Community Phase 1.1); Cornus sericea-Salix (bebbiana, discolor, petiolaris)/Calamagrostis stricta Shrub Swamp (CEGL002187) (Community Phase 1.2) (Nature Serve 2015)
Biophysical Settings: Central Interior and Appalachian Shrub-Herbaceous Wetland Systems (BpS 4314930) (LANDFIRE 2009)
Natural Resources Conservation Service – Iowa Plant Community Species List: Wet Meadow, Lake Sedge (Community Phase 1.1); Shrub Meadow, Dogwood – Mixed Willow (Community Phase1.2) (USDA-NRCS 2007)
Iowa Department of Natural Resources: Prairie Marsh (INAI 1984)
U.S. Army Corps of Engineers: Sedge Meadows (Eggers and Reed 2015)Ecological site concept
Ponded Upland Depression Sedge Meadows are located within the blue areas on the map (Figure 1). They occur in upland depressions on slopes generally less than 2 percent. The soils are Mollisols that are very poorly-drained and deep, formed in loess. The site experiences rare to frequent, brief to long ponding from precipitation, overland flow, and groundwater flow. The native plant community is comprised of hydrophytic herbaceous vegetation.
The historic pre-European settlement vegetation on this ecological site was dominated by herbaceous species adapted to temporarily ponded conditions. Wheat sedge (Carex atherodes Spreng.) and Hayden’s sedge (Carex haydenii Dewey) are the dominant species of Ponded Upland Depression Sedge Meadows. Other sedges and grasses that may occur include woolly sedge (Carex pellita Muhl. ex Willd.), broom sedge (Carex scoparia Schkuhr ex Willd.), rigid sedge (Carex tetanica Schkuhr), and bluejoint (Calamagrostis canadensis (Michx.) P. Beauv.). Plant species typical of a natural plant community associated with this ecological site include pickerelweed (Pontederia cordata L.) and eastern marsh fern (Thelypteris palustris Schott) (Drobney et al. 2001; LANDFIRE 2009; Eggers and Reed 2015). Few shrubs may be present in very low densities and can include silky dogwood (Cornus amomum Mill.) and white meadowsweet (Spiraea alba Du Roi). Depth and duration of ponding as well as periodic fire are the primary disturbance factors that maintain this site, while drought is a secondary factor (LANDFIRE 2009; NatureServe 2015).Associated sites
R108XC516IA Wet Loess Upland Flat Prairie
Wet-mesic prairies on broad upland flats that do not experience ponding, including Garwin, Kalona, Mahaska, Muscatine, and Taintor soils
R108XC517IA Wet Loess Upland Flat Savanna
Wet-mesic savannas on broad upland flats that do not experience ponding, including Atterberry, Givin, Rubio, and Walford soils
Similar sites
R108XC519IA Wet Upland Drainageway Prairie
Wet Upland Drainageway Prairies are similar in landscape position, but site is a SLOPE: topographic, flow-through wetland
Table 1. Dominant plant species
Tree Not specified
Shrub Not specified
Herbaceous (1) Carex atherodes
(2) Carex haydeniiPhysiographic features
Ponded Upland Depression Sedge Meadows occur on upland depressions (Figure 2). They are situated on elevations ranging from approximately 600 to 1401 feet ASL. Ponding is rare to frequent and lasts from 2 to less than 30 days. Ponded water depths can be as high as 12 inches.
Figure 2. Figure 1. Location of Ponded Upland Depression Sedge Meadow ecological site within MLRA 108C.
Figure 3. Figure 2. Representative block diagram of Ponded Upland Depression Sedge Meadow and associated ecological sites.
Table 2. Representative physiographic features
Slope shape across (1) Concave
Slope shape up-down (1) Concave
Landforms (1) Upland > Depression
Runoff class Negligible to low Flooding frequency None Ponding duration Brief (2 to 7 days) to long (7 to 30 days) Ponding frequency Rare to frequent Elevation 600 – 1401 ft Slope 0 – 2 % Ponding depth 0 – 12 in Water table depth 0 in Aspect Aspect is not a significant factor Climatic features
The Illinois and Iowa Deep Loess and Drift, West-Central Part falls into the hot humid continental climate (Dfa) Köppen-Geiger climate classification (Peel et al. 2007). In winter, dry, cold air masses periodically shift south from Canada. As these air masses collide with humid air, snowfall and rainfall result. In summer, moist, warm air masses from the Gulf of Mexico migrate north, producing significant frontal or convective rains. Occasionally, hot, dry winds originating from the Desert Southwest will stagnate over the region, creating extended droughty periods in the summer from unusually high temperatures. Air masses from the Pacific Ocean can also spread into the region and dominate producing mild, dry weather in the autumn known as Indian Summers (NCDC 2006).
The soil temperature regime of MLRA 108C is classified as mesic, where the mean annual soil temperature is between 46 and 59°F (USDA-NRCS 2006). Temperature and precipitation occur along a north-south gradient, where temperature and precipitation increase the further south one travels. The average freeze-free period of this ecological site is about 187 days, while the frost-free period is about 170 days (Table 2). The majority of the precipitation occurs as rainfall in the form of convective thunderstorms during the growing season. Average annual precipitation is approximately 39 inches, which includes rainfall plus the water equivalent from snowfall (Table 3). The average annual low and high temperatures are 40 and 61°F, respectively.
Climate data and analyses are derived from 30-year averages gathered from five National Oceanic and Atmospheric Administration (NOAA) weather stations contained within the range of this ecological site (Table 4).Table 3 Representative climatic features
Frost-free period (characteristic range) 140-140 days Freeze-free period (characteristic range) 170-180 days Precipitation total (characteristic range) 40-40 in Frost-free period (actual range) 140-150 days Freeze-free period (actual range) 170-180 days Precipitation total (actual range) 40-40 in Frost-free period (average) 140 days Freeze-free period (average) 170 days Precipitation total (average) 40 in Characteristic rangeActual rangeBarLineFigure 4. Monthly precipitation range
Characteristic rangeActual rangeBarLineFigure 5. Monthly minimum temperature range
Characteristic rangeActual rangeBarLineFigure 6. Monthly maximum temperature range
BarLineFigure 7. Monthly average minimum and maximum temperature
Figure 8. Annual precipitation pattern
Figure 9 Annual average temperature pattern
Climate stations used
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(1) WASHINGTON [USC00138688], Washington, IA
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(2) FAIRFIELD [USC00132789], Fairfield, IA
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(3) OSKALOOSA [USC00136327], Oskaloosa, IA
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(4) MT PLEASANT 1 SSW [USC00135796], Mount Pleasant, IA
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(5) NEWTON [USC00135992], Newton, IA
">Influencing water features
Ponded Upland Depression Sedge Meadows are classified as a DEPRESSIONAL: Recharge, Ponded, Closed Depression; herbaceous wetland under the Hydrogeomorphic (HGM) classification system (Smith et al. 1995; USDA-NRCS 2008) and as a Palustrine Persistent Emergent Wetland under the National Wetlands Inventory (FGDC 2013). Precipitation, overland flow from adjacent uplands, and groundwater discharge are the main sources of water for this ecological site (Smith et al. 1995). Infiltration is very slow (Hydrologic Group D) for undrained soils, and surface runoff is negligible to low (Figure 5). <br />
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Primary wetland hydrology indicators for an intact Ponded Upland Depression Sedge Meadow may include: A1 Surface water, A2 High water table, A3 Saturation, and B7 Inundation visible on aerial photography. Secondary wetland hydrology indicators may include: C2 Dry-season water table, D1 Stunted or stressed plants, D2 Geomorphic position, and D5 FAC-neutral test (USACE 2010).
Figure 10. Figure 5. Hydrologic cycling in Ponded Upland Depression Sedge Meadow ecological site.
Soil features
Soils of Ponded Upland Depression Sedge Meadows are in the Mollisols orders, further classified as Typic Argialbolls that are impermeable with negligible to low runoff potential. The soil series associated with this site includes Sperry (Figure 6). The parent material is loess, and the soils are very poorly-drained and deep with seasonal high-water tables. Soil pH classes are strongly acid to slightly alkaline (Table 5). An abrupt textural change is noted as a rooting restriction for the soils of this ecological site.
Sperry soil map units in the MLRA may meet the definition of hydric soils and are listed as meeting criteria 2 and 3 of the hydric soils list (77 FR 12234).
Figure 11. Figure 6. Profile sketch of soil series associated with Ponded Upland Depression Sedge Meadow.
Table 4. Representative soil features
Parent material (1) Loess
Surface texture (1) Silt loam
(2) Silty clay loam
Family particle size (1) Fine
Drainage class Very poorly drained Permeability class Very slow Soil depth 80 in Surface fragment cover <=3" Not specified Surface fragment cover >3" Not specified Available water capacity
(Depth not specified)3 – 4 in Calcium carbonate equivalent
(Depth not specified)0 – 5 % Soil reaction (1:1 water)
(Depth not specified)5.1 – 7.8 Subsurface fragment volume <=3"
(Depth not specified)Not specified Subsurface fragment volume >3"
(Depth not specified)Not specified Ecological dynamics
The information in this Ecological Site Description, including the state-and-transition model (STM), was developed based on historical data, current field data, professional experience, and a review of the scientific literature. As a result, all possible scenarios or plant species may not be included. Key indicator plant species, disturbances, and ecological processes are described to inform land management decisions.
The MLRA lies within the transition zone between the eastern deciduous forests and the tallgrass prairies. The heterogeneous topography of the area results in variable microclimates and fuel matrices that in turn are able to support prairies, savannas, woodlands, and forests. Ponded Upland Depression Sedge Meadows form an aspect of this vegetative continuum. This ecological site occurs on upland depressions on very poorly drained soils. Species characteristic of this ecological site consist of hydrophytic herbaceous vegetation.
Ponding and fire are the most important ecosystem drivers for maintaining this ecological site. The depth and duration of ponding affect species composition, cover, and vegetative production due to alternating aerobic and anaerobic surface substrate conditions. Replacement fires likely occurred on a ten-year rotation interval and helped to reduce the accumulation of peat. The combination of fire and high-water levels prevented the establishment of shrubs for any significant amount of time (LANDFIRE 2009).
Drought has also played a role in shaping this ecological site. The periodic episodes of reduced soil moisture in conjunction with the very poorly-drained soils have favored the proliferation of plant species tolerant of such conditions. Drought can slow the growth of plants and result in dieback of certain species. When coupled with fire, periods of drought can eliminate or greatly reduce the occurrence of woody vegetation, substantially altering the extent of shrubs and trees (Pyne et al. 1996).
Today, Ponded Upland Depression Sedge Meadows have been virtually eliminated as the land has mostly been converted to agricultural production. Corn (Zea mays L.) and soybeans (Glycine max (L.) Merr.) are the dominant crops grown, but small patches of forage land may be present. A return to the historic plant community is likely not possible due to significant hydrologic and water quality changes in the watershed, but long-term conservation agriculture or habitat reconstruction efforts can help to restore some natural diversity and ecological functioning. The state-and-transition model that follows provides a detailed description of each state, community phase, pathway, and transition. This model is based on available experimental research, field observations, literature reviews, professional consensus, and interpretations.State and transition model
Custom diagramStandard diagram
More interactive model formats are also available. View Interactive Models
More interactive model formats are also available. View Interactive Models
Click on state and transition labels to scroll to the respective textEcosystem states
States 2 and 5 (additional transitions)
State 1 submodel, plant communities
State 2 submodel, plant communities
State 3 submodel, plant communities
State 4 submodel, plant communities
State 5 submodel, plant communities
State 1
Reference StateThe reference plant community is categorized as a sedge meadow community, dominated by hydrophytic herbaceous vegetation. The two community phases within the reference state are dependent on ponding and fire. The depth and duration of ponding alters species composition, cover, and extent, while regular fire intervals keep woody species from encroaching. Drought has more localized impacts in the reference phases, but does contribute to overall species composition, diversity, cover, and productivity.
Community 1.1
Wheat Sedge – Hayden’s SedgeSites in this reference community phase are dominated by sedges with grasses and forbs interspersed. Mature plants typically range between 1.5 and 3 feet tall, and ground cover is continuous (75 to 100 percent). Wheat sedge and Hayden’s sedge are the dominant species. Woolly sedge, broom sedge, rigid sedge, and bluejoint can also occur. Common forbs include knotweeds (Polygonum sagittatum L., Polygonum amphibium L., Polygonum pensylvanicaum L.), giant goldenrod (Solidago gigantea Aiton), marsh hedgenettle (Stachys palustris L.), and Virginia mountainmint (Pycnanthemum virginanum (L.) T. Dur. & B.D. Jacks. ex B.L. Rob. & Fernald) (LANDFIRE 2009; NatureServe 2015).
Community 1.2
Silky Dogwood – White Meadowsweet/Wheat Sedge – Hayden’s SedgeThis reference community phase can occur when the frequency and depth of ponding are reduced such as from periodic drought. This phase can also occur when fire return intervals decrease. The community assumes more of a shrub-carr assemblage, and shrubs, such as silky dogwood and white meadowsweet, become more prominent in the community encompassing at least 25 percent cover (NatureServe 2015). Sedges and forbs are still present but are likely reduced in areas where shrubs create pockets of shade (LANDFIRE 2009).
Pathway 1.1A
Community 1.1 to 1.2Reduced fire return intervals and/or periodic drying results in a reduction of the average soil water levels.
Pathway 1.2A
Community 1.2 to 1.1Increased fire return intervals and/or average soil water levels rise.
State 2
Hydrologically-altered StateHydrology is the most important determinant of wetlands and wetland processes. Hydrology modifies and determines the physiochemical environment (i.e., sediments, soil chemistry, water chemistry) which in turn directly affects the vegetation, animals, and microbes (Mitsch and Gosselink 2007). Human activities on landscape hydrology have greatly altered Ponded Upland Depression Sedge Meadows. Alterations such as agricultural tile draining and conversion to cropland on adjacent lands have changed the natural hydroperiod, increased the rate of sedimentation, and intensified nutrient pollution (Werner and Zedler 2003; Mitsch and Gosselink 2007).
Community 2.1
Reed Canarygrass – Wheat SedgeThis community phase represents the early changes to the natural wetland hydroperiod, sedimentation, and nutrient runoff. Sedimentation results in a reduction of soil organic matter and high dry bulk density. It also leads to a homogenization of the local microtopography, reducing the surface area and associated species diversity (Green and Galatowitsch 2002; Werner and Zedler 2002). Wheat sedge continues to form a component of the herbaceous layer, but the highly-invasive reed canarygrass (Phalaris arundinacea L.) co-dominates.
Community 2.2
Reed Canarygrass – Nodding BeggartickSites falling into this community phase have experienced significant sedimentation and are dominated by either a monoculture of reed canarygrass or a combination of reed canarygrass and nodding beggartick (Bidens cernua L.). Reed canarygrass stands can significantly alter the physiochemical environment as well as the biotic communities, making the site only suitable to reed canarygrass. These monotypic stands create a positive feedback loop that perpetuates increasing sedimentation, altered hydrology, and dominance by this non-native species, especially in sites affected by nutrient enrichment from agricultural runoff (Vitousek 1995; Bernard and Lauve 1995; Green and Galatowitsch 2002; Werner and Zedler 2002; Kercher et al. 2007; Waggy 2010).
Pathway 2.1A
Community 2.1 to 2.2Continuing alterations to the natural hydrology and increasing sedimentation.
State 3
Forage StateThe forage state occurs when the site is converted to a farming operation that emphasizes domestic livestock production known as grassland agriculture. Fire suppression, periodic cultural treatments (e.g., clipping, drainage, soil amendment applications, planting new species and/or cultivars, mechanical harvesting) and grazing by domesticated livestock transition and maintain this state (USDA-NRCS 2003). Early settlers seeded non-native species, such as smooth brome (Bromus inermis Leyss.) and Kentucky bluegrass (Poa pratensis L.), to help extend the grazing season (Smith 1998). Over time, as lands were continuously harvested or grazed by herds of cattle, the non-native species were able to spread and expand across the landscape, reducing the native species diversity and ecological function.
Community 3.1
HayfieldSites in this community phase consist of forage plants that are planted and mechanically harvested. Mechanical harvesting removes much of the aboveground biomass and nutrients that feed the soil microorganisms (Franzluebbers et al. 2000; USDA-NRCS 2003). As a result, soil biology is reduced leading to decreases in nutrient uptake by plants, soil organic matter, and soil aggregation. Frequent biomass removal can also reduce the site’s carbon sequestration capacity (Skinner 2008).
Community 3.2
Continuous Pastured GrazingThis community phase is characterized by continuous grazing where domestic livestock graze a pasture for the entire season. Depending on stocking density, this can result in lower forage quality and productivity, weed invasions, and uneven pasture use. Continuous grazing can also increase the amount of bare ground and erosion and reduce soil organic matter, cation exchange capacity, water-holding capacity, and nutrient availability and retention (Bharati et al. 2002; Leake et al. 2004; Teague et al. 2011). Smooth brome, Kentucky bluegrass, and white clover (Trifolium repens L.) are common pasture species used in this phase. Their tolerance to continuous grazing has allowed these species to dominate, sometimes completely excluding the native vegetation.
Community 3.3
Periodic-rest Pastured GrazingThis community phase is characterized by periodic-rest grazing where the pasture has been subdivided into several smaller paddocks. Subdividing the pasture in this way allows livestock to utilize one or a few paddocks, while the remaining area is rested allowing plants to restore vigor and energy reserves, deepen root systems, develop seeds, as well as allow seedling establishment (Undersander et al. 2002; USDA-NRCS 2003). Periodic-rest pastured grazing includes deferred periods, rest periods, and periods of high intensity – low frequency, and short duration methods. Vegetation is generally more diverse and can include orchardgrass (Dactylis glomerata L.), timothy (Phleum pretense L.), red clover (Trifolium pratense L.), and alfalfa (Medicago sativa L.). The addition of native prairie species can further bolster plant diversity and, in turn, soil function. This community phase promotes numerous ecosystem benefits including increasing biodiversity, preventing soil erosion, maintaining and enhancing soil quality, sequestering atmospheric carbon, and improving water yield and quality (USDA-NRCS 2003).
Pathway 3.1A
Community 3.1 to 3.2Mechanical harvesting is replaced with domestic livestock utilizing continuous grazing.
Pathway 3.1B
Community 3.1 to 3.3Mechanical harvesting is replaced with domestic livestock utilizing periodic-rest grazing.
Pathway 3.2A
Community 3.2 to 3.1Domestic livestock are removed, and mechanical harvesting is implemented.
Pathway 3.2B
Community 3.2 to 3.3Periodic-rest grazing replaces continuous grazing.
Pathway 3.3B
Community 3.3 to 3.1Domestic livestock are removed, and mechanical harvesting is implemented.
Pathway 3.3A
Community 3.3 to 3.2Continuous grazing replaces periodic-rest grazing.
State 4
Cropland StateThe low topographic relief across the MLRA has resulted in nearly the entire area being converted to agriculture (Eilers and Roosa 1994). The continuous use of tillage, row-crop planting, and chemicals (i.e., herbicides, fertilizers, etc.) has effectively eliminated the reference community and many of its natural ecological functions in favor of crop production. Corn and soybeans are the dominant crops for the site, and oats (Avena L.) and alfalfa (Medicago sativa L.) may be rotated periodically. These areas are likely to remain in crop production for the foreseeable future.
Community 4.1
Conventional Tillage FieldSites in this community phase typically consist of monoculture row-cropping maintained by conventional tillage practices. They are cropped in either continuous corn or alternating periods of corn and soybean crops. The frequent use of deep tillage, low crop diversity, and bare soil conditions during the non-growing season negatively impacts soil health. Under these practices, soil aggregation is reduced or destroyed, soil organic matter is reduced, erosion and runoff are increased, and infiltration is decreased, which can ultimately lead to undesirable changes in the hydrology of the watershed (Tomer et al. 2005).
Community 4.2
Conservation Tillage FieldThis community phase is characterized by periodically alternating crops and utilizing various conservation tillage methods to promote soil health and reduce erosion. Conservation tillage methods include strip-till, ridge-till, vertical-till, or no-till planting operations. Strip-till keeps seedbed preparation to narrow bands less than one-third the width of the row where crop residue and soil consolidation are left undisturbed in-between seedbed areas. Strip-till planting may be completed in the fall and nutrient application either occurs simultaneously or at the time of planting. Ridge-till uses specialized equipment to create ridges in the seedbed and vegetative residue is left on the surface in between the ridges. Weeds are controlled with herbicides and/or cultivation, seedbed ridges are rebuilt during cultivation, and soils are left undisturbed from harvest to planting. Vertical-till operations employ machinery that lightly tills the soil and cuts up crop residue, mixing some of the residue into the top few inches of the soil while leaving a large portion on the surface. No-till management is the most conservative, disturbing soils only at the time of planting and fertilizer application. Compared to conventional tillage operations, conservation tillage methods can improve soil ecosystem function by reducing soil erosion, increasing organic matter and water availability, improving water quality, and reducing soil compaction.
Community 4.3
Conservation Tillage with Cover Crop FieldThis community phase applies conservation tillage methods as described above as well as adds cover crop practices. Cover crops typically include nitrogen-fixing species (e.g., legumes), small grains (e.g., rye, wheat, oats), or forage covers (e.g., turnips, radishes, rapeseed). The addition of cover crops not only adds plant diversity but also promotes soil health by reducing soil erosion, limiting nitrogen leaching, suppressing weeds, increasing soil organic matter, and improving the overall soil ecosystem. In the case of small grain cover crops, surface cover and water infiltration are increased, while forage covers can be used to graze livestock or support local wildlife. Of the three community phases for this state, this phase promotes the greatest soil sustainability and improves ecological functioning within a row crop operation.
Pathway 4.1A
Community 4.1 to 4.2Tillage operations are greatly reduced, alternating crops occurs on a regular interval, and crop residue remains on the soil surface.
Pathway 4.1B
Community 4.1 to 4.3Tillage operations are greatly reduced or eliminated, alternating crops occurs on a regular interval, crop residue remains on the soil surface, and cover crops are planted following crop harvest.
Pathway 4.2A
Community 4.2 to 4.14.2A – Intensive tillage is utilized, and monoculture row-cropping is established.
Pathway 4.2B
Community 4.2 to 4.3Cover crops are implemented to minimize soil erosion.Cover crops are implemented to minimize soil erosion.
Pathway 4.3B
Community 4.3 to 4.1Intensive tillage is utilized, cover crops practices are abandoned, monoculture row-cropping is established on a more-or-less continuous basis.
Pathway 4.3A
Community 4.3 to 4.2Cover crop practices are abandoned.
State 5
Reconstructed Sedge Meadow StateSedge meadow habitats provide multiple ecosystem services including flood abatement, water quality improvement, and biodiversity support. However, many sedge meadow communities have been stressed from watershed-scale changes in hydrology or eliminated as a result of type conversions to agricultural production, thereby significantly reducing these services (Zedler 2003). The extensive alterations of lands adjacent to Ponded Upland Depression Sedge Meadows may not allow for restoration back to the historic reference condition. However, ecological reconstruction can aim to aid the recovery of degraded, damaged or destroyed functions. A successful reconstruction will have the ability to structurally and functionally sustain itself, demonstrate resilience to the natural ranges of stress and disturbance, and create and maintain positive biotic and abiotic interactions (SER 2002; Mitsch and Jørgensen 2004).
Community 5.1
Early Successional Sedge MeadowThis community phase represents the early community assembly from sedge meadow reconstruction and is highly dependent on seed viability, hydroperiod, soil organic matter content, and site preparation. Successful establishment of sedges can be maximized by using seed collected during the same growing season, utilizing genotypes adapted to the environmental location, ensuring soil moisture is saturated at the time of seeding, and improving the water holding capacity and fertility of the soil (Budelsky and Galatowitsch 1999; van der Valk et al. 1999; Mitsch and Gosselink 2007; Hall and Zedler 2010). In addition, suppression and removal of non-native species is essential for reducing competition (Perry and Galatowitsch 2003).
Community 5.2
Late Successional Sedge MeadowLate Successional Sedge Meadow – Appropriately timed disturbance regimes (e.g., hydroperiod, prescribed fire) and nutrient management applied to the early successional community phase can help increase the species richness, pushing the site into a late successional community phase over time (Mitsch and Gosselink 2007).
Pathway 5.1A
Community 5.1 to 5.2Maintenance of proper hydrology and nutrient balances in line with a developed wetland management plant.
Pathway 5.2A
Community 5.2 to 5.1Reconstruction experiences a setback from extreme weather event or improper timing of management actions.
Transition T1A
State 1 to 2Direct and indirect alterations to the landscape hydrology from human-induced land development transition the site to the hydrologically-altered state (2).
Transition T1B
State 1 to 3Cultural treatments to enhance forage quality and yield transition the site to the forage state (3).
Transition T1C
State 1 to 4Installation of drain tiles, seeding of agricultural crops, and non-selective herbicide transition the site to the cropland state (4).
Transition T2A
State 2 to 3Cultural treatments to enhance forage quality and yield transition the site to the forage state (3).
Transition T2B
State 2 to 4Installation of drain tiles, seeding of agricultural crops, and non-selective herbicide transition the site to the cropland state (4).
Restoration pathway R2A
State 2 to 5Hydroperiod restoration, site preparation, non-native species control, and seeding native species transition the site to the reconstructed sedge meadow state (5).
Transition T3A
State 3 to 2Land abandonment transitions the site to the hydrologically-altered state (2).
Transition T3B
State 3 to 4Tillage, seeding of agricultural crops, and non-selective herbicide transition this site to the cropland state (4).
Restoration pathway R3A
State 3 to 5Hydroperiod restoration, site preparation, non-native species control and seeding native species transition this site to the reconstructed sedge meadow state (5).
Transition T4A
State 4 to 2Land abandonment transitions the site to the hydrologically-altered state (2).
Transition T4B
State 4 to 3Cultural treatments to enhance forage quality and yield transitions the site to the forage state (3).
Restoration pathway R4A
State 4 to 5Hydroperiod restoration, site preparation, non-native species control and seeding native species transition this site to the reconstructed sedge meadow state (5).
Transition T5A
State 5 to 2Land is abandoned and left fallow; natural succession by opportunistic species transition this site the hydrologically-altered state (2).
Transition T5B
State 5 to 3Cultural treatments to enhance forage quality and yield transition the site to the forage state (3).
Transition T5C
State 5 to 4Installation of drain tiles, seeding of agricultural crops, and non-selective herbicide transition the site to the cropland state (4).
Additional community tables
Table 5. Community 1.1 plant community composition
Group Common name Symbol Scientific name Annual production () Foliar cover (%) Table 6. Community 1.2 plant community composition
Group Common name Symbol Scientific name Annual production () Foliar cover (%) Table 7. Community 2.1 plant community composition
Group Common name Symbol Scientific name Annual production () Foliar cover (%) Table 8. Community 2.2 plant community composition
Group Common name Symbol Scientific name Annual production () Foliar cover (%) Table 9. Community 3.1 plant community composition
Group Common name Symbol Scientific name Annual production () Foliar cover (%) Table 10. Community 3.2 plant community composition
Group Common name Symbol Scientific name Annual production () Foliar cover (%) Table 11. Community 3.3 plant community composition
Group Common name Symbol Scientific name Annual production () Foliar cover (%) Table 12. Community 4.1 plant community composition
Group Common name Symbol Scientific name Annual production () Foliar cover (%) Table 13. Community 4.2 plant community composition
Group Common name Symbol Scientific name Annual production () Foliar cover (%) Table 14. Community 4.3 plant community composition
Group Common name Symbol Scientific name Annual production () Foliar cover (%) Table 15. Community 5.1 plant community composition
Group Common name Symbol Scientific name Annual production () Foliar cover (%) Table 16. Community 5.2 plant community composition
Group Common name Symbol Scientific name Annual production () Foliar cover (%) Interpretations
Supporting information
Inventory data references
Tier 3 Sampling Plot used to develop the reference state, community phases 1.1 and 1.2: State County Ownership Legal Description Easting Northing Iowa Muscatine Shield Prairie – Iowa Department of Natural Resources T77N R2W S7 656760 4593869 Tier 3 Sampling Plot used to develop alternative state, community phase 2.2: State County Ownership Legal Description Easting Northing Iowa Muscatine Shield Prairie – Iowa Department of Natural Resources T77N R2W S18 656426 4593679
Other references
Baker, R.G., C.A. Chumbley, P.M. Witinok, and H.K. Kim. 1990. Holocene vegetational changes in eastern Iowa. Journal of the Iowa Academy of Science 97: 167-177.
Baker, R.G., L.J. Maher, C.A. Chumbley, and K.L. Van Zant. 1992. Patterns of Holocene environmental changes in the midwestern United States. Quaternary Research 37: 379-389.
Bernard, J.B. and T.E. Lauve. 1995. A comparison of growth and nutrient uptake in Phalaris arundinacea L. growing in a wetland and a constructed bed receiving landfill leachate. Wetlands 15: 176-182.
Bharati, L., K.-H. Lee, T.M. Isenhart, and R.C. Schultz. 2002. Soil-water infiltration under crops, pasture, and established riparian buffer in Midwestern USA. Agroforestry Systems 56: 249-257.
Budelsky, R.A. and S.M. Galatowitsch. 1999. Effects of moisture, temperature, and time on seed germination of five wetland Carices: implications for restoration. Restoration Ecology 7: 86-97.
Changes in Hydric Soils Database Selection Criteria. 77 Federal Register 12234 (29 February 2012), pp. 12234-12235.
Cleland, D.T., J.A. Freeouf, J.E. Keys, G.J. Nowacki, C. Carpenter, and W.H. McNab. 2007. Ecological Subregions: Sections and Subsections of the Coterminous United States. USDA Forest Service, General Technical Report WO-76. Washington, DC. 92 pps.
Drobney, P.D., G.S. Wilhelm, D. Horton, M. Leoschke, D. Lewis, J. Pearson, D. Roosa, and D. Smith. 2001. Floristic Quality Assessment for the State of Iowa. Neal Smith National Wildlife Refuge and Ada Hayden Herbarium, Iowa State University, Ames, IA. 123 pps.
Eggers, S.D. and D.M. Reed. 2015. Wetland Plants and Plant Communities of Minnesota and Wisconsin, Version 3.2. U.S. Army Corps of Engineers, Regulatory Branch, St. Paul District. St. Paul, MN. 478 pps.
Federal Geographic Data Committee. 2013. Classification of Wetlands and Deepwater Habitats of the United States. FGDC-STD-004-2013. Second Edition. Wetlands Subcommittee, Federal geographic Data Committee and U.S. Fish and Wildlife Service, Washington, D.C. 90 pps.
Franzluebbers, A.J., J.A. Stuedemann, H.H. Schomberg, and S.R. Wilkinson. 2000. Soil organic C and N pools under long-term pasture management in the Southern Piedmont USA. Soil Biology and Biochemistry 32:469-478.
Green, E.K. and S.M. Galatowitsch. 2002. Effects of Phalaris arundinacea and nitrate-N addition on the establishment of wetland plant communities. Journal of Applied Ecology 39: 134-144.
Hall, S.J. and J.B. Zedler. 2010. Constraints on sedge meadow self-restoration in urban wetlands. Restoration Ecology 18: 671-680.
Iowa Natural Areas Inventory [INAI]. 1984. An Inventory of Significant Natural Areas in Iowa: Two Year Progress Report of the Iowa natural Areas Inventory. Iowa Natural Areas Inventory, Iowa Department of Natural Resources, Des Moines, IA.
Kercher, S.M. A. Herr-Turnoff, J.B. Zedler. 2007. Understanding invasion as a process: the case of Phalaris arundinacea in wet prairies. Biological Invasions 9: 657-665.
LANDFIRE. 2009. Biophysical Setting 4314930 Central Interior and Appalachian Shrub-Herbaceous Wetland Systems. In: LANDFIRE National Vegetation Dynamics Models. USDA Forest Service and US Department of Interior. Washington, DC.
Leake, J., D. Johnson, D. Donnelly, G. Muckle, L. Boddy, and D. Read. 2004. Networks of power and influence: the role of mycorrhizal mycelium in controlling plant communities and agroecosystem functioning. Canadian Journal of Botany 82: 1016-1045.
Mitsch, W.J. and S.E. Jørgensen. 2004. Ecological Engineering and Ecosystem Restoration. John Wiley & Sons, Inc. Hoboken, NJ. 428 pps.
Mitsch, W.J. and J.G. Gosselink. 2007. Wetlands, Fourth Edition. John Wiley & Sons, Inc. Hoboken, NJ. 582 pps.
National Climate Data Center [NCDC]. 2006. Climate of Iowa. Central Region Headquarters, Climate Services Branch, National Climatic Data Center, Asheville, NC.
NatureServe. 2015. NatureServe Explorer: An online encyclopedia of life [web application]. Version 7.1 NatureServe, Arlington, VA. Available at http://explorer.natureserve.org. (Accessed 13 February 2017).
Peel, M.C., B.L. Finlayson, and T.A. McMahon. 2007. Updated world map of the Köppen-Geiger climate classification. Hydrology and Earth System Sciences 11: 1633-1644.
Perry, L.G. and S.M. Galatowitsch. 2003. A test of two annual cover crops for controlling Phalaris arundinacea invasion in restored sedge meadow wetlands. Restoration Ecology 11: 297-307.
Prior, J.C. 1991. Landforms of Iowa. University of Iowa Press for the Iowa Department of Natural Resources, Iowa City, IA. 153 pps.
Pyne, S.J., P.L. Andrews, and R.D. Laven. 1996. Introduction to Wildland Fire, Second Edition. John Wiley and Sons, Inc. New York, New York. 808 pps.
Skinner, R.H. 2008. High biomass removal limits carbon sequestration potential of mature temperate pastures. Journal for Environmental Quality 37: 1319-1326.
Smith, R.D., A. Ammann, C. Bartoldus, and M.M. Brinson. 1995. An Approach for Assessing Wetland Functions Using Hydrogeomorphic Classification, Reference Wetlands, and Functional Indices. U.S. Army Corps of Engineers, Waterways Experiment Station, Wetlands Research Program Technical Report WRP-DE-9. 78 pps.
Smith, D.D. 1998. Iowa prairie: original extent and loss, preservation, and recovery attempts. The Journal of the Iowa Academy of Sciences 105: 94-108.
Society for Ecological Restoration [SER] Science & Policy Working Group. 2002. The SER Primer on Ecological Restoration. Available at: http://www.ser.org/. (Accessed 28 February 2017).
Teague, W.R., S.L. Dowhower, S.A. Baker, N. Haile, P.B. DeLaune, and D.M. Conover. 2011. Grazing management impacts on vegetation, soil biota and soil chemical, physical and hydrological properties in tall grass prairie. Agriculture, Ecosystems and Environment 141: 310-322.
Tomer, M.D., D.W. Meek, and L.A. Kramer. 2005. Agricultural practices influence flow regimes of headwater streams in western Iowa. Journal of Environmental Quality 34:1547-1558.
Undersander, D., B. Albert, D. Cosgrove, D. Johnson, and P. Peterson. 2002. Pastures for Profit: A Guide to Rotational Grazing (A3529). University of Wisconsin-Extension and University of Minnesota Extension Service. 43 pps.
U.S. Army Corps of Engineers [USACE]. 2010. Regional Supplement to the Corps of Engineers Wetland Delineation Manual: Midwest Region (Version 2.0). U.S. Army Corps of Engineers, Wetlands Regulatory Assistance Program, U.S. Army Engineer Research and Development Center, Vicksburg, MS. 141 pps.
United States Department of Agriculture – Natural Resources Conservation Service (USDA-NRCS). 2003. National Range and Pasture Handbook, Revision 1. Grazing Lands Technology Institute. 214 pps.
United States Department of Agriculture – Natural Resources Conservation Service (USDA-NRCS). 2006. Land Resource Regions and Major Land Resource Areas of the United States, the Caribbean, and the Pacific Basin. U.S. Department of Agriculture Handbook 296. 682 pps.
United States Department of Agriculture – Natural Resources Conservation Service (USDA-NRCS). 2007. Iowa NRCS Plant Community Species Lists. Des Moines, IA. Available at https://www.nrcs.usda.gov/wps/ portal/nrcs/detail/ia/technical/ecoscience/bio/?cid=nrcs142p2_008160. (Accessed 19 January 2018).
United States Department of Agriculture – Natural Resources Conservation Service (USDA-NRCS). 2008. Hydrogeomorphic Wetland Classification: An Overview and Modification to Better Meet the Needs of the Natural Resources Conservation Service. Technical Note No. 190-8-76. Washington, D.C. 8 pps.
U.S. Environmental Protection Agency [EPA]. 2013. Level III and Level IV Ecoregions of the Continental United States. Corvallis, OR, U.S. EPA, National Health and Environmental Effects Research Laboratory, map scale 1: 3,000,000. Available at http://www.epa.gov/eco-research/level-iii-andiv-ecoregions-continental-united-states. (Accessed 1 March 2017).
Van der Valk, A.G., T.L. Bremholm, and E. Gordon. 1999. The restoration of sedge meadows: seed viability, seed germination requirements, and seedling growth of Carex species. Wetlands 19: 756-764.
Vitousek, P.M. 1990. Biological invasions and ecosystem processes: towards an integration of population biology and ecosystem studies. Oikos 57: 7-13.
Waggy, M.A. 2010. Phalaris arundinacea. In: Fire Effects Information System [Online]. U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station, Fire Sciences Laboratory. Available at: https://www.feis-crs.org/feis/. (Accessed 1 February 2017).
Werner, K.J. and J.B. Zedler. 2002. How sedge meadow soils, microtopography, and vegetation respond to sedimentation. Wetlands 3: 451-466.
Zedler, J.B. 2003. Wetlands at your service: reducing impacts of agriculture at the watershed scale. Frontiers in Ecology and the Environment 1: 65-72.Contributors
Lisa Kluesner
Ryan DermodyApproval
Suzanne Mayne-Kinney, 11/04/2024
Acknowledgments
This project could not have been completed without the dedication and commitment from a variety of partners and staff (Table 6). Team members supported the project by serving on the technical team, assisting with the development of state and community phases of the state-and-transition model, providing peer review and technical editing, and conducting quality control and quality assurance reviews. Organization Name Title Location Drake University: Dr. Tom Rosburg Professor of Ecology and Botany Des Moines, IA Iowa Department of Natural Resources: Kevin Andersen Private Lands Biologist Fairfield, IA John Pearson Ecologist Des Moines, IA LANDFIRE (The Nature Conservancy): Randy Swaty Ecologist Evanston, IL Natural Resources Conservation Service: Rick Bednarek Iowa State Soil Scientist Des Moines, IA Leland Camp Soil Scientist Waverly, IA Stacey Clark Regional Ecological Site Specialist St. Paul, MN Ryan Dermody Soil Survey Leader Waverly, IA Tonie Endres Senior Regional Soil Scientist Indianapolis, IN John Hammerly Soil Data Quality Specialist Indianapolis, IN Lisa Kluesner Ecological Site Specialist Waverly, IA Sean Kluesner Earth Team Volunteer Waverly, IA Jeff Matthias State Grassland Specialist Des Moines, IA Kevin Norwood Soil Survey Regional Director Indianapolis, IN Doug Oelmann Soil Scientist Des Moines, IA James Phillips GIS Specialist Des Moines, IA Jason Steele Area Resource Soil Scientist Fairfield, IA Doug Wallace Ecologist ACES Program Columbia, MO This site was originally published by Lisa Kluesner on 7/1/2019.
Rangeland health reference sheet
Interpreting Indicators of Rangeland Health is a qualitative assessment protocol used to determine ecosystem condition based on benchmark characteristics described in the Reference Sheet. A suite of 17 (or more) indicators are typically considered in an assessment. The ecological site(s) representative of an assessment location must be known prior to applying the protocol and must be verified based on soils and climate. Current plant community cannot be used to identify the ecological site.
Author(s)/participant(s) Contact for lead author Date 08/23/2026 Approved by Approval date Composition (Indicators 10 and 12) based on Annual Production Indicators
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Number and extent of rills:
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Presence of water flow patterns:
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Number and height of erosional pedestals or terracettes:
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Bare ground from Ecological Site Description or other studies (rock, litter, lichen, moss, plant canopy are not bare ground):
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Number of gullies and erosion associated with gullies:
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Extent of wind scoured, blowouts and/or depositional areas:
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Amount of litter movement (describe size and distance expected to travel):
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Soil surface (top few mm) resistance to erosion (stability values are averages - most sites will show a range of values):
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Soil surface structure and SOM content (include type of structure and A-horizon color and thickness):
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Effect of community phase composition (relative proportion of different functional groups) and spatial distribution on infiltration and runoff:
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Presence and thickness of compaction layer (usually none; describe soil profile features which may be mistaken for compaction on this site):
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Functional/Structural Groups (list in order of descending dominance by above-ground annual-production or live foliar cover using symbols: >>, >, = to indicate much greater than, greater than, and equal to):
Dominant:
Sub-dominant:
Other:
Additional:
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Amount of plant mortality and decadence (include which functional groups are expected to show mortality or decadence):
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Average percent litter cover (%) and depth ( in):
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Expected annual annual-production (this is TOTAL above-ground annual-production, not just forage annual-production):
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Potential invasive (including noxious) species (native and non-native). List species which BOTH characterize degraded states and have the potential to become a dominant or co-dominant species on the ecological site if their future establishment and growth is not actively controlled by management interventions. Species that become dominant for only one to several years (e.g., short-term response to drought or wildfire) are not invasive plants. Note that unlike other indicators, we are describing what is NOT expected in the reference state for the ecological site:
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Perennial plant reproductive capability:
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PrintThe Ecosystem Dynamics Interpretive Tool is an information system framework developed by the USDA-ARS Jornada Experimental Range, USDA Natural Resources Conservation Service, and New Mexico State University.
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